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Annual Report 2006
Jahresforschungsbericht 2006
Berichte des IGB Heft 24/2007
Leibniz-Institut für Gewässerökologie und Binnenfischerei
Leibniz-Institute of Freshwater Ecology and Inland Fisheries
im Forschungsverbund Berlin e.V.
Annual Report 2006
Jahresforschungsbericht 2006
Herausgeber
Leibniz-Institut für Gewässerökologie und Binnenfischerei (IGB)
im Forschungsverbund Berlin e. V.
Müggelseedamm 310, 12587 Berlin
Direktor (kommissarisch)
Prof. Dr. Gunnar Nützmann
Gestaltung
Antje Herrmann, Götz Greiner (Weimar)
Druck
ebert-druck + werbung Berlin
ISSN Nr. 1432-508X
© 2007 IGB
Content Inhalt
Preface Vorwort
1
The IGB – Structure and Services
12
Das IGB – Struktur und Service
1.1
Structure
12
Struktur
1.2
Administration
14
Institutsleitung
1.3
Scientific Advisory Board
15
Wissenschaftlicher Beirat
1.4
Staff
18
Mitarbeiter
1.5
Works Committee, Ombudsman and Equal Opportunity
Commissioner
21
Betriebsrat, Ombudsmann und Gleichstellungsbeauftragte
1.6
Research Services
22
Service
2
Research Program 2005-2007
27
FE-Programm 2005-2007
3
Research Reports – Selected papers
31
Forschungsberichte – Ausgewählte Publikationen
3.1
Research Topic 1 Forschungsschwerpunkt 1
31
Environmental signalling
Umweltbedingte chemische Kommunikation
3.1.1
Environmental pollution by bisphenol A: sources and fate
in the Elbe basins and biological effects
Umweltverschmutzung durch Bisphenol A: Einträge und
Stoffverhalten im Elbe-Einzugsgebiet
sowie biologische Wirkungen
JAGNYTSCH , O., KRÜGER , A., O PITZ , R., LUTZ , I., B EHRENDT, H.,
KLOAS , W.
33
3.2
43
Processes at interfaces
Prozesse an Grenzflächen
3.2.1
Reconstruction of pristine morphology, flow, nutrient
45
conditions and submerged vegetation of lowland River
Spree (Germany) from palaeomeanders
Rekonstruktion der Referenzbedingungen der
Unteren Spree hinsichtlich Morphologie, Abfluss,
Nährstoffkonzentrationen und Unterwasservegetation
aus Paläomäandern
HILT, S., S CHÖNFELDER , I., RUDNICKA, A., CARLS , R.,
N IKOLAEVICH, N., S UKHODOLOV, A., E NGELHARDT , C.
3.2.2
Infiltration of surface water into ground-water
55
under transient pressure gradients
Infiltration von Oberflächenwasser in den
Grundwasserleiter bei instationären Druckgradienten
W IESE , B., N ÜTZMANN ,G..
3.2.3
Modelling dissolved oxygen dynamics in ice-covered
65
shallow lakes
Modellierung des dynamischen Sauerstoffverbrauchs
in zugefrorenen Flachseen
G OLOSOV, S., K IRILLIN, G..
3.3
75
Adaptation, plasticity, and dynamics of communities
Adaptation, Plastizität und Dynamik von Biozönosen
3.3.1
Detection and phylogenetic characterization of
77
polyphosphate accumulating bacteria in lake sediments
Nachweis und phylogenetische Charakterisierung von
Polyphosphat-akkumulierenden Bakterien in
Seesedimenten
G LOESS , S., HUPFER , M., R ATERING, S., G ROSSART, H.-P..
3.3.2
Depth distribution of abundant benthic
invertebrates in Lake Stechlin
Tiefenverteilung von häufigen benthischen Wirbellosen
im Stechlinsee
HELLAND, I.P., B RAUNS , M., F REYHOF ,J.
89
3.4
97
Sustainable management of aquatic ecosystems
Nachhaltiges Gewässermanagement
3.4.1
Do littoral habitats with high structural complexity mitigate
99
the impact of ship-induced waves on benthic invertebrates?
Reduzieren literorale Habitate mit hoher struktureller
Komplexität die Auswirkungen schiffsinduzierten
Wellenschlags auf benthische Wirbellose?
G ARCIA , X.-F., G ABEL , F., H OCHMUTH , H., B RAUNS , M.,
S UKHODOLOV, A., P USCH , M..
3.4.2
Integrated protection of surface waters
109
Integrierter Gewässerschutz von Binnengewässern
K OSCHEL , R., B EHRENDT, H., HUPFER , M..
3.4.3
Dissolved organic matter (DOM) modulates the cadmium
121
accumulation in zebrafish (Danio rerio) embryos
Huminstoffe beeinflussen die Cadmium-Akkumulation in
Zebrabärblingsembryonen (Danio rerio)
M EINELT, T., B URNISON, B. K., P LAYLE , R., P IETROCK , M.,
W IENKE , A., S TEINBERG , C.E.W.
3.4.4
Towards improved management of infection in
131
aquaculture: strategies arising from the host-parasite
interactions in rainbow trout Oncorhynchus mykiss
and the pathogenic flagellate Spironucleus salmonis
Wege zu einem verbesserten Management von
Infektionskrankheiten in der Aquakultur: Strategien
basierend auf der Wirt-Parasit Interaktion zwischen
der Regenbogenforelle Oncorhynchus mykiss und
dem pathogenen Flagellaten Spironucleus salmonis
P OYNTON, S.L., S AGHARI F ARD, M.R., B LEISS , W.,
J ØRGENSEN , A., W EISHEIT, C., M EINELT , T., RENNERT, B.,
C HENG , J., K IRSCHBAUM , F., KNOPF , K.
3.4.5
Growth performance and body composition of carp
(Cyprinus carpio) fed diets containing housefly maggot
meal (magmeal)
Wachstum und Körperzusammensetzung von Karpfen
(Cyprinus carpio) denen Futtermittel mit Fliegenmadenmehl
verabreicht wurden
O GUNJI , J.O., S UTTER , D., RENNERT, B., KLOAS , W., S CHULZ , C.
140
4
Statistics Statistik
149
4.1
Peer-reviewed papers
151
Artikel in referierten Zeitschriften
4.2
Non-reviewed papers, books, book chapters and reports
161
Artikel in nichtreferierten Zeitschriften, Bücher, Buchbeiträge
und Berichte
4.3
Degrees
168
Abschlüsse
4.3.1
Bachelor and Master Theses
168
Bachelor- und Diplomarbeiten
4.3.2
PhD Theses
169
Doktorarbeiten
4.3.3
Pre-Professional Theses
170
Habilitationen
4.4
Lectures at universities
171
Vorlesungen an Universitäten
4.5
Memberships in Scientific and Editorial Boards
174
Verantwortliche Positionen in Fachgesellschaften oder Gremien
4.6
Projects and Grants
176
Projekte und Stipendien
4.7
Summary
184
Gesamtübersicht
4.8
List of published IGB reports
Liste der bisher veröffentlichten Berichte des IGB
185
Preface
Vorwort
Freshwater is the earth’s most valuable natural resource. The main
challenge of our century is to reconcile the needs for water in human
societies with the requirements for healthy freshwater ecosystems.
Management of these resources must rely upon the best available scientific
knowledge including the factors controlling the structure, function, quality,
and quantity of freshwaters.
Based on these premises the Leibniz-Institute of Freshwater Ecology and
Inland Fisheries (IGB, established on 1 January 1992) is engaged in studies
comprizing the functioning, diversity, and management of freshwater
ecosystems based on multidisciplinary research activities.
Research areas typically located in NE Germany and adjoining regions
include: interactions between surface and groundwater, deep stratified and
shallow lakes, shallow lakes interconnected with lowland rivers, river
stretches and ponds. The state Brandenburg e.g., is characterized by more
than 3.000 lakes of various sizes and characteristics indicating the need for
substantial research.
The IGB’s national and international reputation in the field of aquatic
ecology has grown steadily and the Institute - comprising approximately 150
staff members and about 50 PhD-students - houses now many prestigious
hydrological, limnological, and fish ecological research groups.
During the year 2006 the completion of the new aquarium hall – the
inauguration ceremony took place on the 4th of October – marked a further
step towards the development of a modern research Institute. The facilities
comprise several independent re-circulatory systems and facilities for various
experimental research activities; these potentials which will further tighten
the cooperation with institutions at the national and international level.
At the end of 2006 the candidates for the open post of the director of the
Institute have presented their ideas on the scientific development of the
IGB. The final decision concerning the open post will be taken in 2007 and
this new personal situation will certainly also have impact on the future
research program of the IGB.
The scientific activities of our Institute are summarized in annual research
reports. We have selected 11 topics from our research programme
comprising four key areas: 1) environmental signalling, 2) processes at
aquatic interfaces, 3) adaptation, plasticity, and dynamics of aquatic
communities and 4) sustainable management of aquatic ecosystems.
From 1997 to 2005 the annual reports were prepared by the departments
of the IGB. The report for 2006 for the first time has been managed in part
by the department IV (Dr. Wolter), and by the head of the library, Mrs.
Grosse. We would like to thank them for their effort and all colleagues for
the work accomplished in 2006.
© IGB 2007
Frank Kirschbaum
Gunnar Nützmann
Department of Biology and
Ecology of Fishes
Director (in charge)
9
Improved experimental facilities – the new aquaria hall
After two years of construction work IGB’s new aquaria hall was
solemnly inaugurated on October 04, 2006.
The architecturally strict and functional building is situated at
Müggelseedamm 310. On two floors it has a main usable space of more than
1000 m², climate chambers, labs, a dissection lab and a modern seminar
room for lectures and conferences.
The largest basins have a volume of 36000 l each, and therein swim
among others mature sturgeons. Other aquaria and circulation systems
contain pike perch, carp, roach, eel, zebra fish and striped mullets used in
several distinct experiments and projects.
The total costs of 2.46 billion Euros have been financed to equal parts
(985,000 € each) by the Berlinean Senate and the Federal Ministry of
Education and Research as well as by the European Union (EFRE 460,000
€). On the other hand, the new improved experimental facilities enabled the
raising of 10 projects with a total budget of 2.43 billion Euros and 17.5
temporary positions since 2005.
10
The main aquaria hall in the basement has nine separate, closed circulation systems
used for harvesting the sturgeon breeding stock, as well as for various experiments
with eels (previous page), carp, tilapia and other fish species.
Photos IGB/Ralf Günter
Each circulation system has its own prufication unit, with mechanical and biological
treatment. In addition ozonisation and UV-desinfection are possible.
© IGB 2007
11
12
Administration Director
Rivers
Prof. Dr. N. Walz
Prof. Dr. R. Koschel
Shallow Lakes
Prof. Dr. G. Nützmann
Stratified Lakes
Limnology of
and Lowland
Limnology of
Department II
Department I
Ecohydrology
Prof. Dr. F. Kirschbaum
Fishes
Ecology of
Biology and
Department IV
Prof. Dr. W. Kloas
Inland Fisheries
Department V
Dr. J. Gelbrecht
Laboratory
Chemical
Central
G. Krätsch
M. Sieber
J. Hochschild
Department III
Administration Team
Technical Team
Dr. F. Fabich
Library
Information
Technology Team
Prof. Dr. H. E. Segner (chair)
Scientific Advisory Committee
Board of Directors of the Research Association Berlin e. V.
Structure
Board of Trustees
General Meeting
1.1
Member of the Research Association Berlin e.V.
Leibniz-Institute of Freshwater Ecology and Inland Fisheries
1
The IGB – Structure and Services
Das IGB – Struktur und Service
Struktur
Further Information
Weitere Informationen
Supporting Organisations
Federal Government (BMBF) and Country of Berlin each 50%
Organisation
The institute is a member of the Research Association Berlin e.V.
(see structure of IGB)
Staff (from 31.12.2006)
39
24
11
26
68
5
Scientists (internally funded)
Scientists (project or grant funded)
Ph.D. students (internally funded)
Ph.D. students (project or grant funded)
Technical and administrative staff (internally funded)
Technical staff (project or grant funded)
Annual budget
8,500,000 €
Publications
The scientific results are continuously published in national and international
journals. Lists of all publications in which staff members are involved are
published regularly in the “Berichte des IGB” / Annual Reports
Journals
„International Review of Hydrobiology”
(ISSN 1434-2944)
„Limnologica”
(ISSN 0075-9511)
„Berichte des IGB“
(ISSN 1432-508X)
© IGB 2007
13
1.2 Administration
Institutsleitung
Prof. Dr. Gunnar Nützmann
Müggelseedamm 310
12587 Berlin
phone:
+49 (0) 30 - 64 181 661
fax:
+49 (0) 30 - 64 181 663
e-mail: [email protected]
14
Head of Administration
G. Krätsch
Müggelseedamm 310
12587 Berlin
phone:
+49 (0) 30 - 64 181 603
fax:
+49 (0) 30 - 64 181 600
e-mail:
[email protected]
Secretary
B. Spieler
Müggelseedamm 310
12587 Berlin
phone:
+49 (0) 30 - 64 181 602
fax:
+49 (0) 30 - 64 181 600
e-mail:
[email protected]
Head of Department I
Ecohydrology
Müggelseedamm 310
12587 Berlin
phone:
+49 (0) 30 - 64 181 661
fax:
+49 (0) 30 - 64 181 663
Head of Department II
Limnology of Shallow Lakes
and Lowland Rivers
Prof. Dr. N. Walz
Müggelseedamm 301
12587 Berlin
phone:
+49 (0) 30 - 64 181 680
fax:
+49 (0) 30 - 64 181 682
e-mail:
[email protected]
Head of Department III
Limnology of Stratified Lakes
Prof. Dr. R. Koschel
Alte Fischerhütte 2
16775 Stechlin-Neuglobsow
phone:
+49 (0) 330 82 - 69 90
fax:
+49 (0) 330 82 - 69 917
e-mail:
[email protected]
Head of Department IV
Biology and Ecology of Fishes
Prof. Dr. F. Kirschbaum
Müggelseedamm 310
12587 Berlin
phone:
+49 (0) 30 - 64 181 610
fax:
+49 (0) 30 - 64 181 750
e-mail:
[email protected]
Head of Department V
Inland Fisheries
Prof. Dr. W. Kloas
Müggelseedamm 310
12587 Berlin
phone:
+49 (0) 30 - 64 181 630
fax:
+49 (0) 30 - 64 181 799
Head of Central Chemical
Laboratory
Dr. J. Gelbrecht
Müggelseedamm 301
12587 Berlin
phone:
+49 (0) 30 - 64 181 730
fax:
+49 (0) 30 - 64 181 682
e-mail:
[email protected]
1.3 Scientific Advisory Committee
Wissenschaftlicher Beirat
Prof. Dr. H. E. Segner
address:
phone:
fax:
e-mail:
member since:
Prof. Dr. H. Rosenthal
address:
phone:
fax:
e-mail:
member since:
Prof. Dr. E. van Donk
address:
phone:
fax:
e-mail:
member since:
Prof. Dr. W. Endlicher
address:
phone:
fax:
e-mail:
member since:
© IGB 2007
Chair of Advisory Committee
Zentrum für Fisch- und Wildtiermedizin am
Institut für Tierpathologie
Universität Bern
Länggass Straße 122
CH-3012 Bern
+41 (0) 31 – 63 12 441
+41 (0) 31 – 63 12 611
[email protected]
01.01.2002
Deputy Chair of Advisory Committee
Schöfferstraße 48
21629 Neu Wulmsdorf
+49 (0) 40 – 70 06 514
+49 (0) 40 – 67 01 02 676
[email protected]
01.12.2000
Department of Food Web Studies
Institute of Ecology
Rijksstraatweg 6
3631 Nieuwersluis
The Netherlands
+31 (0) 294 – 239 353
+31 (0) 294 – 232 224
[email protected]
01.12.2004
Humboldt-Universität zu Berlin,
Mathem.-Naturwissensch. Fakultät II
Geographisches Institut
Unter den Linden 6
Sitz: Rudower Chaussee 16
10099 Berlin
+49 (0) 30 – 20 93 68 08
+49 (0) 30 – 20 93 68 44
[email protected]
01.01.2003
15
Dr. K. Fent
address:
phone:
fax:
e-mail:
member:
Prof. Dr. F. Frimmel
address:
phone:
fax:
e-mail:
member since:
Prof. Dr. U. Grünewald
address:
phone:
fax:
e-mail:
member since:
Prof. Dr. E. A. Huisman
address:
phone:
e-mail:
member:
16
Institut für Umwelttechnik
Fachhochschule beider Basel
St. Jakobs-Strasse 84
CH-4132 Muttenz
+41-(0)61-467 45 05
+41-(0)61-467 42 90
[email protected]
[email protected]
01.12.1998 - 30.11.2006
Universität Karlsruhe (TH),
Engler-Bunte-Institut,
Lehrstuhl für Wasserchemie
Richard-Willstätter-Allee 5
76131 Karlsruhe
+49 (0) 721 – 60 82 581
+49 (0) 721 – 69 91 54
[email protected]
01.12.2000
Brandenburgische Technische Universität
Cottbus, Fakultät Umweltwissenschaften
und Verfahrenstechnik
Postfach 10 13 44
03013 Cottbus
+49 (0) 355 69 42 33
+49 (0) 355 69 42 35
[email protected]
01.12.2004
Institute of Animal Sciences
Wageningen
c/o Koningsweg 6
NL-66 55 AC Puiflijk
+31 (0) 487 – 51 56 79
[email protected]
01.12.2000 - 06.10.2006
Prof. Dr. W. Lampert
address:
phone:
fax:
e-mail:
member:
Prof. Dr. S. Peiffer
address:
phone:
fax:
e-mail:
member since:
Prof. Dr. K.-J. Peters
address:
phone:
fax:
e-mail:
member since:
Prof. Dr. Th. Weisse
address:
phone:
fax:
e-mail:
member since:
© IGB 2007
Max-Planck-Institut für Limnologie Plön
Postfach 165
24302 Plön
+49 (0) 45 22 – 76 32 70
+49 (0) 45 22 – 76 33 10
[email protected]
01.12.1998 - 30.11.2006
Universität Bayreuth
Lehrstuhl für Hydrologie
95440 Bayreuth
+49 (0) 921 55 22 51
+49 (0) 921 55 23 66
[email protected]
01.12.2004
Humboldt-Universität zu Berlin
Institut für Nutztierwissenschaften
Phillippstr. 13
10115 Berlin
+49 (0) 30 – 20 93 63 63 oder -62
+49 (0) 30 – 20 93 63 70
[email protected]
01.01.2003
Institut für Limnologie
Österreichische Akademie der
Wissenschaften
Mondseestr. 9
A-5310 Mondsee
+43 (0) 6232 - 3125
+43 (0) 6232 - 3578
[email protected]
01.12.2004
17
1.4 Staff (December 31, 2006)
Mitarbeiter (31. Dezember 2006)
Director
Internally funded
Nützmann, Gunnar
Sakowsky, Alexandra
Spieler, Brigitte
Administration and Technical Team
Internally funded
Albrecht, Gerda
Bednarz, Stefan
Gaertner, Hartmut
Gürtler, Frido
Krätsch, Gisela
Schäricke, Kerstin
Schmidt, Mathias
Information Technology Team
Internally funded
Henke, Vera
Hochschild, Johannes
Kalberg, Christian
Voß, Astrid
Library
Internally funded
Große, Christine (since 09/2006)
Hentschel, Ute
Sieber, Magdalena (till 07/2006)
Central Chemical Laboratory
18
Internally funded
Project or grant funded
Exner, Hans-Jürgen
Gelbrecht, Jörg
Guder, Sylvia
Herzog, Christiane
Hupfer, Michael
Krüger, Angela
Lüder, Antje
Rossoll, Thomas
Schütze, Bernd
Zwirnmann, Elke
Kleeberg, Andreas
Żak, Dominik
Ecohydrology (Dept. I)
Internally funded
Brüggemann, Rainer
Bungartz, Heinz
Engelhardt, Christof
Friedrich, Hans-Jörg
Kobisch, Barbara
Lewandowski, Jörg
Nützmann, Gunnar
Schwamm, Dagmar
Siegert, Grit
Sukhodolov, Alexander
Ginzel, Gerhard
Golosov, Sergey
Hamann, Enrico
Horner, Christoph
Kirillin, Georgiy
Molkenthin, Christian
Schnauder, Ingo
Suhodolova, Tatiana
Limnology of Shallow Lakes and Lowland Rivers (Dept. II)
Internally funded
Adrian, Rita
Behrendt, Horst
Graupe, Marianne
Hintze, Thomas
Hölzel, Reinhard
Klockau-Raddatz, Sylvia
Köhler, Jan
Kozerski, Hans-Peter
Lehmann, Katrin
Meinck, Barbara
Newen, Ursula
Pusch, Martin
Täuscher, Helgard
Walz, Norbert
Winkler, Hanna
Bauer, Nadine
Brauns, Mario
Carl, Peter
Gericke, Andreas
Hilt, Sabine
Hirt, Ulrike
Hofmann, Jürgen
Huber, Veronika
Leszinski, Marc
Mischke, Ute
Opitz, Dieter
Strube, Torsten
Venohr, Markus
Wagner, Carola
Wilhelm, Susann (till 10/2006)
Limnology of Stratified Lakes (Dept. III)
© IGB 2007
Internally funded
Allgaier, Martin
Beyer, Ute
Casper, Peter
Dalchow, Johanna
Degebrodt, Monika
Degebrodt, Roman
Glöß, Stefanie
Grossart, Hans-Peter
Kasprzak, Carola
Kasprzak, Peter
Koschel, Rainer
Krienitz, Lothar
Mach, Elke
Mallok, Uta
Papke, Monika
Pommerening, Eleonore
Roßberg, Reingard
Sachtleben, Michael
Scheffler, Adelheid
Schulz, Marina
Tesch, Edith
Wiedner, Claudia
Dziallas, Claudia
Eixler, Sebastian
Hutalle, Kristine Michelle L.
Jander, Jörn
Koppe, Cathleen
Rychla, Anna
Sergelen, Gongor
Stüken, Anke
Wauer, Gerlinde
19
Biology and Ecology of Fishes (Dept. IV)
Internally funded
Arlinghaus, Robert
Daedlow, Katrin
Faller, Markus
Fischer, Leonore
Freyhof, Jörg
Helms, Christian
Kirschbaum, Frank
Kuntze, Karena
Löschau, Peter
Mehner, Thomas
Ohlberger, Jan
Osman, Alaa Gad El-Karim Mahmoud
Pohlmann, Kirsten
Rohde, Titus
Simon, Marcel
Staaks, Georg
Stelbrink, Björn
Türck, Alexander
Uusi-Heikkilä, Silva
Wolter, Christian
Zwadlo, Henrik
Baganz, Daniela
Beardmore, Alan Benedict
Dorow, Malte
Garcia, Xavier-Francois
Geßner, Jörn
Helland, Palm Ingeborg
Huckstorf, Volker
Lewin, Wolf-Christian
Würtz, Sven-Holger
Inland Fisheries (Dept. V)
20
Internally funded
Ballegooy, Christoph van
Cuppok, Ingo
Hübner, Bettina
Kersten, Petra
Kloas, Werner
Knopf, Klaus
Kohlmann, Klaus
Kunow, Mathias
Lorenz, Claudia
Lutz, Ilka
Meinelt, Thomas
Neumann, Nadja
Nimptsch, Jorge
Pflugmacher, Stephan
Pietsch, Constanze
Rennert, Bernhard
Schumacher, Wibke
Stüber, Angelika
Tillack, Antje
Urbatzka, Ralph
Vassilakaki, Maria
Viehmann, Viola
Wiedemann, Caterina
Wiegand, Claudia
Ballot, Andreas
Contardo Jara, Valeska
Fard, Mohammad Reza Saghari
Frank, Sabrina
Grigutyte, Reda
Jagnytsch, Oana
Kamara, Sheku
Menzel, Ralph
Opitz, Robert
Peuthert, Anja
Rienau, Stefanie
Trubiroha, Achim
1.5 Works Committee, Ombudsman and Equal
Opportunity Commissioner
Betriebsrat, Ombudsmann und Gleichstellungsbeauftragte
Chairman
E. Zwirnmann
Müggelseedamm 301
12587 Berlin
phone: +49 (0) 30 – 64 181 735
P. Casper
16775 Stechlin-Neuglobsow
phone: +49 (0) 33 082 – 69 929
C. Engelhardt
Müggelseedamm 301
12587 Berlin
phone: +49 (0) 30 – 64 181 664
M. Kunow
Müggelseedamm 310
12587 Berlin
phone: +49 (0) 30 – 64 181 702
Th. Hintze
Müggelseedamm 301
12587 Berlin
phone: +49 (0) 30 – 64 181 689
J. Dalchow
16775 Neuglobsow
phone: +49 (0) 33 082 – 69 916
K. Wagner
Müggelseedamm 301
12587 Berlin
phone: +49 (0) 30 – 64 181 693
Ombudsman “Safeguarding good scientific practice”
M. Hupfer
Müggelseedamm 301
12587 Berlin
phone: +49 (0) 30 – 64 181 605
Equal Opportunity Commissioner
A. Krüger
Müggelseedamm 301
12587 Berlin
phone: +49 (0) 30 – 64 181 735
© IGB 2007
21
H OCHSCHILD , J.
1.6 Research Services
Service
1.6.1 Information Technology Team
Informatik und Rechentechnik
The Information Technology Team (ITT) of the IGB provides computer,
software and net equipment for all research departments, management
offices, and the library in our institute. That means to design, to set up and
to maintain the intra-network, file and application services and, last but not
least, the connection to the internet (e-mail, www, ftp, vpn, etc).
The largest part of ITT’s task spectrum is the maintenance of the
workplace computer pool (Intel PCs, mostly running MS-Windows, W2K),
which consists of approximately 500 PCs, including 100 computers for
special jobs in the laboratories and 80 notebooks. In addition to the
hardware and operating system oriented activities, ITT has also to purchase,
install, set up and evaluate standard and special software. In a lot of cases
ITT is even developing new software solutions, e.g. a measurement database,
interface software for measuring devices, and a cgi access to the IGB
literature catalogue for the IGB website.
The next, just as important, part of ITT’s area of responsibility is the
administration and maintenance of the big fileservers and the pool of special
servers. A very important field to do it is the safeguarding of the data stored
on the servers, against any loss or destruction. For this purpose ITT
developed a novel system with a special magnetic tape library, so that data
can be restored up to three month backdated. For higher security and good
availability of IGB’s data pool, in 2004 began the use of Server-RAIDsystems. In the following years the use of RAID-systems was powerful
expanded.
Beginning in the October 2006 in the IGB was installed a Wireless Local
Area Network. The scientists and students have now easy accesses to the
internet and the common IGB network with their notebooks on any places
in the IGB buildings.
For the other services, such as email, databases, etc. the server pool still
containing several HP, IBM RS6000, SUN, Compaq Alpha, and Intel/Linux
servers. Some SUN and Intel workstations perform special jobs for
simulations and special numerical calculations.
ITT also maintains some web servers e.g. "www.igb-berlin.de" or
“www.adaptfish.igb-berlin.de” or “www.flake.igb-berlin.de” and supports the
activities of the research departments in developing their own homepages,
and guarantees the web presentation of the IGB, which is of great
importance for the publicity of the institute. With the ever growing
expansion of the internet, we are permanently faced with different security
problems in the IGB network. By setting up and maintaining a firewall
router, we spend a great deal of our resources on the protection of the
systems from actions of foreign hackers.
22
The IGB has its own internet domain, named "igb-berlin.de". All
scientists, staff and guest researchers and the technical staff can use the
internet and e-mail services, web browsers and FTP-tools directly from their
workplaces. Incoming and outgoing e-mails are collected in a common mail
host, where viruses and spam mails are filtered out, so that only checked
mails are distributed to the recipients. Infected mails are returned to the
senders.
In order to print documents and graphics, members of the institute have
access to more than 80 greyscale and colour laser printers. Posters can be
designed and printed with equipment consisting of a graphic workstation and
a DIN-A0-HP-Posterjet 5000. Other periphal devices include scanners, slide
exposers, digitalising tablets, projectors and notebooks.
The IGB administration is working with a SAP/R3 database. Seven PCs
are connected by X21/ISDN wires with a central SAP system.
The most used software applications in the IGB are MS-Office,
CorelDraw 12, Havard-Graphics 4.0, SigmaPlot, Origin, Mathlab, ModelMaker, SPSS, SAS, AVS, Esri’s GIS “ArcInfo/ArcView”, Reference
Manager, BISLOK and the programming languages C/C++, Java, Fortran,
Simula and Pascal.
In 2006 for the first time was provided a “Windows 2003 Server”
configured as a terminal server to make available comprehensive statistical
and other special software to the workplace pcs.
The freeware SAMBA, running on the UNIX-machines, is used to
resolve the network file services.
© IGB 2007
23
G ROSSE , C H .
1.6.2 Library
Bibliothek
General information
The library is a special scientific library providing the central information
supply for the Leibniz-Institute of Freshwater Ecology and Inland Fisheries.
The information transfer is determined by the research profile of the
institute, and subject specialisations in limnology, ecohydrology, geohydrodynamics, fishery sciences and water management.
While the library mainly serves to support the employees of the IGB with
literature, visitors and students can also use the library, under slightly
restricted conditions.
Tasks and services
acquisitions (literature selection and literature procurement by
-
purchase, exchanges and gifts)
bibliographical search through international and external data bases
documentation of IGB publications
literature supply from other facilities via inter-library loan
publications: list of periodicals, new acquisitions list
supply of books
Library software
BIS-LOK Version 5, Alephino 3.0 (change 09/2006)
Search possibilities
In the library:
alphabetical and classified catalogues (accessioning of the bookstock
before 2002)
OPAC =Online Public Access Catalogue (proof of all bookstock)
ASFA = Aquatic Science and Fisheries Abstracts (for 1978 to 2002,
CD-ROM)
Online:
ISI/JCR = Institute for Scientific Information/Journal Citation
Reports
ISI/WoS = Institute for Scientific Information/Web of Sciences
Use
-
24
open access library
reference collection – loan to employees
Technical provision
18 reading seats
-
3 PC work stations with internet access
2 microfilm readers
photocopier
Users
employees of the institute, guests researchers, students and other
-
external users
Opening hours
for employees and guests during normal working hours at the
-
institute
external users according to agreement by telephone
Staff
Magdalena Sieber (till 08/2006)
Christine Große (since 09/2006)
Head of Library
phone: 030/64 181 655
fax:
030/64 181 676
[email protected]
© IGB 2007
Ute Hentschel
Librarian
phone: 030/64 181 656
fax:
030/64 181 676
25
P OYNTON , S. L.
1.6.3 Scientific Communications Skills: Advanced
Course
Wissenschaftliche Kommunikation: Kurse für Fortgeschrittene
The commitment of IGB to supporting the professional development of its
members was shown again in summer 2006, when scientists in Berlin had the
opportunity to participate in a course entitled “Scientific Communication
Skills: Advanced Level”. The intensive course, taught in English, focussed
on the strategies and skills needed to make the transition from good to
excellent scientific communications.
The course began with a brief review of the history of scientific
communication, and recognised that over the millennia, many different
languages have been dominant, including Latin, Greek, Chinese, German,
French, and currently English. Special consideration was then given to some
stylistic differences in writing styles between German and English, and
avoidance of common errors in usage. When examining the art of scientific
writing, participants learned how to craft effective – audience specific –titles,
how to write persuasive introductions and discussions, the importance of
strong opening and closing sentences and paragraphs, and how to write
smoothly flowing elegant texts. By comprehensive class critique of published
texts, and those currently being written by the participants, the class learned
to recognise strong and weak writing styles, and began to develop skills for
editing texts for content, form and style.
In addressing spoken communication skills, emphasis was placed not only
on the content of a presentation, but also on the crucial importance of
effective delivery. Participants had many opportunities to practice giving
presentations on different topics, and in a variety of formats. In each class,
feedback was given on correct vocabulary, grammar and pronunciation. For
this advanced course, attention was also drawn to broad aspects of
professional development, such as networking, leadership, and active and
effective participation in conferences.
The participants brought to the course, a diversity of research expertise,
levels of experience, and language skills, which greatly enriched the learning
environment. The small class size ensured intense interaction, individual
attention, and many opportunities to speak English. The course was taught
by Dr. Sarah Poynton, an experienced research scientist and international
educator, who has directed and taught the Scientific Communications Skills
program in IGB for nearly 10 years. Classes were competently supported by
Dr. Poynton’s teaching assistant, Mr. M. Reza Saghari Fard, a Ph.D. student
from Department V.
26
2 Research Program 2005-2007
FE-Programm 2005-2007
2.1 Focus 1: Environmental signalling
Focust 1: Umweltbedingte chemische Kommunikation
Co-ordinator: Werner Kloas
The highly evolved sensitivity of signal receptors to exogenous chemical
stimuli can make organisms vulnerable to natural compounds and man-made
chemicals that mimic specific chemical cues or interfere with receptors.
The environmental signalling research programme will focus upon the
stimuli emitted by cyanobacterial secondary metabolites, natural
biogeochemicals and endocrine disrupters, and will determine their effects
on molecular modes of action, organisms and ecosystems. We investigate
various aspects of signalling, biotransformation processes, signal pathways
via reactive oxygen species (ROS), receptor signal transduction and gene
expression, in a range of aquatic organisms from cyanobacteria to
vertebrates, thus encompassing multiple compartments of lake ecosystems.
The studies emphasize broadening and deepening our understanding of
how aquatic organisms perceive and respond to both internal and external
signals in order to ensure appropriate changes in their cellular metabolism,
energy allocation, growth, development, reproduction and behaviour. Since
many effects of environmental signalling are phenomenological, the major
research effort will elucidate the corresponding modes of action.
The central focus of our research will seek to determine if environmental
signalling by natural compounds (cyanobacterial secondary metabolites and
humic substances), as well as by natural and man-made endocrine disrupters,
have the potential to significantly impact individual organisms and, in turn,
also populations. Thus these mechanistic approaches to research will create
information for potential risk assessment of aquatic ecosystems.
2.2 Focus 2: Processes at interfaces
Focus 2: Prozesse an Grenzflächen
Co-ordinators: Gunnar Nützmann, Norbert Walz
In the glacially formed landscape of North-Eastern Germany, nutrients and
energy are mutually transformed and transported at the interfaces between
groundwater and sediment and between sediment and surface water. This
situation raises the question as to how the amount and the velocities of these
transformations underlie biological, chemical or physical processes. We will
focus on quantifying the exchange processes at these interfaces in order to
better understand the underlying mechanisms and to provide a foundation
for better modelling.
© IGB 2007
27
In this subject group, we focus on a unique combination of expertise in
different disciplines (hydrology, mathematical modelling, water chemistry,
macrophyte- plankton-and benthos-ecology) as wellas on the hydrology and
biogeochemistry of this landscape.
Project 2.1 (Hydrodynamic control of fluxes and biota) is desiqued to
study the turbulent currents in rivers and lakes which influence all processes
at the interfaces between open water and the biota. In projects 2.2, 2.3 and
2.4 processes occurring at specific interfaces are examined: the exchange of
ground and surface water through the sediment (Project 2.2, Connectivity
between ground and surface waters), the biogeochemical transformations
between sediment and surface water, especially their promotion by biological
factors (Project 2.3, Biogeochemical processes in microzones) and the
biological exchange between benthic structures and open water that
determine the ecological status of shallow waters (Project 2.4, Benthic
pelagic coupling and bistability in shallow systems).
2.3 Focus 3: Adaptation, plasticity, and dynamics
of communities
Focus 3: Adaptation, Plastizität und Dyanmik von Biozönosen
Co-ordinator: Rainer Koschel
Research focus 3 will identify ecological and evolutionary based optimisation
strategies of speciation and of biodiversity. A better understanding of
adaptation, plasticity and dynamics of microorganisms, plankton and fish
communities will lay a new theoretical foundation for the sustainable
management of aquatic ecosystems.
Our research builds upon previous IGB investigations of lowland
ecosystems as the lakes Müggelsee, Stechlin and Breiter Luzin and the rivers
Spree and Oder.
Project 3.1 “Structuring of microbiota by biological interactions” will
examine the genotype and chemotype diversity and phenotypic plasticity of
bacteria, methanogenic archaea, cyanobacteria and algae. Project 3.2
“Regulation of fish diversity in running waters” is focused on key abiotic
factors, life history differentiation and hybridisation of sturgeon species.
Project 3.3 “Ecological factors in speciation of fishes” will address
differential ecological adaptation and sympatric speciation of cisco species
(Coregonus spp.). Project 3.4, directed to “Climate change biology”, is guided
by the hypothesis that climate changes induce long-term changes in the
phenology of plankton and subsequent pertubations in species interactions.
28
2.4 Focus 4: Sustainable management of aquatic
ecosystems
Focus 4: Nachhaltiges Gewässermanagement
Coordinator: Christian Wolter
Research focus 4 was established in 2000 to develop scientifically rigorous
approaches for adaptive and sustainable water and ecosystem management
strategies in freshwaters. The individual projects are primarily designed to
facilitate sustainable use and to expand our knowledge of the structure and
functioning of freshwater ecosystems. This approach supports the statutory
mission of the IGB, which includes transfer of the results of basic ecologic
research into applied science.
Our results include the development of in-lake restoration techniques,
assessment schemes for biological classifications of lakes and rivers, and a
characterization of recreational fisheries as one of the major users of fish
stocks.
In future, integrative management options will be analysed and evaluated,
such as reduction of external nutrient loading combined with in-lake
ecological engineering, biodiversity protection and conservation-driven
fisheries management, to maximize stakeholder benefits and minimize
environmental impacts. The response of stagnant and running freshwater
systems to restoration measures will be used as large-scale scientific
experiments to improve the ecosystem theory of degraded water systems and
to promote the costs-by-cause principle in conservation. In urban areas, the
ecological potential of heavily modified water bodies will be assessed to aid
in the implementation of the Water Framework Directive (WFD).
Beyond 2008 we will attempt to integrate ecological and socio-economic
studies to reflect the human dimensions in natural resource management.
This work will be done in co-operation with social and economic research
institutes and by expanding our own scientific expertise.
Research focus 4 comprises the following projects:
4.1 Management of river systems: development of ecological knowledge to
support sustainable restoration and management concepts for running
waters.
4.2 Ecological engineering and lake ecosystem development: long-term
analyses of manipulated and restored, deep, thermally-stratified lakes and
drainage basins in Germany’s Baltic Lake District.
4.3 Inland Fisheries: development of sustainable aquaculture strategies to
support the improvement of fish culture while minimising environmental
impacts. Furthermor, we seek a holistic understanding of the human and
biological component of fisheries systems and their management.
© IGB 2007
29
30
3 Research Reports – Selected Papers
Forschungsberichte – Ausgewählte Publikationen
3.1 Research Topic 1
Forschungsschwerpunkt 1
Environmental signalling
Umweltbedingte chemische Kommunikation
© IGB 2007
31
32
J AGNYTSCH , O., K RÜGER , A., O PITZ , R., L UTZ , I., B EHRENDT , H.,
K LOAS , W.
3.1.1 Environmental pollution by bisphenol A:
sources and fate in the Elbe basins and
biological effects
Umweltverschmutzung durch Bisphenol A: Einträge und Stoffverhalten
im Elbe-Einzugsgebiet sowie biologische Wirkungen
Key words: bisphenol A, emission, retention, endocrine disruptor, Xenopus
laevis, thyroid system, reproductive system
Abstract
Households and industrial discharges are the main sources of bisphenol A
(BPA), an environmental chemical suspected to cause severe effects on
endocrine systems, in surface waters. The emissions are realised by waste
water treatment plants (WWTP) and combined sewer systems as well as
industrial direct discharges. It was estimated that the total inputs into the
river system of Elbe are about 970 kg/a by WWTP, 70 kg/a by sewer
systems and 510 by two industrial discharges in the Czech part of Elbe. The
retention within the surface waters of Elbe is 790 kg/a or 51%. Xenopus laevis
premetamorphic tadpoles at stages 48 and 51 were exposed to different BPA
concentrations ranging from 223 ng/L to 223 µg/L to analyse effects on
sexual differentiation and thyroid system. BPA caused moderate effects on
thyroid system by interference with thyroid receptors but had adverse effects
on sexual differentiation disrupting normal gonadal development particularly
in males as shown by gross morphological and histological determinations.
Zusammenfassung
Haushalte und industrielle Direkteinleiter gehören zu den Haupteinträgern
von Bisphenol A (BPA) in die Oberflächengewässer des ElbeEinzugsgebietes. Die Emission erfolgt dabei über kommunale Kläranlagen
(WWTP), Gemischtwasserkanalisation sowie industrielle Direkteinleiter. Der
Gesamteintrag von BPA über die WWTP beläuft sich auf etwa 970 kg/a, der
über die Gemischtwasserkanalisation auf 70 kg/a und etwa 510 kg/a
entfallen auf zwei industrielle Direkteinleiter im tschechischen Teil der Elbe.
Die Retention innerhalb der Oberflächengewässer der Elbe beträgt 790 kg/a
bzw. 51%. Xenopus laevis Kaulquappen im Entwicklungsstadium 48 bzw. 51
wurden mit verschiedenen BPA-Konzentrationen im Bereich von 223 ng/L
bis 223 µg/L exponiert, um die Wirkungen von BPA auf die
Sexualdifferenzierung und das Schilddrüsensystem zu untersuchen. BPA
beeinflußte das Schilddrüsensystem über Interaktionen mit dem
Schilddrüsenrezeptor nur moderat, zeigte aber adverse Auswirkungen auf die
Sexualdifferenzierung durch Störungen bei der Gonadenentwicklung von
männlichen Individuen auf morphologischer und histologischer Ebene.
© IGB 2007
33
3.1.1.1
Introduction
Climate change is recently one of the most important issues in environmental
sciences. Many scientific groups are concerned about worldwide temperature
and precipitation changes within near future. However, not only rising
temperatures and increase of natural disaster are able to modify regions,
nutrients, animal or human populations but also environmental pollution in
surface water. Since few years especially xenobiotica and recently
pharmaceutical compounds are objects of ecotoxicological studies.
Xenobiotica contain to the group of “endocrine disruptors” (ED). EDs are
compounds which interfere with endocrine systems and disrupt their normal
functions within an organism without remarkable toxicity (Colborn et al.
1996, Kloas 2002). Since the 1990`s an increasing pollution of such
compounds was noticed for instance in surface waters, agricultural areas, and
atmosphere, especially since the analytical methods for detection have been
continuously improved.
Bisphenol A (BPA) is one of the most common chemicals for production
of epoxy resins and polycarbonate plastics (Fig. 1).
CH3
HO
C
OH
CH3
Fig. 1: Chemical structure of bisphenol A.
BPA is widely used for all kind of products like computer housings,
carpets, upholstery, for car paintings and flame retardants such as
tetrabromobisphenol A (TBBA). BPA attracted public attention when it has
been generally known that it can leach out of plastic baby bottles or cans and
migrate into milk and food (Goodson et al. 2004, Braunrath et al. 2005).
Since BPA could be detected in diverse human tissues and environmental
samples it is nessessary to analyze its biological effects. Clear evidences exist
for feminization caused by BPA in snails, fish, and amphibians (Oehlmann et
al. 2005, Yokota et al. 2000, Levy et al. 2004) and many publications have
shown effects regarding reproduction but some findings are still
controversely discussed (Pickford et al. 2003, Yoshida et al. 2004).
To get a better understanding of BPA in a prospective perspective it is
necessary to assess the general sources and environmental fate of BPA.
Therefore the Elbe River system was used as a model. It is the second-largest
river system in Germany and one of the largest in central Europe. The
biological effects on thyroid system and reproduction were evaluated by
means of an amphibian model, the South African clawed toad Xenopus laevis.
3.1.1.2
Material and Methods
Bisphenol A emissions and retention
The Elbe river system has been investigated for BPA emission and retention.
Literature and internet were used to collect informations about chemical
properties, and usage of BPA as well as to accumulate data about BPA
34
determination of surface water samples. Mean BPA emissions have been
calculated by using the MONERIS model (Behrendt et al. 2003). This model
considers following 7 different pathways: particle entry via erosion, dissolved
entry via avulsion, basis flow, interflow, tile drainage, atmospheric deposition
on water surface areas, sealed urban areas, and point source discharges.
Based on informations about inflow and outflow of several WWTP BPA
retention for WWTP was calculated. The following retention function was
used to create a graph which compares observed BPA concentrations
measured along the Elbe main stream and calculated BPA concentrations:
C BPA
C BPAINPUT
1
1 a º HL 1
HL: Hydraulic loading
a= 7.18
BPA determination of water samples of Elbe-river catchment by HPLC
Additional to existing environmental data several water samples within the
Elbe catchment and tributaries were collected to determine BPA in surface
water. Water samples were taken monthly from Spree, Havel, Havel/Spree as
well as from WWTP outflow Münchehofe and Erpe. Samples from Wuhle I,
II, and Elbe were taken once. 2000 mL water sample were taken from the
middle stream and gross filtrated by using glass fiber filters. Each sample was
supplemented by 10 g NaCl and concentrated HCl for acidification. RP18
columns were used to concentrate BPA of 1000 mL water sample volume,
followed by eluation with acetone. Eluats were dried and resuspended in 1
mL acetonitrile. BPA determination was done by mean of HPLC.
Test Animals
The animals used for the exposure experiments are coming from an animal
stock of the Leibniz-Institute of Freshwater Ecology and Inland Fisheries,
Berlin, Germany. Adult frogs were induced to spawn by injecting human
chorionic gonadotropin (Sigma-Aldrich, Steinheim, Germany) into the dorsal
lymph sac according to Kloas et al. (1997). Fertilized eggs and larvae were
maintained in 60 L tanks filled with 40 L demineralized water and mixed with
0.25 g/L sea salt (Tropic Marin, Wartenberg, Germany). The water was
aerated by using airstones and the water temperature was adjusted to 22 ±
1°C. The pH-value ranged from 7.0 ± 0.5. The light-dark cycle was 12:12 h
during the exposure time. Tadpoles were held under these conditions until
they reached stages 48 or 51, respectively.
Short-term exposure of stage 51 tadpoles
Determination of potential effects of BPA on thyroid system was
accomplished by exposing tadpoles at stage 51 to BPA alone (100, 250, and
500 µg/L) and to BPA plus 0.1 nM T3 (thyroid hormone (TH)) using a semistatic exposure system (Fig. 2) (n=30, respectively). Stage 51 is particularly
qualified for this kind of gene expression determination, because the thyroid
gland is not yet functioning. Consequently, no endogenous TH circulate in
the blood stream, but several tissues are already competent to respond very
© IGB 2007
35
sensitively to exogenous addition of TH by modified gene expression
patterns. Test solutions were changed daily.
After 24, 48, and 72 h, head tissue was sampled to analyze the thyroid
system-specific biomarker thyroid hormone receptor ß (TRß) at the gene
expression level.
All test chemicals (E2, BPA, T3) were purchased from Sigma
(Taufkirchen, Germany).
Long-term exposure of stage 48 tadpoles
To determine the effects of BPA on morphological parameter (body weight,
whole body length), gonadal gross morphology and histology tadpoles at
stage 48 were exposed to BPA concentrations ranging from 10-9 to 10-6 M for
up to 75 days using a flow through system (Fig. 2). In parallel the natural
estrogen 17ß-estradiol (E2) was used as a positive control at 0.2 µg/L. Each
treatment contained 4 tanks with 7 L test solution and 25 tadpoles,
respectively. At the end of metamorphosis (stage 66), body weight, whole
body length and phenotypic sex was determined for all animals. Gonadal
tissues were collected for histological analyses.
Fig. 2: Design of a semistatistic system and a flow through sytem.
Gene expression determination in head tissues
Total RNA of head tissues was isolated using the phenolic reagent Trizol
(Invitrogen, Karlsruhe, Germany). Diluted RNA was transcribed in cDNA
by reverse transcription (RT). Following the amplification of cDNA for
EF1a, and TRß genes were carried out as described by Jagnytsch et al. (2005).
3.1.1.3
Results and Discussion
Bisphenol A emission
The total emission of BPA into the Elbe catchment was found to be 970
kg/a by WWTP, 70 kg/a by sewer systems and 510 kg/a by two industrial
discharges in the Czech part of Elbe (Fig. 3). The retention within the surface
waters of Elbe is 790 kg/a or 51%
The specific emission of 0.24 g/a*inhabitant was calculated. The
inhabitant specific discharge out of sewage plants was calculated to be 0.056
g/a*inhabitant. No data were found to atmospheric deposition, particle entry
via erosion, dissolved entry via avulsion, basis flow, interflow, and tile
drainage. The calculated specific emission of BPA correspond with data
36
found in literature (Fries, 2002), which specify a range 0.013-0.144
g/a*inhabitant.
33%
62%
5%
W W TP
Sew er System
Industrial discharges
Fig. 3: Total emission of BPA into Elbe catchment.
Using the retention function several BPA concentrations could be
calculated for different monitoring stations among the Elbe river. The
comparison of these calculated concentrations versus observed BPA
concentrations has shown that most of the data were within the 30%
deviation but some data were underestimated especially stations downriver of
Valy (Fig. 4A). Possible reason for that could be emssions of industrial
discharges like Spolchemie and Spolana in the Czech area. Considering these
industrial discharges all values were within the 30% deviation of retention
(Fig. 4B).
A
B
Fig. 4: Comparison of calculated and observed BPA concentrations among the Elbe river. A
without industrial discharges. B with industrial discharges.
BPA determination of water samples of Elbe-river catchment
BPA was determined in water samples taken from different tributaries of the
Elbe catchment. Data are given in table 1. BPA could be detected in all tested
water systems. The concentrations ranged from 0-1.5 µg/L. The highest BPA
concentration could be measured in WWTP Münchehofe outflow.
© IGB 2007
37
Tab. 1: BPA detection in water samples of the Elbe-river catchment. The unit of the given
data is ng/L.
Water system
Oct 06
Nov 06
Dec 06
0
144.3
0
0
127.1
302.7
30.7
112.7
Havel/Spree (Potsdam)
363.5
268.9
20.4
43.6
WWTP Outflow Münchehofe
1062.3
347.0
1002.8
1508.1
Erpe + WWTP Münchehofe
911.8
256.2
627.0
n.d.
Elbe (Krippen)
481.9
n.d.
n.d.
n.d.
Wuhle I (Marzahn)
n.d.
137.8
n.d.
n.d.
Wuhle II (Hellersdorf)
n.d.
112.2
n.d.
n.d.
Erpe above WWTP Münchehofe
n.d.
n.d.
n.d.
547.4
Spree (Große Tränke)
Havel (Hennigsdorf)
Jan 07
Short-term exposure of stage 51 tadpoles
TRß-mRNA
[CHANGE vs CONTROL]
TRß mRNA expression was significantly up-regulated by 0.1 nM T3 already
after 24 h and remained elevated over the entire experimental exposure until
72 h. Within 24 hours, T3 treatment caused a 4-fold higher expression of
TRß gene in head tissues compared to untreated controls (Fig. 5A). The
highest BPA concentration antagonized the T3-induced TRß expression at all
sampling points (Fig. 5B). 250 µg/L BPA caused a significant downregulation of the T3-induced TRß expression after 48 h. In the absence of
T3, BPA alone did not affect TRß expression.
10
8
SC
100 µg/L BPA + SC
250 µg/L BPA + SC
500 µg/L BPA + SC
A
0.1 nM T3
100 µg/L BPA + T3
250 µg/L BPA + T3
500 µg/L BPA + T3
6
***
B
***
***
4
2
24h
48h
72h
24h
48h
72h
Fig. 5: Relative TRß-mRNA expression after short-term exposure with BPA. A BPA
compared to untreated control. B BPA compared to T3.
Long-term exposure of stage 48 tadpoles
At the end of metamorphosis, mean weight of tadpoles treated with BPA was
increased in a dose dependent manner being significant already at 10-8 M
BPA for males and females, respectively (Fig. 6). Mean whole body length of
tadpoles exposed to BPA was also increased compared to controls (Fig. 6).
This increase was significant at 10-6 M BPA for males and at 10-7 M and 10-6
M BPA for females. At the end of metamorphosis gonads were dissected for
histological analyses. The exposure of males to 10-6 M BPA caused
remarkable changes in gonadal gross morphology. Histological analyses of
these gonads have clearly shown leackages in testicular tissues compared to
control animals (Fig. 7A/B). Similar effects could be observed in males
which were exposed to the natural estrogen 17ß-estradiol (E2) (Fig. 7C).
38
male
female
Co
*
**
***
E2 10-9 10-8 10-7 10-6
Whole body length [mm]
Total body weight [g]
1,0
0,9
0,8
0,7
0,6
0,5
0,4
0,3
0,2
0,1
male
female
21
20
**
***
19
18
17
16
15
Co
E2 10-9 10-8 10-7 10-6
BPA [M]
BPA [M]
Fig. 6: Total body weight and whole body length after long-term exposure with BPA.
At the end of metamorphosis gonads were dissected for histological
analyses. The exposure of males to 10-6 M BPA caused remarkable changes
in gonadal gross morphology. Histological analyses of these gonads have
clearly shown leakages in testicular tissues compared to control animals (Fig.
7A/B). Similar effects could be observed in males exposed to E2 (Fig. 7C).
A
B
C
Fig. 7: Hematoxylin-eosin staining of male gonads of juvelile frogs: A untreated control male,
B after 10 -6 M BPA treatment, C after E2 treatment.
3.1.1.4 Discussion
Biodegradation experiments have demonstrated a half-life of up to 4 days for
BPA in river waters (Klecka et al. 2001). Despite it seems to be degraded
rapidely after a lag phase it could be shown that BPA is permanently
detectable in the Elbe River and several tributaries.
Investigations about emissions have shown that mainly WWTP´s and
industrial discharges are responsible for the BPA release into the Elbe
catchment. A retention rate of 51 % for BPA by WWTP´s was calculated
which means the absolute inflow of the WWTP´s must be twice as much.
This inflow must be mainly caused by households as well as small and
medium sized enterprises. Possible sources of BPA could be toilet paper,
© IGB 2007
39
plastic material cleaned in a dishwasher or food rests which are disposed by
sewer systems (Gehring 2004, EFSA 2006). Another source of BPA is
released from PVC pipes or surface coating agents. Depending on state of
the technology the retention of WWTP´s are quite different. Old WWTP´s
with trickling filtration and activated sludge barely degrade BPA whereas
WWTP´s using membrane filtration, nano-filtration and membrane
bioreactors have a BPA elimination rate of at least 75% (Gehring 2004).
The amphibian model was used to analyze effects of BPA on the thyroid
and reproductive system. Several studies have evaluated that the amphibian
Xenopus laevis is a valuable model to determine effects of ED on endocrine
system (Opitz et al. 2002, Kloas 2002, Levy et al. 2004). TH produced and
released from thyroid gland are essential for different developmental phases
during metamorphosis. Interferences of ED with thyroid system can be
observed by stimulation or deceleration of metamorphosis in long-term
exposure.
In this study a short-term exposure with BPA and a combination of TH
and BPA was performed to determine effects of BPA on TRß gene
expression level. TRß is an early response gene of TH. Within 24 h it
responds rapidely to exogenous given TH induction in stage 51 premetamorphic tadpoles. Challenge experiment with BPA and T3 clearly
demonstrated a dose response inhibitory action of BPA at concentrations of
250 and 500 µg/L BPA on TH induced gene expression of TRß. Similar
inhibitory effects have been observed for TBBA which is the brominated
form of BPA and a most commonly used flame retardant (Jagnytsch et al.
2006). The BPA effect was significant but less pronounced compared to that
caused by TBBA. These results suggest that compounds with similar
chemical structure can have similar properties.
Long-term exposure with BPA has shown significant increases in mean
body weight and whole body length of juvenile frogs in a dose dependent
manner. Studies about effects of BPA on body weight are quite controversial.
In several studies it was documented that BPA can cause an increase of single
organ weights like uterus and liver in rats and mice (Papaconstantinou et al.
2000). Rubin et al. (2001) has demonstrated the increase of body weight in rat
offspring treated by BPA. Further in vivo studies have shown a decrease in
mouse and chicken testis weight or body weight probably caused by toxic
side effects (Al-Hiyasat et al. 2002, Furuya et al. 2002). However, the natural
estrogen E2 was also tested in long-term exposure as a positive control and
there was no difference in body weight and whole body length seen
suggesting that growth promoting effects of BPA are not induced by
estrogenic modes of action but might affect regulation of insulin like growth
factors.
Investigations of the reproductive system were done by using long-term
exposure where the positive control E2 caused 75% feminization. Remaining
E2 males have mixed sex gonads or testis with leakages within the tissue.
Exposure of males to 10-6 M BPA caused remarkable changes in gonadal
gross morphology too. Histological analyses of these gonads also
demonstrated leakages in several testicular tissues but less pronounced. From
40
E2 treatment it appeared that feminization of male gonads starts with tissue
degradation and disaggregation. After a couple of time, testis changes to
mixed gonads which means ovarian and testicular tissue in one gonad until
just ovarian tissue is remaining. That means remarkable observation in gross
morphology and histology of BPA male gonads could be evidences for
beginning feminization procedures. So the tested concentrations of BPA
were too low for causing complete feminization. In zebrafish 1820 µg/L
BPA caused 32% ovo-testis (Yokota et al. 2000).
In summary, BPA action on thyroid system is just moderate resulting in
minor competition of BPA and TH on thyroid hormone receptor level or
transport binding proteins. Results on gross morphology and histology are
not finished yet. But these given results clearly demonstrate that higher BPA
concentrations can interfere with the thyroid system probably mediated via
its moderate thyroid hormone receptor binding in a competitive manner and
also with the reproductive system. Lower concentrations of BPA did not
show any remarkable effect. BPA is widely spread in the environment.
Especially in regard to animal and human health it is necessary to improve
the degradation of such compounds in WWTPs and also to minimize the
release of such harmful substances by industries into to surface water.
Acknowledgement
The research was funded by BMBF (GLOWA-Elbe). The authors thank
Wibke Schuhmacher, Ingo Cuppok, Antje Lüder, Bernd Schütze, Björn
Hermelink, and Maria Jagnytsch for technical assistance. Special thanks to
Marcel Simon and Liane Wieczorek for histological assistance.
References
AL-HIYASAT, A. S., DARMANI, H., ELBETIEHA, A. M. (2002): Effects of bisphenol A
on adult male mouse fertility. Eur J Oral Sci, Vol. 110, 163-167.
BEHRENDT, H., CONSTANTINESCU, L.T., CVITANIC, I., DRUMEA, D., JABUCAR, D.,
JURAN, S., PATAKI, B., SCHREIBER, H.,
SNISHKO, S., ZESSNER, M. (2003):
Nährstoffeinträge und –frachten im Flusssystem der Donau - Ergebnisse einer
flussdifferenzierten Modellanalyse: Nutrient inputs and loads in the Danube River
system – Results of a river system oriented model analysis. ÖWAW., Heft 9-10,
1-7.
BRAUNRATH, R., PODLIPNA, D., PADLESAK, S., CICHNA-MARKL, M. (2005):
Determination
of
bisphenol
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in
canned
foods
by
immunoaffinity
chromatography, HPLC, and fluorescence detection. J Agric Food Chem, Vol. 53,
8911-8917.
COLBORN, T., Dumanoski, D., Myers, J. P. (1996): Our stolen future. Little Brown &
Co., London.
EFSA. (2006): Opinion of the scientific panel on food additives, flavourings,
processing aids and materials in contact with food on a request from the
commssion related to 2,2-bis(4-hydroxyphenyl)propane (bisphenol A). The EFSA
Journal, Vol. 428, 1-75.
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FURUYA, M., SASAKI, F., HASSANIN, A. M. A., KUWAHARA, S., TSUKAMOTO, Y.
(2002): Effects of bisphenol A on the growth of comp and testes of male chicken.
The Canad J of Veterenary Res, Vol. 67, 68-71.
GEHRING, M. (2004): Verhalten der endokrin wirksamen Substanz Bisphenol A bei
der kommunalen Abwasserentsorgung. Doktorarbeit. http://rcswww.urz.tudresden.de/~gehring/deutsch/dt/mitar/ge/dige_lic.pdf
GOODSON, A., ROBIN, H., SUMMERFIELD, W., COOPER, I. (2004): Migration of
bisphenol A from can coatings - effects of damage, storage conditions and
heating. Food Additives Contaminants, Vol. 21, 1015-1026.
JAGNYTSCH, O.,
OPITZ,
R., LUTZ, I.,
KLOAS,
W. (2006):
Effects
of
tetrabromobisphenol A on larval development and thyroid hormone regulated
biomarkers of the amphibian Xenopus laevis. Environ Res, Vol. 101, 340-348.
KLOAS, W. (2002): Amphibian as a model for the study of endocrine disruptors. Int
Rev Cytol, Vol. 216, 1-57.
LEVY, G., LUTZ, I., KRÜGER, A., KLOAS, W. (2004): Bisphenol A induces feminization
in Xenopus laevis tadpoles. Environ Res, Vol. 94, 102-111.
OEHLMANN, J., SCHULTE-OEHLMANN, U., BACHMANN, J., OETKEN, M., LUTZ, I.,
KLOAS, W., TERNES, T. A. (2006): Bisphenol A induces superfeminization in the
Ramshorn snail Marisa cornuarietis (Gastropoda Prosobranchia) at environmentally
relevant concentrations. Environ Health Prospective, Vol. 114, 127-133.
OPITZ, R., LEVY, G., BÖGI, C., LUTZ, I., KLOAS, W. (2002): Endocrine disruption in
fish and amphibians. Recent Res Devel Endocrinol, Vol. 3, 127-170.
YOKOTA, H., TSURUDA, Y., MAEDA, M., OSHIMA, Y., TADOKORO, H., NAKAZONO,
A.,HONJO, T., KOBAYASHI, K. (2000): Effects of bisphenol A on the early live
stage in Japanese medaka (Oryzias latipes). Environ Toxicol and Chem, Vol. 19,
1925-1930.
PAPACONSTANTINOU, A. D., UMBREIT, T. H., FISHER, B. R., GOERING, P. L., LAPPAS,
N. L., BROWN, K. M. (2000): Bisphenol A-induced increase in uterine weight and
alterations in uterine morphology in ovariectomized B6C3F1 Mice: Role of the
estrogen receptor. Toxicol Sci, Vol. 56, 332-339.
PICKFORD, D. B.., HETHERIDGE, M. J., CAUNTER, J. E., TILGHMAN HALL, A.,
HUTCHINSON, T. H. (2003): Assessing chronic toxicity of bisphenol A to larvae of
the African clawed frog (Xenopus laevis) in a flow-through system. Chemosphere,
Vol. 53, 223-235.
RUBIN, B. S., MURRAY, M. K., DAMASSA, D.A., KING, J.C., SOTO, A. M. (2001):
Perinatal exposure to low doses of bisphenol A affects body weight, patterns of
estrous cyclicity, and plasma LH level. Environ Health Persp, Vol. 109, 675-680.
YOSHIDA, M., SHIMOMOTO, T., KATASHIMA, S., WATANABE, G., TAYA, K.,
MAEKAWA, A. (2004): Maternal Exposure to low doses of bisphenol A has no
effects on development of female reproductive tract and uterine carcinogenesis in
Donryu rats. J of Reprod and Develop, Vol. 50, 349-360.
42
Processes at interfaces
Prozesse an Grenzflächen
© IGB 2007
43
44
H ILT , S., S CHÖNFELDER ,I., R UDNICKA , A., C ARLS , R., N IKOLAEVICH ,
N., S UKHODOLOV , A., E NGELHARDT , C.
3.2.1 Reconstruction of pristine morphology, flow,
nutrient conditions and submerged vegetation
of lowland River Spree (Germany) from
palaeomeanders
Rekonstruktion der Referenzbedingungen der Unteren Spree
hinsichtlich Morphologie, Abfluss, Nährstoffkonzentrationen und
Unterwasservegetation aus Paläomäandern
Key words: bankfull palaeodischarge, diatoms, macrofossil remains,
macrophytes, nutrient concentrations, reference conditions, water framework
directive, lowland river
Abstract
The European Water Framework Directive requires the definition of
reference conditions for each type of surface waters as a base to establish a
classification system in which deviations from this high quality status must
be determined. In order to reconstruct pristine conditions in the lower River
Spree we investigated palaeomeanders using palaeohydrological and
palaeolimnological methods. Reconstructions show narrower and shallower
channels for the undisturbed lower Spree as compared to recent conditions.
Flow velocities and discharge at bankfull stage have been smaller in
reconstructed sub-fossil channels and flow variability was higher. Diatominferred total phosphorus concentrations indicate eutrophic to hypertrophic
conditions and suggest naturally slightly lower nutrient levels than today.
These past nutrient conditions, morphology and large numbers of
macrofossil remains indicate optimum growth conditions for submerged
macrophytes growth.
Zusammenfassung
Die EU-Wasserrahmenrichtlinie fordert für jeden Gewässertyp die Definition von Referenzbedingungen als Grundlage für ein Klassifizierungssystem,
das auf Abweichungen von diesem Status höchster Qualität beruht. Um die
Referenzbedingungen der Unteren Spree zu rekonstruieren wurden Paläomäander mittels paläohydrologischer und paläolimnologischer Methoden
untersucht. Die unbeeinflusste Untere Spree war im Vergleich zu heutigen
Bedingungen enger und flacher. Die Fließgeschwindigkeiten und der Abfluss
im bordvollen Zustand waren geringer und die Variabilität der Fließgeschwindigkeiten höher. Die über Diatomeen-Analysen rekonstruierten Gesamtphosphorkonzentrationen waren etwas geringer als die aktuellen und indizieren eutrophe bis hypertrophe Bedingungen für den Referenzzustand.
Eutrophe Bedingungen sowie die rekonstruierte Morphologie und große
Mengen makrofossiler Reste submerser Makrophyten deuten auf optimale
Bedingungen für die Entwicklung submerser Makrophyten.
© IGB 2007
45
3.2.1.1
Introduction
The European Water Framework Directive (Directive 2000/60/EC of the
European Parliament), potentially the most significant piece of legislation
ever to be enacted in the interest of conservation of fresh and saline
ecosystems, requires the restoration of aquatic habitats to a so-called good
ecological status. For each ecotype, reference conditions must be defined as
a base to establish a classification system in which deviations from this
pristine status must be determined. Establishment of reference conditions
from existing sites is difficult as there are few, if any, such sites available in
Europe (Moss et al. 2003). Thus, there is a need to determine the reference
conditions, for example with palaeoecological reconstructions.
Reconstructions increase in significance when multiple palaeoindicators are
used (Brown 2002), e.g. when the reconstruction relies on both
palaeohydrological and palaeolimnological parameters.
The following study was carried out to reconstruct the reference
conditions regarding hydromorphology, flow characteristics, bankfull
discharge, nutrient conditions and the aquatic vegetation in the lower River
Spree (North-eastern Germany). Palaeomeanders suitable for these
reconstructions were identified using aerial infrared photographs,
sedimentological analyses of sediment cores from transects across
palaeomeanders and geodetic surveys. For the reconstruction of the bankfull
palaeodischarge, a model was developed that includes a parametrization of
the velocity distribution in the recent river channel under local conditions of
flow resistance, thus, avoiding the empirical formulas commonly used in
palaeohydrological reconstruction.
Over longer time scales (decades and centuries) a meandering river forms
a channel, which is able to transport the amount of water and sediment
supplied by the catchment basin (Leopold 1994). This quasi-equilibrium
between discharge and channel morphology of pristine rivers is the prerequisite for the reconstruction of hydrological characteristics using
palaeochannels. The relationship between the reconstructed channel
morphology and the unknown palaeodischarge is often defined through a
single, dominant discharge that produces the observed channel. It is often
assumed to be close to bankfull (Lauer & Parker 2006). Thus the key to
determining discharge under undisturbed flow conditions (hydraulic
reference conditions) is the reconstruction of the only water stage that leaves
a clear trace in the morphology of a river channel, the stage of the so-called
bankfull discharge (Rotnicki 1991).
Palaeolimnological reconstructions can be used when sediments
accumulate in continuous sequences, for example, in deep lakes (e.g. Lotter
2001) and often also in shallow lakes (e.g. Bennion et al. 2001). In rivers,
which have high sediment dynamics, continuous sedimentation is limited to
low current areas (e.g. deposition zones at the inner bank of the meander
loop). Thus, cores drilled across a meander apexes would (at the inner bank)
contain settled material that, at least partly, consists of autochthonous microand macrofossils from the flowing river. The succession of any meandering
river further emphasises that meander loops are characterized mainly by
46
expansion until the meandering pattern is destroyed by a cut-off. Once
abandoned these former parts of the main river channel accumulate
sediments that still contain river-borne material that enters the oxbow lake
during flooding events, but an increasing share of material characterizing the
oxbow-lake-stage. The latter can be distinguished from the flowing-riverstage by its sediment texture and changes in the phytoplankton and
macrophytes species composition. Macrofossils of palaeomeanders only
partly originate from the main river, but can be used to reconstruct pristine
river conditions when used in combination with information on
hydromorphological conditions and nutrient concentrations.
3.2.1.2
In order to find suitable palaeomeanders for the reconstruction of pristine
hydrological and limnological conditions of the lower River Spree we used
colour-infrared (CIR) aerial photographs of the Drahendorfer Spree. In a
first step we selected all palaeomeanders with exact delimitation and a
complete meander bend. Afterwards sediment cores were taken in the apex,
and meanders showing a clear boundary between the active channel
documented by mineral material (especially sand and gravel) and the silting
up material (muds, peat) were selected for further investigation.
Subsequently, cross profiles were determined by sediment core drillings in
the apex domain of the selected meanders. Palaeomeanders suitable for the
calculation of the cross-sectional area at bankfull stage were dated and those
representing periods with low anthropogenic impact used for the analysis of
diatoms and macrofossil remains to reconstruct nutrient concentrations and
the colonization with aquatic macrophytes, respectively. Detailed
information about the methodology can be found in Hilt et al. (2007).
Fig. 1:. Reconstructed vertical cross-section and bankfull stage of investigated
palaeomeander and approximation of the detected cross-profile by a parabolic function
© IGB 2007
47
3.2.1.3
Results
TN
:T
P
Diatom Zone
(m
g*
l -1)
DI
-
DI
-T
N
0
Ac
hn
a
Fr nth
a
e
Ac gila s h
hn ria un
Na a ca ga
vic nth pu ric
e
a
Au ula s m cina (G
la pu in va run
co
p u
o
se ula tiss r. m w)
ira
K im es G
Au
gr ützi a K ole run
la
ng üt pt ow
co
an
z
se
ul
va in a (R
at
ira
sm
a ( r. p g va ab
am
Eh up r. en
al
lb
u m h
re
bi
en
gu
nb la inu ors
th
a (
er
tis t)
Au
ic
G
g)
sim Ra
la
Fr
r
u
Si
Co co
ag
no
a ben
m
ila
c s
w
on
ho
Cy co eira
)
r
i
se
rs
Si
as
clo nei la
t
m
n
pp
G s s e
se
on
om te pl vis
.
ns
se
Fr ph ph ace sim
u
n
ag o an n a
la
t
n
to
St ila e os ul (G
a
e r m
r
M pha ia u a p dub var uno
el n ln a iu . li w
o o a rv s
n )
G sira disc (Ni ulu (Fri eat Kra
om v u tzs m ck a m
c (K e) (E m
p ar s
G hon ians neo h ) L ütz Ro hre er
o
e
A a a in u n
Fr mph ma gastra nge g ) Knd ber
g)
ag o
-B ü
m rd e
Va
# ilar nem icr h a Ha ert tzin
nH
of ia a op
ka alo g v
ta ca s
eu
ns t v ar
xa p ar us K
rc
s
a
uc co
üt
on r. . pa
k
u
zin
in ph
& ln rvu
ao a
DI
g
a
H
-T
th gu
ick se lum
er s G
P
el ns
(µ
v
r
u
ar eg
g*
la
s . or
l -1)
to
y
Of 15 palaeomeanders identified from aerial photographs of the floodplain
of the Drahendorfer Spree, eight were suitable for the reconstruction of
hydromorphological characteristics (see Fig. 1 in Hilt et al. 2007). Following
dating, three sites (in downstream order D5, D7, D1) were chosen for
further calculations as they represent periods of low anthropogenic impact.
Channel width at bankfull stage varied between 16 and 21.5 m and mean
depth between 0.64 and 0.99 m.
A flow model was developed for the reconstruction of bankfull flow
characteristics and discharge of the lower River Spree (for details see Hilt et
al. 2007). This model was applied to the surveyed morphometrical data of
the palaeomeanders D5, D7, and D1. Their cross-sections were
approximated by a parabolic function (Fig. 1). Using the bankfull stage, flow
velocity at each point of the cross-section was calculated using a closed
system of analytical equations (Hilt et al. 2007). Integration of the calculated
flow velocities over the cross-sectional area results in the mean flow velocity.
Calculated bankfull discharges varied between 5.5 and 10.3 m³ s-1 (Table 1).
10
Core depth (cm)
20
30
40
II
50
60
70
80
90
I
100
0 20
0 20 40 20 0 20
Relative diatom abundance (%)
0 20
20
80 120 30 90 150 0.8
2.4
10 20 30
Fig. 2: Relative abundance of important diatom taxa, number of differentiated taxa, diatominferred total phosphorus (DI-TP), DI-total nitrogen (TN) and DI-TN:TP in a sediment core of
palaeomeander D5 of the Drahendorfer Spree.
Diatom-based reconstructions were performed for the core of
palaeomeander D5. The diatom assemblage can be divided into two zones
(Fig. 2). Zone I (105-85 cm, ~1100–500 BC) was characterized by benthic
Achnanthes hungaria (Grunow) Grunow (3-13%), Achnanthes minutissima
Kützing var. minutissima (1-5%) and Navicula pupula Kützing var. pupula (05%), as well as tychoplanktonic Fragilaria capucina var. mesolepta (Rabenhorst)
Rabenhorst (1-6%). Zone II (80-1 cm, ~500 BC to 2003) was characterized
by increased abundances of planktonic Aulacoseira ambigua (2-23%) and
Aulacoseira granulata (4-34 %), as well as taxa typically found in bogs, such as
taxa from the genus Eunotia and Pinnularia. Additionally, small, benthic
Fragilaria spp. (F. brevistriata Grunow, F. construens (Ehrenberg) Grunow f.,
48
construens, F. construens f. binodis (Ehrenberg) Hustedt and F. construens f. venter
(Ehrenberg) Hustedt), Gomphonema micropus Kützing, Gomphonema sarcophagus
Gregory, as well as planktonic Aulacoseira laevissima (Grunow) Krammer and
tychoplanktonic Melosira varians Agardh, which occurred in low abundances
in zone I (together < 18%), comprised 11-32% of the assemblage in zone II.
Diatom-inferred total phosphorus (DI-TP) increased from 59-73 µg L-1 in
zone I to 59-98 µg L-1 in zone II, while DI-TN hardly changed throughout
the core (median zone I = 1.3 mg L-1, median zone II = 1.5 mg L-1) (Fig. 2).
Macrofossil remains of both, submerged or floating-leaved plants (seven
taxa) and emergent aquatic plants (eight taxa) were found at the base of
palaeomeander cores D5, D7 and D1. For example; seeds of the submerged
genus Ranunculus sect. Batrachium were present in all three meanders. In
contrast, remains of submerged or floating-leaved species were absent in the
upper sediments (except for Lemna spp.; core D5, zone II in Fig. 3), whereas
most emergent species were found throughout the core (Fig. 3).
Floating
Emergent
Po
ta
m
og
et
on
ob
tu
si
fo
liu
s
R
an
St unc
ra ul
tio us
te s
N
s ec
ym
al t.
oi B
de a
N ph
up ae
s tra
ch
Le har a a
iu
m lu lba
m
Al na tea
is sp
m p
a .
pl
an
ta
go
O
-a
en
qu
an
at
t
he
ic
M
a
en
aq
th
u
a
a
aq tica
Ly
au
co
tic
C pu
ar s
a
ex eu
sp rop
Ju
p. a
eu
nc
s
Sc us
irp sp
us p.
sp
p.
Submerged
0
10
Core depth (cm)
20
30
40
50
60
70
80
90
100
110
0
20 40 60 0
0
20
0
0 0
20 40
20
20
0
20
Macrofossil remains (n * 100 ml-1)
Fig. 3: Macrofossil remains in a sediment core of palaeomeander D5 of the Drahendorfer
Spree.
3.2.1.4
Discussion
The palaeomeanders investigated in our study represent reference conditions
of the lower River Spree. AMS dating suggests that the sediments at the base
of three investigated cores (D5, D7 and D1) represent the late Subboreal/early Sub-atlantic, a time of low anthropogenic impact in the
catchment of the River Spree (Bork et al. 1998, Driescher & Behrendt 2002).
The pristine lower River Spree had narrower and shallower channels
compared to the recent river (Table 1). Both mean flow velocities at bankfull
stage were slower and flow variability was higher in the reconstructed
subfossil channels of the Lower Spree.
© IGB 2007
49
Tab. 1: Hydrological characteristics at bankfull discharge of the recent (meander near
Neubrück) and the pristine lower River Spree (mean of palaeomeanders D5, D7, D1).
Discharge
Meander slope
Mean width at bankfull stage
Mean depth at bankfull stage
Mean flow velocity
Local characteristic (shear) velocity
Recent
Reconstructed
51.7 m³ s -1
0.00005
35.2 m
1.63 m
0.9 m s -1
2.8 cm s -1
8.2 m³ s -1
0.00008
19.6 m
0.79 m
0.53 m s -1
2.4 cm s -1
Palaeohydrological reconstructions are all subject to error, because of
limited or unreliable data or simplifications inherent to model formulas
(Williams 1988). Our newly derived approach to identify suitable
palaeomeanders for reconstructions using aerial photography in combination
with geomorphology resulted in rather robust hydromorphological data sets.
The estimation of bankfull discharge by planar parameters of a
palaeomeander such as width (e.g. Durys (1977) formula) or width and
sinuosity (e.g. Rundquists (1975) formula) is mostly less accurate (Knighton
1998) than that from a combination of planar, cross-sectional parameters,
and slope (e.g. Williams` (1978) formula). Hydraulically based equations for
discharge as those developed by Grishanin (1979) or Rotnicki (1991)
additionally involve the flow resistance to which the velocity (and thus the
discharge) is strongly related. Our model calculates the flow velocity
distribution over a bankfull cross-sectional area directly, using a
parametrization developed from field data in the recent Drahendorfer Spree.
Discharge in this model yields from the mean cross-sectional velocity and
the area at bankfull discharge. Our bankfull discharge reconstruction is in
good agreement with the more complex models of Williams (1978) and
Rotnicki (1991). Our model is more sensitive to the local slope of the
meander than the most advanced models of Williams (1978) and Rotnicki
(1991), where slope occurs with the exponent 0.28 and 0.5, respectively. To
illustrate the uncertainty of the modelled bankfull discharge, the maximum
possible (slope of the floodplain) and the minimum possible slope (detected
slope of the recent Drahendorfer Spree measured in field) was used instead
of slope calculated by the equation for meandering rivers (Hilt et al. 2007).
The resulting maximum bankfull discharge values for D1, D7, D5 are then
11.2 m³ s-1, 5.8 m³ s-1 and 9.3 m³ s-1, respectively; the minimum values are 8
m³ s-1, 3.9 m³ s-1, and 6.3 m³ s-1, respectively. When these three
palaeomeanders are considered, the modelled mean bankfull discharge is 8.2
m³ s-1 (6.1-8.7 m³ s-1, Table 1). In sand-bed rivers, the grain roughness
(which is expressed by Manning´s number in Rotnicki`s formula) is often
less important than other components of the total flow resistance resulting
from frictional effects at the bank and the bed of the channel. The flow
model presented here includes these effects and should therefore minimize
the error usually associated with reconstructed bankfull discharge.
The difference between the recent (~52 m³ s-1) and the reconstructed (~8
m³ s-1) bankfull discharge of the Lower River Spree can only partly be
explained by the current additional input of mining water into the Spree
(~14 m³ s-1). Similarly, climatic conditions in Central Europe did not change
50
dramatically during the last 3000 years (Lamb 1977, Glaser 2001) and can
therefore not fully explain the discharge increase either. For example, using a
macrophysical runoff model driven solely by climatic data, Bryson et al.
(2003) simulated a less than 10% greater discharge of Central European
Rivers in the middle Holocene than today. In contrast, many examples
indicate that river discharge may greatly increase when natural vegetation is
cleared (Bosch & Hewlett 1982, Sahin & Hall 1996, Foley et al. 2005) as
deforestation alters both the balance between rainfall and evapotranspiration
and the runoff response of a drainage basin. In Germany, the forested area
declined from 90% in the 6th century to 15% in the early 14th century
(Schmidtchen & Bork 2003). Furthermore, channelization, bank protection
and river regulation measures, typical for the River Spree (Driescher 2002),
also increase flow velocity and transport capacity of a river. For example,
bankfull discharge of the River Raba (Poland) increased by a factor of 2.4
after channelization due to reduced floodplain storage and greater
concentration of water within the channel zone (Wyzga 1996). Therefore,
land-use changes and river straightening were probably responsible for most
of the inferred discharge changes in the lower River Spree.
Diatom assemblages in zone I of the investigated core of palaeomeander
D5 are assumed to represent reference conditions of the River Drahendorfer
Spree for the following reasons: 1) Dating techniques suggest that zone I
represents ~1100-500 BC, a time in which the study area was hardly
inhabited (Driescher & Behrendt 2002). Therefore, anthropogenic impact on
the water quality was probably very low or absent in zone I. 2) Taxa present
in diatom zone I are typical taxa from the River Drahendorfer Spree. For
example, in the River Drahendorfer Spree many planktonic diatoms, such as
Aulacoseira laevissima, originate in Lake Schwielochsee (I. Schönfelder,
unpublished data), which is located just 12 km upstream of the study site.
These taxa were abundant in zone I. Additionally, taxa typically reflecting
oxbow rather than river conditions were almost absent in zone I, but
common in zone II, such as taxa typically found in bogs. Overall, diatominferred chemical water conditions in zone I suggest that the Drahendorfer
Spree had naturally eutrophic to hypereutrophic nutrient levels. Still,
reference TP levels (~ 62 µg L-1) are lower and reference TN levels (~ 1.3
mg L-1) slightly lower than today (94 µg L-1 and 1.8 mg L-1, respectively).
Naturally high nutrient levels could be due to the geology of the catchment
area (Driescher 2002). Another possible source of nitrogen is Lake
Schwielochsee, which probably had naturally favourable conditions for
nitrogen-fixing blue-green algae during the summer months (I. Schönfelder,
unpublished data). Similarly high or even higher nutrient reference
conditions were inferred for flushed lakes and river reaches both up- and
downstream of Drahendorfer Spree (Hilt et al. 2007) as well as other lakes in
the vicinity and in River Havel (Schönfelder 1997).
The reconstructed low water depth (Table 1), diatom-inferred eutrophic
to hypertrophic conditions and large numbers of macrofossil remains
© IGB 2007
51
indicate optimum growth conditions for submerged macrophytes in the
pristine lower River Spree. Due to the shallow water and the small river
width (Table 1), the main limiting factor for submerged macrophytes in the
pristine lower River Spree has probably been shading by bankside trees
(Dawson & Kern-Hansen 1978). Higher flow variability generally results in a
less uniform colonization and higher species diversity (Hey et al. 1994). In
addition to submerged species of the genera Ranunculus sect. Batrachium
(Water-crowfoot) and Potamogeton (pondweeds) that were detected by seeds,
other species probably also occurred under pristine conditions. Birks (2000)
already pointed out that lack of seed representation may result from
vegetative production for survival. In reaches with higher flowing velocities
and water depths above 1 m, a community dominated by River Watercrowfoot (Ranunculus fluitans) may have occurred, whereas slow flowing
stretches were probably dominated by species-rich Sparganium emersum
communities comparable to the present vegetation in the River Müggelspree
(Schulz et al. 2003). Similar to the diatoms, all submerged and emergent
macrophyte species detected indicate eutrophic conditions (Krausch 1996).
Acknowledgement
We acknowledge the help of Lina Wischnewsky and Arthur Brande during
macrofossil counting and determination, Christiane Herzog and Jörg
Gelbrecht during diatom preparation, Petra Werner for linguistic
improvements and Matthias Rehfeld-Klein, Jörg Schönfelder, Jan Köhler
and Martin Pusch for scientific discussions. The study was financially
supported by the Senate of Berlin.
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54
W IESE , B., N ÜTZMANN , G.
3.2.2 Infiltration of surface water into groundwater under transient pressure gradients
Infiltration von Oberflächenwasser in den Grundwasserleiter bei
instationären Druckgradienten
Key words: surface water, groundwater, bank filtration, infiltration, leakage
coefficient, numerical modelling
Abstract
Several kinds of managed aquifer recharge techniques provide very good
purification of surface water since more than 100 years. In order to maintain
a reliable supply of clean water, they are becoming increasingly popular all
over the world. Especially bank filtration methods require low technical
effort. Exemplarily, at a test site at Lake Tegel, Berlin, Germany, the
hydraulic processes of infiltration are modelled.
By means of 3D long term regional and transient hydraulic modelling it
was detected that the existing approaches for determining the leakance
induce large errors in the water balance and describe the infiltration zone
insufficiently. The leakance could be identified to be triggered by the
groundwater table, causing air exchange and intrusion of atmospheric
oxygen, which reduces clogging by altered redox conditions by at least one
order of magnitude. This causes that changes of the groundwater table are
mitigated much more than previously assumed. Taking these findings into
account, a transient water balance is determined and bank filtration ratios are
quantified.
Zusammenfassung
Seit mehr als 100 Jahren wird Oberflächenwasser mit verschiedenen
Verfahren versickert, wobei sich dessen Qualität stark verbessert. Sie finden
zunehmend weltweit Anwendung, um eine zuverlässige Versorgung mit
sauberem
Trinkwasser
zu
gewährleisten.
Insbesondere
die
Uferfiltrationstechnik erfordert nur einen geringen technischen Aufwand.
Am Beispiel eines Untersuchungsgebiets am Tegeler See in Berlin werden die
hydraulischen Prozesse modelliert.
Die regionale, instationäre und 3-dimensionale Modellierung eines
langen Zeitraums zeigt, dass die bisher verwendeten linearen Ansätze zur
Beschreibung der Durchlässigkeit der Kolmationsschicht sowohl die
infiltrierten Wassermengen als auch die Infiltrationsprozesse nur
unzureichend wiedergeben. Grundwasserpiegelschwankungen werden
stärker als bisher angenommen gedämpft. Als Folge dieser
Wasserspiegelschwankungen wird die Bodenluft in der ungesättigten
Bodenzone ausgetauscht und Sauerstoff eingetragen. Auf diese Weise erhöht
sich die Durchlässigkeit der Kolmationsschicht um mindestens eine
© IGB 2007
55
Größenordnung. Auf Grundlage dieser Ergebnisse wurden eine instationäre
Wasserbilanz aufgestellt und die Uferfiltratanteile bestimmt.
3.2.2.1
Introduction
During bank filtration horizontal or vertical collector wells induce a hydraulic
gradient which causes infiltration of surface water into the aquifer. During
the underground passage mechanical as well as biogeochemical reactions
proceed, substantially improving the water quality regarding suspended
solids, algae, pathogens and other bacteria, algal toxins, dissolved organic
carbon, nitrate, organic pollutants and pharmaceutical residues. These
constituents are eliminated or significantly reduced, peak concentrations of
the surface water are mitigated. In Europe, predominatly river bank filtration
is used (Doussan et al. 1993, Grischek et al. 2003), and especially in lowland
regions, where shallow lakes form a part of river system, bank filtration was
operated also at lakes (Miettinen et al. 1997, Fritz et al. 2004).
For the quantitative and qualitative management of bank filtration
systems, flow velocities, travel times and infiltration capacities need to be
known. The latter is the crucial point because it depends on well operation
and hydraulic resistance of lake bed sediments, also affecting by clogging.
The permeability of river beds is known to be time variable because of
continuous change by shear stress, bed load transport, discharge, water level
fluctuation and other factors (Huettel et al. 2003). Exchange coefficients
between lakes and groundwater are not reported to be time-variant, neither
under natural nor anthropogenic conditions.
The bank filtration system at Lake Tegel, NW of Berlin, is characterized
by highly transient well operation whereby hydraulic head differences
between lake and groundwater show strong temporal variations. To model
the groundwater response, however, the dynamic infiltration from surface
water into the adjacent aquifer cannot be simulated assuming a linear
relationship, where the water fluxes across the aquatic sediment surface is
proportional to the hydraulic head differences, and the unknown factor is
defined as leakage coefficient (Bear 1972).
The observed highly variable infiltration dynamics reveal that typically
used boundary conditions of third order or something like that are
insufficient. Previously applied nonlinear approaches regarding depthdependent changes of permeability and temperature effects also could not
describe the mechanisms (Schubert 2002, Lin et al. 2003, Holzbecher et al.
2006). They do neither quantify the mass transfer fluxes nor its spatial
distribution. Here a gap in mechanistic understanding and modelling
approaches of exchange between surface water and groundwater exists.
The present study discussed infiltration behaviour of a lake bank
filtration system, showing transient infiltration dynamics on different
temporal and spatial scales. Different assumptions about mathematical
formulation and distribution of leakage are made and expressed in four
differing paramatrizations. The goodness of tempospatial infiltration
characteristics is assessed by comparison with time-series of hydraulic heads,
56
in situ infiltration measurements and geochemical data. The comprehensive
interpretion shows that infiltration can only be described sufficiently when
leakage is modelled transiently, considering the interaction of water flow, air
flow in the unsaturated zone and biological processes in the clogging layer.
3.2.2.2
Investigation area
The investigated area is located at Lake Tegel in the NW of Berlin, Germany
(Figure 1). Here, Berlin largest waterworks is pumping about 45 million m3
per year from 6 well fields around the lake and from two on the islands. This
affects groundwater flow within an area of 50 km2.
Fig. 1: Lake Tegel and adjacent well fields. Small red dots indicate vertical collector wells,
the red circle on Scharfenberg indicates a horizontal collector well. GWA denotes
groundwater recharge ponds.
The two upper aquifers in the model domain as well as Lake Tegel itself
are formed during the Saale ice-age. The 1st aquifer is unconfined consists of
fine to coarse sand, has a thickness of about 15 m and a hydraulic
conductivity of about 3.5*10-4 m/s. The 2nd and main aquifer also consists of
fine to coarse sand with a thicknes between 25 to 50 m, covered by a glacial
till of about 4 m thickness. The hydraulic conductivities range from 2*10-4
m/s to 5.5*10-4 m/s. In this 2th aquifer the vertical collector wells are
screened. Both aquifers are hydraulically well connected.
Hydraulic Modelling
The model domain is depicted in Figure 2, including the two upper aquifers,
where the waterweorks abstracts raw water. In order to focus on the
© IGB 2007
57
infiltration process at the Lake Tegel and to avoid a large-scale regional
model set-up, the size of the model is reduced through the appropriate
choice of boundary conditions, which are discussed in detail in Wiese (2006).
Simulation is carried out between January 1st 1998 and April 30th 2005. The
first 90 days are simulated steady state; afterwards simulation is transient with
weekly discretization. Spatially the model is discretized by 7 layers, with a
thickness between 4 m and 8 m, the horizontal cell size varies between 5 * 5
m close to the transect to 15 * 50 m next to the boundary. The model is set
up under PMWinPro7 (WebTech360 2003) with the flow model of
MODFLOW (Harbaugh et al. 2000).
Fig. 2: Top view on the model domain with boundary conditions. The coloured symbols
indicate observation wells.
Parameter estimation
The focus of the model calibration is set to an adequate description of the
leakage because this study showed that it is the most sensitive parameter. As
shown in Figure 3, simulation of hydraulic head time series doesn’t match
the observed ones using overall constant leakage coefficients. With high
leakage in shallow water decreasing to zero at 5 m depth, the model
calculates too large infiltration rates or is entirely drained. Therefore, the
model is parametrized as follows. Four scenarios (cases) are derived based on
different assumptions about the description of infiltration (Wiese 2006). For
case 1 to case 3, the spatially distribution of the leakage is defined by 8 zones
(or parameters), each comprising an elevation interval of 1 m between 25 m
and 32 m NN, see Figure 4.
58
Fig. 3: Observed and measured piezometric heads at observation well TEG050 with two
temporally and spatially constant leakage coefficients.
In case 2 and 3 their values are additionally multiplied by a timedependent function, so that the temporal and spatial distribution of the
leakage could be modelled. For case 4 it is assumed that the leakage is
triggered temporally and spatially by the thickness of the unsaturated zone
below the infiltration area. Thus, the numbers of parameters to be fitted are
different for each case: 9 parameters for case 1, 11 parameters for case 2, 54
parameters for case 3 and 5 parameters for case 4.
Fig. 4: Spatial distribution of the depth dependent leakage. Each colour represents one
parameter.
Due to the great impact of infiltration, the hydraulic conductivity of the
aquifer is insensitive to calibration. The hydraulic model has been calibrated
using PEST (Doherty 2003). Because measurement errors are not available
and the impact of the structure of observations is much higher, each single
hydraulic head measurement is weighted according to the time for which it is
© IGB 2007
59
representative, divided by the standard deviation of all observations of the
particular piezometer.
Transport modelling
Transport simulations are carried out in order to show the plausibility of the
concept of temporal variant leakage. Due to restricted data and travel times
they are carried out only within a small area of the flow model domain (see
Figure 2, around transect in the center of the area including the observation
wells 3312 and 3313). The species 18O and temperature are modelled. 18O is
an ideal tracer and data are available between 2002 and 2005. Temperature is
modelled because time series are available since 2000.
The transport model was set up with the following parameters: effective
porosity of 0.22, aquifer bulk density of 1.820 g/cm3, aquifer heat capacity of
cs = 800 J kg-1 K-1, water heat capacity of cw = 4184 J kg-1 K-1, and thermal
diffusivity of 1.3 * 10-6 m2/s. Dispersivity is insensitive up to a length of 1 m
and a larger dispersivity deteriorates the fit. In order to minimize mass
balance error it is set to nil. Transport is simulated with MT3DMS (Zheng &
Wang 1999) and the HMOC particle tracking scheme.
3.2.2.3
Groundwater flow
The comparison of measured and simulated hydrographs of the observation
well TEG050 (as a representative example) shows the general behaviour of
the hydraulic model. This observation well is located far enough from the
well field, so that switching of wells and effects of local aquifer configuration
are mitigated. The boundaries are far enough, thus, simulated heads are
sensitive to the model parameterization. The variations of hydraulic head are
induced by pumping regime of the waterworks Tegel, principially of well
field West.
Fig. 5: Measured and simulated piezometric heads (case 2 and 3) at observation well
TEG050.
60
The fit of all four cases appears acceptable; in Figure 5 comparison of
measured and simulated results are shown for the cases 2 and 3. Comparing
the objective function for TEG050, case 3 is the best fit, the goodness of
case 2 and 4 is similar, and case1 is the worst representation of the observed
groundwater dynamics.
The ratio of 1.6 between the largest and smallest value of the objective
function is lowest for observation well 3301. Daily measurements are
included into the model, which has a weekly time discretization. Thus, the
model can only be optimized to a mean curve through the daily fluctuations.
Though observation well 3301 contributes between 40% (case 1) and 70%
(case 3) to the objective function, it shall be emphasized, that parameters
only change slightly if it is taken out from the objective function. This is a
strong indication that the parameterization is physically based (Hill 1998).
Leakage
The leakage coefficients are first approximatively calculated from in situ
measurements, where the thickness of the clogging layer is assumed to be 10
cm (Wiese 2006). In Figure 6 measured and depth dependent leakage
coefficients are depicted for the four cases to be studied. The depth
dependency as well as the time variability of these coefficients is determined
by inverse modelling.
Fig. 6: Measured and modelled leakage of the lake bed. Each point represents the mean
value at a certain observation location. Measurements of Hoffmann (2006) have been
carried out between March 2004 and February 2005, measurements of this study in June
and July 2004. Modelled values are adapted to the hydraulic situation in June/July 2004.
In order to implement temporal variant leakage coefficients as well as
easy communication with PEST, the MODFLOW2000 code has been
modified. The resulting hydraulic heads are quite similar for both, case 2 and
3 (Fig. 5), though the parameterisation is quite different (Fig. 6). Under the
premise of a linear temporal behaviour, the leakage is higher in greater depth.
If the temporal behaviour is not forced to be linear, measurements indicate
© IGB 2007
61
that the pattern is quite variable (Fig. 7) and the leakage is higher in shallow
water (Fig. 6). A higher temporal resolution neither led to a considerably
lower objective function nor resulted in a significantly different temporal
behaviour.
Fig. 7: Temporal leakage for case 2 and 3 (left axis); the pumping rate (right axis) is the
monthly average of well field West.
The leakage has revealed to be temporally variable. Potentiall, many
mechanisms could cause the leakage to vary with time: Viscosity of water
due to temperature effects, compression of lake bed by changing pressure
head, clogging by suspended matter, chemical or bioclogging etc.
Fig. 8: Measured and simulated piezometric heads at observation well TEG050 with case 4
parameterization.
As show in Figure 7, for case 3 the leakage is correlated (R2=0.42) with
the pumping rate and reacts with a small delay, but the observed hydraulic
heads of the groundwater indicate an unsaturated zone for the shallower
regions of Lake Tegel, which would cause the hydraulic independence of the
62
infiltration to the groundwater table. If the thickness of the clogging layer is
small in comparison to the hydraulic head differences, high infiltration rates
could occur because an increased hydraulic gradient across the clogging layer
increases infiltration more than proportional. Using a simple, not physical
based function of the leakage depending on the thickness of the unsaturated
zone, the resulting distribution is shown in Figure 6 (turquoise line).
The simulated hydraulic heads at observation well TEG050 are plotted in
Figure 8. The application of case 4 instead of case 2 or case 3 improves the
fit of observed and simulated hydraulic heads in general. The temporal
dynamic coincides better, and also the arithmetic mean of hydraulic head in
observation well 6053 between January 1998 and April 2002 of 28.84 m NN
of case 4 is much closer to the observed mean of 28.81 m NN than case 3
with 29.23 m NN. The current parameterisation reproduces the most
important temporal behaviour, and the reduction from 45 to 2 parameters is
a significant improvement in parameter parsimony and solution uniqueness.
Transport simulation
The results of transport model are obtained using the hydraulic model of
case 3 and transport parameters described above. Since the model is only
calibrated using hydraulic data, the goodness of the presented transport
behaviour indicate the correctness of the flow field (see Fig. 9). Temperature
is only shown for well 13. Only for temperature the inland boundary values
are well known thus results are very important for abstraction wells. As one
example, the resulting travel times between the infiltration zone and
observation wells 3301 and 3302 are approximately 4 month.
Fig. 9: Selected results of transport modelling. 18O is shown for observation wells 3301,
3302, TEG371op, TEG371up, Well 12 and Well 13 for a period between 2002 and 2005.
Temperature time series is presented for Well 13 for a perid between 2000 and 2005.
© IGB 2007
63
Acknowledgement
This study was carried out within the NASRI (Natural and Artificial Systems
for Recharge and Infiltration) project of the KompetenzZentrum Wasser
Berlin. The authors thank Berliner Wasser Betriebe and Veolia Water for the
financial support of this study.
References
BEAR, J. (1972): Dynamics of fluids in porous media. Dover Publ., New York.
DOHERTY, J. (2003): PEST – Model independent parameter estimation user manual,
Watermark Numerical Computing, 336 pp.
DOUSSAN, C., TOMA, A., PARIS, B., POITEVIN, G, LEDOUX, E., DETAY, M. (1993):
Coupled use of thermal and hydaulic data characterize river-groundwater
exchange. J. Hydrol., 153, 215-229.
FRITZ, B., RINCK-PFEIFFER, S., NÜTZMANN, G., HEINZMANN, B. (2004):
Conservation of water resources in Berlin, Germany, through different re-use of
water. In: Steenvorden, J., Endreny, Th. (eds.): Wasrewater re-use and
groundwater quality. IAHS publ. 285, 48-52.
GRISCHEK, T., SCHOENHEINZ, D., WORCH, E., HISCOCK, K. (2003): Bank filtration in
Europe – an overview. In: Dillon. P. (eds.): Management of aquifer recharge for
sustainability. Balkema, Lisse, 485-488.
HARBAUGH, A. W., BANTA, E. R., HILL, M. C., MCDONALD, M. G. (2000):
MODFLOW-2000,The U. S. Geological Survey modular groundwater model.
Open-file report 00-92.
HILL, M. C. (1998): Methods and guidelines for effective model calibration. U.S.
Geological Survey Water Resources Investigations Report 98-4005, Denver, CO.
HOLZBECHER, E., ENGELMANN, B., NÜTZMANN, G. (2006): The viscosity effect on
infiltrating surface water. Hydrogeol. J. (under review).
HUETTEL, M., ROY, H., PRECHT, E., EHRENHAUSS, S. (2003): Hydrodynamical impact
on biogeochemical processes in aquatic sediments. Hydrobiologia, 494, 231-236.
LIN, C., GREENWALD, D., BANIN, A. (2003): Temperature dependence of infiltration
rate during large-scale water recharge into soils. Soil Sci. Soc. Am. J., 67, 487-493.
MIETTINEN, I., VARTIAINEN, T., MARTIKAINEN, P. J. (1997): Microbial growth and
assimilable organic carbon in Finnish drinking waters. Water Science Technol. 35,
301-306.
SCHUBERT, J. (2002): Hydraulic aspects of riverbank filtrtaion – field studies. J.
Hydrol., 266, 145-161.
WEBTECH360 (2003): Processing Modflow Pro – Users Manual, Fairbanks, USA, 413
pp.
WIESE, B. (2006): Spatially and temporally scaled inverse hydraulic modelling, multitracer transport modelling and interaction with geochemical processes at a highly
transient bank filtration site. PhD thesis, Geographical Institut, HumboldtUniversity of Berlin, 233 pp.
ZHENG, C., WANG, P. P. (1999): MT3DMS – a modular three-dimensional
multispecies model for simulation of advection, dispersion and chemical reactions
of contaminants in groundwater systems, Documentation and User’s Guide, Rep.
SERDP-99-1, Vicksburg, M.S.
64
G OLOSOV , S., K IRILLIN , G.
3.2.3 Modelling dissolved oxygen dynamics in icecovered shallow lakes
Modellierung des dynamischen Sauerstoffverbrauchs in zugefrorenen
Flachseen
Key words: water quality, anaerobic zone, thermal regime, shallow lakes
Abstract
Based on the observational data from five freezing lakes located in
Northwestern Russia and North America, the effect of the heat interaction
between a water column and sediments on the formation, development, and
duration of existence of anaerobic zones in ice-covered lakes is estimated. A
simple one-dimensional model that describes the formation and
development of the dissolved oxygen deficit in shallow ice-covered lakes is
suggested. The model reproduces the main features of dissolved oxygen
dynamics during the ice-covered period, that is, the vertical structure, the
thickness and rate of an increase of the anaerobic zone in bottom layers. The
model verification is performed against observational data. Results of
verification show that the model adequately describes the dissolved oxygen
dynamics in winter. The rates of DO consumption by bacterial plankton and
by bottom sediments, depending on the heat transfer through the watersediment interface, are calculated. Received results allow predicting
appearance of potentially dangerous anaerobic zones in shallow lakes and in
separate lake areas in dependence on the thermal regime changes.
Zusammenfassung
Auf der Datengrundlage von fünf Seen aus dem Nordwesten Russlands und
dem Norden Amerikas soll abgeschätzt werden, welche Rolle der
Wärmeaustausch zwischen Wassersäule und Sediment bei der Bildung und
der räumlichen und zeitlichen Entwicklung anaerober Zonen in eisbedeckten
Flachseen spielt. Dafür wird ein einfaches 1-D-Modell vorgeschlagen, mit
Hilfe dessen die Entstehung und der Verlauf eines Mangels an gelöstem
Sauerstoff unter Eis beschrieben werden kann. Das Modell gibt die
wesentlichen Merkmale des dynamischen Verhaltens von gelöstem
Sauerstoff während der Eisbedeckung wieder, nämlich die Dicke der
anaeroben Schicht, ihre vertikale Struktur und die Rate, mit der sie sich
ausdehnt. Der Vergleich der Modellsimulationen mit den Messdaten zeigt,
daß die Dynamik des gelösten Sauerstoffs im Winter vom Modell adequat
widergespiegelt wird. Die vom Wärmeaustausch an der Wasser-SedimentGrenze abhängigen Raten, mit denen der gelöste Sauerstoff von bakteriellem
Plankton und dem Sediment verbraucht wird, stellt das Modell ebenfalls
bereit. Die erzielten Ergebnisse erlauben vorauszusagen, ob bei einem
Wandel des thermischen Regimes in Flachseen (oder deren Teilen) potenziell
gefährliche, anaerobe Zonen auftreten können.
© IGB 2007
65
3.2.3.1
Introduction
The water quality in freshwater reservoirs in many respects is determined by
the content of dissolved oxygen (DO). In lakes with high DO concentration,
the bacterial destruction of organic matter is accompanied by extraction of
carbon dioxide, which is harmless for hydrocoles, into water. A decrease of
the DO concentration or its complete absence leads to the activation of
anaerobic processes, which usually occur with evolving such deoxidized
gases as methane (CH4), hydrogen sulphide (H2S), and ammonia (NH3).
Those are capable to not only worsen the water quality, but also to be toxic
(especially it concerns H2S). The onset and continuous existence of the
anaerobic zone in lakes leads to such negative consequences as fish kill, loss
of benthic organisms, changes in the trophic chains of water ecosystems, etc.
A DO deficit in shallow lakes occurs in absence of water aeration. The
formation of anaerobic zones in lakes may take place during the open-water
period and in winter. The duration of such phenomenon in the former case
is rather short as occasional wind mixing of water column from top to
bottom provides aeration of the bottom layers. The most dramatic situation
may occur in ice-covered lakes located in moderate and high latitudes
because the factors defining a DO regime in a shallow ice-covered lake
essentially differ from those during the open-water period. First, it is related
to main sources of oxygen flow. In winter, the ice cover excludes a gas
exchange with atmosphere. Besides, amount of solar radiation penetrating
into water becomes negligible that leads to a drastic decrease of
photosynthetic intensity. Thus, main sources of oxygen supply practically
disappear, and only consumption of oxygen by bacterial plankton in the
process of organic matter decomposition together with its absorption by
bottom sediments control the DO content in a lake (Hargrave 1972).
The rate of DO consumption in ice-covered lakes as a rule depends on a
set of biological and hydrophysical factors. Usually, the biochemical factors,
such as vital functions of the different organisms (including bacterial
plankton) within the benthic community, the concentration of the organic
matter and DO in the near-bottom layers, are considered as the main
parameters responsible for the formation of the oxygen depletion in icecovered lakes (Hutchinson 1957; Hargrave 1972; Mathias and Barica 1980;
Cornett and Rigler 1987). On the other hand, it is well known that the life
activity of the bacterial plankton, which is the main consumer of DO, is
strongly dependent on the water temperature (Boylen and Brock 1973;
Welch et al. 1976; Charlton 1980; Kovaleva et al. 2003). In spite of this fact,
it is commonly assumed that as long as the temperature in ice-covered lakes
is low and varies in a very narrow range (from 0 to 4-5°C), its effect on the
bacterial activity is not great and DO winter depletion depends only on the
concentration of organic matter in water column.
Nevertheless, in the frames of the present study the efforts to evaluate
the role of the temperature in the development of DO winter depletion in
ice-covered lakes were undertaken. As it will be shown below, in some cases
66
the so-called “effect of under-ice warming” can lead to considerable
strengthening in the development of anoxic conditions in ice-covered lakes.
3.2.3.2
Field data collected in three Russian, one American, and one Canadian
freezing lake were taken as the empirical material to perform the study.
Russian and American lakes are natural water-bodies of different trophic
state. Russian lakes Chainoe, Krasnoe, and Vendyurskoe are classified as
mesotrophic. American Lake Alequash belongs to the eutrophic type
whereas Canadian Lake Midnapore is an artificial urban water body of
mesotrophic type located in Calgary (for details see Golosov et al. 2007).
The phenomenon of winter DO depletion is intrinsic to Lake Allequash in
the same way as for the Russian lakes (often to the point of full DO
disappearance). In Lake Midnapore appearance of DO depletion is irregular
and there were detected no cases of full DO consumption (Meding 2000).
All data from Russian, American and Canadian lakes represents the DO
and water temperature vertical distributions from top to bottom of the water
column, measured in different dates from the beginning to the end of icecovered periods. Except Lake Midnapore, the thermal regime of the lakes in
consideration is similar, including the under-ice warming of the water
column due to heat flux from the sediments. The near bottom temperature
varies from 0.5-1.0°C in the beginning of the ice-covered period to 4-5°C in
the end.
The data from Russian lakes and Lake Alequash were used to derive
parameterizations of the model. These data were analyzed and processed in
terms of the time dependent relations between the values of the DO deficit
and temperature. Obtained functional relations were used to estimate the
rates of the total DO consumption in lakes in dependence on the water
temperature. The model verification was performed against the most detailed
data from Lake Vendyurskoe and data from Lake Midnapore as the
independent lake. Finally, the derived results were used in numerical
experiments on studying the formation and development of the anoxic
conditions in Lake Vendyurskoe.
3.2.3.3
Empirical verification of the model parameterisations
The model considers the DO vertical distribution within a ‘water-sediment’
system for the three most common cases (see Fig.1 a, b, c), that are: 1) the
anoxic zone in a bottom water layer is absent and oxidizing conditions in the
upper layer of bottom sediments prevail; 2) the DO concentration in the
bottom layer is close to zero, the oxidized layer in bottom sediments is
absent; and 3) the DO in the near-bottom layer is absent, and the anoxic
zone starts to develop from bottom towards top of the water column.
It is evidently from the field data, that the temporal variability of DO
concentration in the vicinity of ice is lower than that in bottom layers for one
order of magnitude at least. Therefore, in the frames of the model the DO
© IGB 2007
67
Fig. 1 Evolution of the DO vertical profile in an ice-covered lake during the winter (see text
for further explanation).
concentration at water-ice boundary can be assumed as constant during the
ice period. A detailed model description of the formation and development
of DO depletion in shallow ice-covered lakes, which uses in analogy to
thermal regime modeling (Mironov et al. 1991; Kirillin 2003; Golosov et al.
2003) the socalled self-similarity approach can be found in Golosov et al.
(2005). In the framework of this approach, invariability of the shapes of the
vertical DO profiles in a water column and the upper layer of sediments is
assumed.
68
The Results of verification of the model are mentioned here only briefly.
A detailed presentation was given in (Golosov et al. 2007). Measured and
calculated vertical DO profiles of Lake Vendyurskoe corresponding to
different dates of the winter 2001-02 were compared for the water column
(Fig. 2a. in Golosov et al. 2007) and for the upper oxidized layer of the
sediments (Fig. 2b in Golosov et al. 2007). Because the authors do not
possess own observational data on the vertical distribution of DO in
sediments (which can be received only with use of special micro-profilers)
data of natural and laboratory studies performed by other investigators
(Archer and Devol 1992; Jorgensson and Revsbech 1985; Lorke et al. 2003)
were used in the sediment comparison. Results of calculations show that the
model describes the temporal variability of the vertical DO profiles, from the
ice cover formation to the end of its existence, fairly well. This means that
the representation of the water DO profile assumed in the model, is quite
realistic.
3.2.3.4
Results of the model runs and Discussion
The verification of the model was performed against the field data collected
in two lakes, namely Lake Vendyurskoe (Russia) and Lake Midnapore
(Canada). Lake Midnapore was chosen for the model verification as
independent object since data from this lake were not used in deriving the
model parameterizations. Among aforementioned field data from different
lakes the most detailed data were obtained in Lake Vendyurskoe in 2001-02.
That was the main reason to choose Lake Vendyurskoe for studying the
peculiarities of the winter DO depletion.
As the first step of the model verification, the temporal dynamics of DO
concentration in Lake Vendyurskoe was calculated. To reveal the
peculiarities of the phenomenon under study, two locations with different
depths were chosen, namely St. 9 and St. 16 of 11.5 m and 5 m depth,
respectively. The differences between the stations consist not only in the
depths and places of location, but mainly in the thermal regime during the
ice-covered period Thus, the near-bottom temperature at St. 16 varies from
0.9°C in the middle of November (beginning of ice formation) to 2.5°C in
the middle of April. The corresponding variability of temperature at St. 9
covers the range from 1.2°C to 4.6°C.
The effect of the temperature on the formation of DO depletion was
studied under different conditions. Firstly, we calculated the DO deficit and
the thickness of the anoxic zone using the real temperature conditions
observed during the surveys. Results of these runs are presented in Fig. 2 a,
b, c.
The distance between both stations does not exceed one kilometer, but
the oxygen conditions differ strikingly. The storage of DO in bottom layers
at the deeper station became negligible no longer than in a half of month
after the ice formation (see Fig. 2a,b), whereas at St. 16 the more or less
essential deficit of DO appeared just in the middle of April (see Fig. 2c). At
St. 9, the completely anoxic zone started developing after full DO
consumption and reached the thickness of 1.5 m in the end of the winter.
© IGB 2007
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Fig. 2: Evolution of the DO concentration and of the anoxic zone thickness H in Lake
Vendyurskoe (a, b, c) and in Lake Midnapore (d). Diamonds and squares are the DO
concentrations measured under the ice cover and in the near-bottom water correspondingly.
Triangles mark the measured thickness of the anoxic zone. Dashed and solid lines
correspond to the model DO concentrations under the ice and in the near-bottom water.
70
At the St. 16, the anoxic zone did not appear at all. The values of the rate
of DO consumption for the under ice and near bottom zones were the same
for the both stations. Thus, the model runs differ from each other only by
the courses of temperature. In other words, the difference in peculiarities of
thermal regime between two stations can be responsible for the features of
formation of DO depletion within lake. In addition to the good agreement
between measured and calculated near bottom DO concentration (Fig. 2a, c),
it should be noted that the variability of DO concentration in the vicinity of
ice actually is very small, e.g. the corresponding assumption accepted at the
model formulation is correct.
The next set of the model runs was intended to reproduce the winter
course of DO concentration in Canadian Lake Midnapore. Before discussion
of the results of simulations, it is essential to note, that the thermal regime of
the lake considerably differs from that of the other lakes. The effect of
under-ice warming is not pronounced in this lake. The near bottom
temperature is almost constant during the whole winter and remains close to
the value of temperature of water maximal density, e.g. 4C. It means that
the limiting effect of the low water temperature on the rate of formation of
DO depletion in this case should be less than that in the case of Lake
Vendyurskoe.
Results of the model application to Lake Midnapore presented in Fig. 2d
confirm that statement. A decrease of the DO concentration in the nearbottom area takes place at essentially higher rate than that at St. 16 in Lake
Vendyurskoe though both sites are of the same depth. As a result, the DO
concentration in Lake Midnapore reaches its minimal values in 90 days after
the ice-covered period started, whereas in Lake Vendyurskoe the same values
of DO concentration were observed in 150 days (Fig. 2c).
The following runs of the model were intended to reveal the effect of the
shift of thermal regime on the formation of DO depletion. The under-ice
DO regime for St. 9 was calculated using the temperature measured at the
“cold” St. 16, and vice versa, the “warm” winter conditions for St. 16 were
simulated with temperature data obtained at the St. 9. Results of simulations
are presented in Fig. 3.
The model experiments show a rather strong dependence between the
DO and thermal regimes of lakes (or their single areas). Under conditions of
“cold” winter, the full consumption of DO at deep St. 9 has been developed
in two months after the ice period began. Respectively, the anoxic zone
started to develop later comparing to the “warm” case and reached
essentially lower thickness in the end of winter. These results were quite
expected. A more dramatic situation was revealed by simulations for shallow
St. 16. The shift in temperature entailed serious worsening in the DO regime.
The fully anoxic zone is observed already in 40 days after the ice formation.
The rate of its development reached 0.5 cm d-1. It is not as high as at St. 9,
but notice that in the case of “cold” winter there was no anoxic zone at this
station at all.
© IGB 2007
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Fig. 3: Results of numerical experiments: a, b – evolution of the near bottom DO
concentration and the thickness of the anaerobic zone at St. 9 in case of “cold” winter; c, d –
the same at the St. 16 in case of “warm” winter.
The results of numerical experiments performed in the present study
allow formulating some conclusions on the nature and the reasons of the
winter DO depletion in shallow ice-covered lakes. In lakes, where the
concentration of the organic matter is not a limiting factor (the cases of
mesotrophic and eutrophic lakes), the winter deficit can be formed due to
peculiarities of the lake winter thermal regime. In turn, the latter is affected
by warming/cooling conditions during the previous summer/autumn and by
the heat interaction between a water column and sediments. So, it means that
72
the winter DO depletion in many respects depends not only on the
biochemical processes in lakes and duration of the ice-covered period, but
can be determined by the physical factors acting long before the ice
formation in a lake. Actually, as soon as the thermal regime of ice-covered
lake plays an important role in formation of DO winter depletion, all factors
affecting the heat storage of sediments, can straightly or indirectly influence
on the rate of formation and duration of anoxic conditions in a lake. First of
all, it concerns to the summer mixing conditions and duration of “autumnwinter” cooling of a lake. The heat accumulation by sediments under neutral
or weak density stratification is much more efficient compared to the
conditions of stably stratified water column. In summer, frequent turbulent
mixing of the water column from top to bottom provides the effective heat
penetration from warm upper layers down to the near-bottom zone. As a
result, sediments accumulate a considerable amount of heat. And vice versa,
the existence of the stable density stratification in a water column prevents
the downward heat penetration. The heat exchange between near-bottom
water and sediments is depressed in this case, and the heat content of
sediments is small. The duration of the “autumn-winter” cooling, following
after summer warming, also influences on the sediments heat content in the
beginning of ice-covered period. In a case of fleeting and very intensive
water column cooling in autumn, sediments retain considerable heat content
to the time of ice formation. That leads to the rapid under-ice water warming
after the freeze-up and, as a consequence, to the rapid formation of DO
depletion. On the contrary, in a case of long “autumn-winter” cooling,
sediments get cold enough and its heat content is too small to provide a
reasonable increase of water temperature during the winter. In this case the
sediments are not able to increase the near-bottom temperature considerably,
and the low water temperature can prevent the fast development of the DO
depletion.
Some logical deduction can be done concerning the effect of the
expected global warming on the DO regime of ice-covered lakes. Taking into
account the aforementioned results of the model runs, the warming may play
an essentially negative role in the deterioration of the DO regime in freezing
lakes. The expected increase in winter near-bottom temperature can lead to a
more frequent formation of the anoxic zones in lakes. Moreover, one can
expect that the time and spatial scales of those events would increase
considerably.
Acknowledgement
The present study is supported by European Commission (project INTAS 01-2132), the Swedish Institute (VISBY Programme), Ǻke och Greta Lisshed
Foundation, Sweden, the Russian Academy of Sciences, and the German
Foundation of the Basic Research (DFG, Project KI-853/3-1 in frames of
the program „AQUASHIFT“). The support is gratefully acknowledged.
Authors express their admiration and gratitude to the field research team of
the Northern Water Problems Institute for their heroic efforts at collecting
field data during winter field campaigns.
© IGB 2007
73
References
ARCHER D, DEVOL A. 1992. Benthic oxygen fluxes on the Washington shelf and
slope: A comparison of in situ microelectrode and chamber flux measurements.
Limnol. Oceanogr. 37: 614-629.
BOYLEN C, BROCK, T. 1973. Bacterial decomposition processes in Lake Wingra
sediments during winter. Limnol. Oceanog. 18(4): 628-634.
CHARLTON M. 1980. Hypolimnion oxygen consumption in lakes: discussion of
productivity and morphometry effects. Can. J. Fish. Aquat. Sci. 37: 1531-1539.
CORNETT R , RIGLER F. 1987. Vertical transport of oxygen into the hypolimnion of
lakes. Can. J. Fish. Aquat. Sci. 44: 852-858.
GOLOSOV S, ZVEREV I, TERZHEVIK A. 2003. Thermal Structure and Heat Exchange
in Ice-Water Column-Sediment System. In: TERZHEVIK, A.(ED) Proc. 7th Int.
Symp. Physical Processes in Natural Waters, July 2003, Petrozavodsk, Russia: 17 28
GOLOSOV S, SHIPUNOVA E, MAHER OA, TERZHEVIK A, ZDOROVENNOVA G. 2005.
Physical background of oxygen depletion development in ice-covered lakes. In:
FOLKARD A, JONES I (EDS). Proc 9th Europ Workshop on Physical Processes in
Natural Waters, September 2005, Lancaster University, UK, 229–237.
GOLOSOV S, MAHER OA., SCHIPUNOVA E, TERZHEVIK A., ZDOROVENNOVA G,
KIRILLIN G.2007. Physical background of the development of oxygen depletion
in ice-covered lakes. Oecologia, 151: 331-340
HARGRAVE B. 1972. A comparison of sediment oxygen uptake, hypolimnetic oxygen
deficit and primary production in Lake Esrom, DK. Verh. Int. Ver. Limnol. 18:
134-139.
HUTCHINSON G. 1957. A treatise on limnology. Vol I. J.Wiley & Son, NY, 1015 p.
JORGENSEN B, REVSBECH N. 1985. Diffusive boundary layers and the oxygen uptake
of sediments and detritus. Limnol. Oceanogr. 30: 111-122.
KIRILLIN G. 2003. Modeling of the Shallow Lake Response to Climate Variability In:
TERZHEVIK, A (ED). Proc. 7th Int. Symp. Physical Processes in Natural Waters,
July 2003, Petrozavodsk, Russia: 144-148.
KOVALEVA N, MEDIENTZ V, GAZETOV E. 2003. Influence of temperature and
oxygen content on the intensity of the organic matter decay in Black Sea.
Gidrobiologicheskiy Zhurnal (J. of Hydrobiology) 39(4): 34-40. (in Russian)
LORKE A, MULLER B, MAERKI M, WUEST A. 2003. Breathing sediments: The control
of diffusive transport across the sediment-water interface by periodic boundarylayer turbulence. Limnol. Oceanogr. 48(6): 2077-2085.
MATHIAS J, BARICA J. 1980. Factors controlling oxygen depletion in ice-covered lakes.
Can. J. Fish. Aquat. Sci. 37: 185-194.
MEDING M. 2000. Structure and function in shallow prairie lakes: macrophytes and
winter anoxia. Master thesis, University of Calgary: 124 p
MIRONOV D, GOLOSOV S, ZILITINKEVICH S, KREIMAN K, TERZHEVIK A. 1991.
Seasonal changes of temperature and mixing conditions in a lake. In:
ZILITINKEVICH S (ED). Modelling Air-Lake Interaction. Physical Background.
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WELCH H, DILLON P, SREEDHARAN A. 1976. Factors affecting winter respiration in
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74
Adaptation, plasticity and dynamics of
communities
Adaptation, Plastizität und Dynamik von Biozönosen
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G LOESS , S., H UPFER , M., R ATERING , S., G ROSSART , H.-P.
3.3.1 Detection and phylogenetic characterization of
polyphosphate accumulating bacteria in lake
sediments
Nachweis und phylogenetische Charakterisierung von Polyphosphatakkumulierenden Bakterien in Seesedimenten
Key words: polyphosphate, sediment, bacteria, polyphosphate accumulating
bacteria (PAO), single cell separation, laser microdissection, DGGE
Abstract
The direct contribution of microorganisms to the mobilization and
immobilization of phosphorus (P) in aquatic sediments has been
controversially discussed since more than one decade. Polyphosphate (PolyP) storage is an universal ability of many microorganisms and has been
technically optimized in wastewater treatment plants (WWTP) by providing
conditions for an enhanced biological phosphorus removal (EBPR). Poly-P
accumulating organisms (PAO) in sediments, thus, might be of high
ecological importance. PAO in sediments are able to insert P into the
benthic food chain and affect the permanent P mineral deposition by
physiologically inducing rapid P release. Although several studies indicate
that Poly-P substantially contributes to total P in the uppermost sediment
layer, its origin as well as the microorganisms and mechanisms involved in
Poly-P storage and cycling are unknown. Therefore, we have screened
sediments from eight lakes different in trophy and limnological features for
the presence of PAO. We have used denaturing gradient gel electrophoresis
(DGGE) with a set of primers specific for bacteria closely related to the
genus Rhodocyclus, belonging to the most popular PAOs in WWTP with
EBPR. Our screening shows that members of the genus Rhodocyclus are
present in all studied sediments. However, subsequent quantification of these
PAO by fluorescence in situ hybridization (CARD-FISH) with oligonucleotide probes specific for the Rhodocyclus-PAO revealed that they only
contribute to <1% of total DAPI counts. Therefore, we have established a
single cell approach for the detection and phylogenetic characterization of
hitherto unknown PAO in freshwater sediments. Sediment bacteria of Lake
Stechlin where highest amounts of Poly-P have been quantified by 31P
Nuclear Magnetic Resonance Spectroscopy were stained with DAPI for
localization of PAO. Poly-P positive cells were subsequently collected by
laser microdissection and could be analyzed with molecular methods for
their phylogenetic characterization. Our preliminary results show that the
presented method can be successfully used to collect and identify single
bacteria with a specific physiological attribute, such as Poly-P storage.
Zusammenfassung
Seit mehr als einem Jahrzehnt wird in der Literatur sehr kontrovers
diskutiert, in welchem Maße Mikroorganismen direkt an der Freisetzung und
© IGB 2007
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Festlegung von Phosphor (P) in Sedimenten beteiligt sind. Polyphosphat
(Poly-P) Speicherung ist eine universelle Eigenschaft von vielen
Mikroorganismen und wurde in Kläranlagen (wastewater treatment plants,
WWTP) durch das Einstellen von Bedingungen, die eine erhöhte biologische
P Entfernung (enhanced biological phosphorus removal, EBPR)
ermöglichen, technisch optimiert. Poly-P akkumulierende Organismen
(PAO) in Sedimenten sind daher von besonderer ökologischer Wichtigkeit.
PAO in Sedimenten können P in die benthische Nahrungskette
einschleussen und beeinflussen die mineralische P Deposition durch ein
schnelles, physiologisch induziertes Freisetzen von P. Obwohl
verschiedenste Studien zeigen, dass Poly-P substantiell zum gesamten P Pool
in der obersten Sedimentschicht beiträgt, sind sowohl der Ursprung als auch
die an der Speicherung und am Umsatz von Poly-P beteiligten
Mikroorganismen und Mechanismen weitestgehend unbekannt. Daher haben
wir Sedimente von acht verschiedenen Seen unterschiedlicher Trophie und
limnologischer Eigenschaften auf die Anwesenheit von PAO mittels
denaturierender Gradienten-Gelelectrophore (DGGE) und Rhodocyclusspezifischen Primern überprüft. Die Gattung Rhodocyclus stellt eine der
häufigsten PAO in WWTP mit EBPR dar. Unsere Ergebnisse zeigen, dass
Vertreter der Gattung Rhodocyclus in allen untersuchten Sedimenten anwesend
sind. Allerdings zeigte die anschliessende Quantifizierung dieser PAO mit
Rhodocyclus-spezifischer Fluoreszenz in situ Hybridisierung (CARD-FISH),
dass ihr Anteil bei <1% der gesamten Bakterienzahl liegt. Daher haben wir
einen Einzelzellansatz für die Detektion und phylogenetische
Charakterisierung von bisher unbekannten PAO in limnischen Sedimenten
entwickelt. PAO aus dem Sediment des Stechlinsees, in dem die höchsten
Poly-P Konzentrationen mittels 31P Nuclear Magnetic Resonance
Spectroscopy (NMR) bestimmt wurden, wurden zur Lokalisierung mit DAPI
gefärbt. Poly-P positive Zellen wurden anschliessend mit der LaserMikrodissektion gesammelt, um sie mit molekular-biologischen Methoden
phylogenetisch zu charakterisieren. Unsere vorläufigen Ergebnisse zeigen,
dass die vorgestellte Methode erfolgreich eingesetzt werden kann, um
einzelne Bakterienzellen mit bestimmten physiologischen Eigenschaften, z.B.
der Poly-P Speicherung, zu sammeln und phylogenetisch zu charakterisieren.
3.3.1.1
Introduction
Many studies show that microbial activity in surface sediments affects the
release of P from sediments into the water by various mechanisms (e.g.
Boström et al. 1988, Gächter & Müller 2003); i.a. hydrolysis of dissolved
Poly-P is fast in pore water of sediments (Hupfer et al. 1995). Several
microorganisms in aquatic ecosystems are able to excessively and rapidly take
up P beyond their physiological need ("luxury uptake"). Synthesis and
storage of Poly-P are common among microorganisms (especially for
cyanobacteria, McDignum et al. 2005) when P is sufficiently available after
phases of acute P starvation (“overplus uptake”). The increased stress due to
limited P availability implies the synthesis of a high-affinity uptake system for
78
orthophosphate and additional enzymes which transform orthophosphate
into insoluble Poly-P inside the cell. These adaptations are valuable
advantages for competition with other organisms such as phytoplankton
when inorganic nutrients become limiting (e.g. Eixler et al. 2006).
Furthermore, laboratory experiments have demonstrated that Poly-P storage
in microalgae and cyanobacteria is influenced by various other environmental
conditions, e.g. light (Sianoudis et al. 1986), sulphur (Lawerence et al. 1998),
and nitrogen availability (Küsel et al. 1989). While it is well accepted that
microorganisms living in activated sludge are able to store high amounts of P
inside the cell in form of Poly-P (e.g. up to 10 % of total dry mass in a pure
culture of Acinetobacter 210A, Deinema et al. 1985), the presence and
influence of such heterotrophic bacteria in lake sediments for P turnover is
still unclear.
Phosphorus in the biomass of sediment microorganisms as a regulator
for the dynamics of benthic P fluxes has been controversially discussed
throughout the last two decades. Experimental data (Gächter et al. 1988,
Waara et al. 1993), theoretical considerations (Davelaar 1993, Gächter &
Meyer 1993), and detection of Poly-P in limnetic sediments (Hupfer et al.
2004, Reitzel et al. 2006) give strong indications that sediment
microorganisms are indeed directly involved in P fixation. Other authors,
however, doubt or ignore the relevance of microbial biomass as an important
link for P cycling in sediments (Golterman 2004).
Most of our present knowledge on Poly-P accumulating bacteria is based
on studies in activated sludge showing an enhanced biological P removal.
For optimization of sewage treatment processes a fundamental
understanding of the bacterial sludge communities and their dynamics is
necessary. Several types of bacteria isolated from activated sludge are able to
take up P excessively and accumulate it intracellular in form of Poly-P, e.g.
species of the genus Acinetobacter (Fuhs and Chen 1975), Microlunatus
phosphovorus (Nakamura et al. 1995), members of the genus Tetrasphaera
(Maszenan et al. 2000) or Lampropedia spp. (Stante et al. 1997). Culture
independent methods (e.g. DGGE, clone libraries, and FISH with specific
oligonucleotide probes) showed that members of the Betaproteobacteria closely
related to the genus Rhodocyclus (e.g. Bond et al. 1995, Hesselmann et al. 1999,
Kong et al. 2004), Alphaproteobacteria (e.g. Kawaharasaki et al. 1999) and
Tetrasphaera related Actinobacteria (e.g. Bond et al. 1999, Kong et al. 2005)
could be detected in large numbers in activated sludge. Using these
techniques, it has been also shown that members of the genus Acinetobacter
contribute to a minor fraction of the sludge community (e.g. Wagner et al.
1994). All bacterial classes potentially involved in Poly-P storage were
detected in lake sediments as well (Uhlmann et al. 1998, Wobus et al. 2003).
This notion is not surprising, since some lake sediments could be considered
as “natural activated sludge” (Höll 1930). Hence, it can be assumed that
PAO are also responsible for the presence of Poly-P in lake sediments
(Davelaar 1993).
Until now the origin as well as the microorganisms and mechanisms
involved in Poly-P storage and cycling in lake sediments are hardly known.
© IGB 2007
79
Therefore, we have screened sediments from eight lakes different in trophy
and limnological features for the presence of PAO by using denaturing
gradient gel electrophoresis (DGGE) with a set of primers specific for
Candidatus “Accumulibacter phosphatis” a member of the family Rhodocyclaceae
and one of the most popular PAO (Crocetti et al. 2000; Kong et al. 2004).
Although these PAO were present in all studied lakes, their quantification by
CARD-FISH revealed that they contributed <1% to the total bacterial
number. Therefore, we aimed to establish a method by which single cells of
PAO from lake sediments can be identified and at the same time separated
for subsequent precise phylogenetic identification. Our previous results show
that single cells with a specific physiological attribute, such as Poly-P storage,
can be collected by laser microdissection for subsequent analysis with
molecular methods for precise phylogenetic characterization.
3.3.1.2
Sampling and sample preparation
For screening of the presence of already known PAO sediments from the
following lakes have been taken: Lake Stechlin (between June 2004 and May
2006), Lake Scharmützel (between June 2004 and April 2005), Lake Arend
(June 2004, October 2004, May 2005), Lake Grosse Fuchskuhle (South-East
and North-West Bassin), Lake Groß Glienicke, Lake Auen, Lake Petersdorf,
and Lake Müggel (each in June 2004). For identification and separation of
single PAO by laser microdissection sediment samples were taken from Lake
Stechlin in June 2006 at the deepest point of the lake (69.5 m). Lake Stechlin
is oligotrophic and characterized by an all-seasonal high hypolimnetic oxygen
concentration near the bottom (> 60% O2 saturation). Sediment cores were
collected using a sediment sampler (Uwitech, Mondsee, Austria). The
uppermost biofilm-like sediment (up to 5 mm) was immediately siphoned
using a 50 ml plastic syringe equipped with a flexible tube. To obtain a
representative composite sample four to seven replicate cores per site were
pooled. The samples were brought into the lab in a dark cool box and
immediately processed for further analyses. For the detection of potential
Poly-P storing bacteria cells were extracted from the sediment with sodiumpyrophosphate (0.1 %, w/v), gentle sonicated and shaked over head for 30
min. After an additional 30 min sedimentation step the supernatant was
removed, sonicated again and the extracts were fixed 1:1 with ethanol (99 %,
v/v). For DAPI (4`, 6- Diaminido-2-phenylindole dehydrochloride)-staining
the fixed extracts were filtered onto 0.2 µm polycarbonate membranes
(Nucleopore®, Whatman, Germany) and incubated with DAPI (20 µg ml-1)
for 15 min. When used at high concentrations DAPI stains Poly-P granula
with an intensive yellow fluorescence (Streichan et al. 1990). The laser
microdissection was performed during the next 48 hours after DAPI
staining. For counting the DAPI positive cells a Leica DR-MB
epifluorescence microscope with 1000x magnification was used.
80
Polyphosphate measurements
The extraction of Poly-P from sediments was done according to a standard
protocol by pre-extraction with edatic acid (EDTA) followed by an alkaline
extraction procedure (NaOH-EDTA) (Hupfer et al. 1995, 2004). 31P-NMR
analyses were carried out on a Bruker 102 DRX 600 spectrometer. The
identification and quantification of peaks are described in Hupfer et al.
(1995).
DNA extraction
About 500 mg sediment was charged with sodium phosphate buffer (120
mM), SDS (25%) and zirconia beads and vortexed in a horizontal vortexer
followed by the enzymatic cell lysis with proteinase K and lysozyme. Proteins
were precipitated using ammoniumacetate (7.5 M). After removing the
proteins through a centrifugation step, the DNA was precipitated using
ispropanol. The pellet was washed twice with 70 % (v/v) ethanol. The DNA
was loaded onto an agarose gel (1.5 %) to check their quality.
PCR and DGGE
For DGGE genomic DNA was amplified using the following PCR reaction
mixture: 2 µl DNA, bovine serum albumin (final conc. 0.125 µg), 250 nM of
each primer (MWG biotech AG, Ebersberg), 200 µM of each dNTP, 2 mM
MgCl2, 10 µl 10x PCR buffer, 0.5 u RedTaq DNA Polymerase (Bioline
GmbH, Luckenwalde). The final volume of 50 µl was adjusted with ultrapure
water. For PCR amplification a Gradient Cycler PT200 (MJ Research) was
used with an initial denaturation step at 95°C for 3 min, followed by 30
cycles of denaturation at 95°C for 1 min , annealing at 60°C for 1 min, and
extension at 72°C for 3 min. A final extension step was carried out at 72°C
and 15 min, cooling at 4°C completed the reaction. The following primer set
has been used: 341f-gc (5’ – CGC CCG CCG CGC CCC GCG CCC GTC
CCG CCG CCC CCG CCC GCC TAC GGG AGG CAG CAG – 3’,
Muyzer et al. 1993) and PAO846 (5'- GTT AGC TAC GGC ACT AAA
AGG -3', Crocetti et al. 2000).
DGGE was performed using the INGENYphorU System (Ingeny
International, Netherlands). PCR products were loaded onto a
polyacrylamide gel in 1xTAE buffer (20 mM Tris, 10 mM acetate, 0.5 mM
EDTA, pH 7.6). The gel consisted of a formamide/urea gradient ranging
from 40 to 70%. Gel electrophoresis was performed for 20 hours and 100 V
at 60°C. Staining of the gel was carried out with 1x SYBR Gold (Molecular
Probes, Invitrogen, Germany) for 35 min followed by a 10 min destaining
step with demineralized water. The stained gel was immediately
photographed on a UV transillumination (BioRad, Germany).
CARD-FISH
Fluorescence in situ hybridization with horseradish peroxidase (HRP)labelled probes and tyramide signal amplification was modified performed
according to the protocol of Pernthaler et al. (2002). In brief, ethanol-fixed
sediment extracts were brought onto coated slides, embedded, and
permeabilized. Whole-cell in situ hybridizations on the slides were done with
© IGB 2007
81
5`-HRP-labelled oligonucleotide probes EUB338 I to III (Bacteria including
Verrumicrobia and Planctomycetes, Daims et al. 1999), PAO462+PAO846
(Crocetti et al. 2000) and with a formamide concentration of 55% in the
hybridization buffer. The oligonucleotide probes were purchased from
ThermoHybaid (Ulm, Germany). The slides were inspected with a Leica DRMB epifluorescence microscope at 1000x magnification.
Non Contact Laser Microdissection
Laser microdissection and pressure catapulting (LMPC) were performed with
the PALM MicroBeam system in combination with the PALM RoboMover
controlled by the PALM RoboSoftware v2.2 (P.A.L.M. Microlaser
Technologies GmbH, Bernried, Germany). The MicroBeam system
consisted of an Axiovert 200 M microscope (Carl Zeiss MicroImaging
GmbH, Germany) equipped with a 100 W mercury lamp. The Nuclepore
filters were inspected with the fluorescence filter FS18 (P.A.L.M. Microlaser
Technologies GmbH, Bernried, Germany) at 400x magnification. Bacterial
cells with bright yellow illuminating inclusions were laser dissected out of the
filter. The excised cells were catapulted into the lid of an AdhesiveCap
(P.A.L.M. Microlaser Technologies GmbH, Bernried, Germany).
DNA Extraction and PCR of excised cells
Lysis of the cells was done “upside down” in the cap for 2 minutes in liquid
nitrogen and subsequently 2 minutes at 96°C, each three times. The cells
were vortexed and centrifuged to the bottom of the cap. The 16S rRNA
genes were targeted for amplification by direct PCR using a DNase I
digested mastermix containing the universal bacterial primer pair 341f (5’ –
CCT ACG GGA GGC AGC AG – 3’) and 907r (5’ – CCG TCA ATT CMT
TTG AGT TT – 3’) (Muyzer et al. 1993) (each 250 nM), bovine serum
albumin (final conc. 0.5 µg; Roth, Karlsruhe, Germany), 200 µM of each
dNTP (Bioline GmbH, Luckenwalde, Germany), 2 mM MgCl2, 10x PCR
buffer, 0.2 U HotStarTaq DNA Polymerase (Qiagen, Hilden, Germany) in.a
final volume of 22 µl. For PCR amplification a Gradient Cycler PT200 (MJ
Research) was used with an initial denaturation step at 95°C for 2 min,
followed by 49 cycles of denaturation at 95°C for 1 min, annealing at 55°C
for 40 sec, and extension at 72°C for 1:30 min. A final extension step was
carried out at 72°C for 10 min; cooling at 4°C completed the reaction.
3.3.1.3
Results and discussion
Evidence for Poly-P
Poly-P was found in surficial sediment samples of oligotrophic Lake Stechlin
and accounted for ca. 20 % of total P (Figure 1). Such high values have never
been published before and, thus, provided a good basis for searching and
identifying Poly-P storing bacteria in lake sediments.
Detection of PAO in lake sediments
We have used the primer pair 341f-gc and PAO846 for DGGE analysis.
Originally primer PAO846 has been used as an oligonucleotide probe
82
specific for members of the Rhodocyclaceae (Crocetti et al. 2000). Rhodocyclus
related sequences were detected by DGGE in all samples (Figure 2)
indicating that this cluster is widely distributed in freshwater sediments.
Fig. 1: 31 P-NMR spectrum of the surficial lake sediment of Lake Stechlin (NaOH-extract),
17.06.2004, 68 m
Fig. 2: DGGE-analysis of samples from lakes Stechlin, Scharmützel, Arend, Grosse
Fuchskuhle (Northeast and Southwest basin), Gross Glienicker, Auen, Petersdorf, Müggel
and activated Sludge (Wassmannsdorf). St = lab internal DGGE standard.
The application of the CARD-FISH protocol with oligonucleotide
probes PAO462 and PAO846 revealed that the popular PAO members of
the Rhodocyclaceae (Figure 3) contributed to <1% of the total bacterial
community suggesting that they play a minor role for Poly-P storage in a
variety of freshwater sediments. This is in obvious contrast to results of
Crocetti et al. (2000) who found that in a laboratory-scale plant with
enhanced biological P removal a positive correlation between percent P in
the sludge and numbers of PAO probebinding cells occur. Since the
percentage of PAO462/PAO846 positive cells was low in all samples studied
we assume that in natural sediment samples (e.g. Lake Stechlin with high
© IGB 2007
83
concentrations of Poly-P) other bacteria must be important for Poly-P
storage. Therefore, we have developed a method to simultaneously identify
and separate single cells of PAO fur further molecular characterization.
Figure 3: Poly-P storing bacterium of the
genus Rhodocyclus detected by CARDFISH using probes PAO462 and 846 (as
indicated by the white arrow).
Separation of Poly-P accumulating bacteria by Laser Microdissection
Poly-P accumulating bacteria from lake sediments were identified by DAPI
staining of intracellular Poly-P granules. DAPI can serve as standard stain for
visualization of Poly-P since at high concentrations DAPI also stains Poly-P
granula with an intensive yellow fluorescence (Figure 4, Streichan et al.
1990). DAPI staining is not exclusively specific for Poly-P, however, DAPI
staining of other polymers results in a weak and fast fading yellow
fluorescence (Streichan et al. 1990). Therefore we are confident that in our
study cells with bright yellow fluorescence were PAO. From Lake Stechlin
sediment sample (June 2006), ca. 100 Poly-P containing cells were cut out
and catapulted into a sterile cap using the PALM MicroBeam technology
(P.A.L.M. Microlaser Technologies GmbH, Bernried, Germany).
10 µm
Lake Stechlin
Activated sludge
Fig. 4: Detection of Poly-P storing bacteria by DAPI staining
Previously the PALM laser technology has been successfully used in
analyzing eukaryotic material for a variety of scientific applications, e.g.
forensic, botany, pathology or neurosciences. Even, potentially pathogenic
bacteria from histological tissue have been detected with fluorescently
labelled oligonucleotide probes, microdissected with the PALM technology,
and identified by using specific primers (Klitgaard et al. 2005). In our study
we were able to successfully extract the DNA of the collected cells and use it
for further DNA analyses. We have applied an universal bacterial primer set
that resulted in an amplicon fragment length short enough for amplification
84
of the extracted DNA but still long enough for reliable phylogenetic
classification. Because of the yet low number of collected cells a statistical
coverage was not possible. Our preliminary results suggest that Poly-P
storage seems to be widespread among sediment bacteria.
In summary, DGGE analyses of various freshwater sediments
demonstrate that the occurrence of PAO of the Rhodocyclaceae family is an
universal feature in many lakes. However, when using CARD-FISH with
oligonucleotide probes specific for these PAO it becomes obvious that these
bacteria account for only a small fraction of the total bacteria and
presumably are insignificant for overall Poly-P storage. Therefore, we have
applied a method by which we can identify and separate individual PAO at
the same time. The PALM MicroBeam technology coupled with molecular
analyses proofed to be an excellent method for the phylogenetic
classification of hitherto unknown Poly-P accumulating bacteria from
environmental samples. The only precondition of this technique is to
visualize the cells of interest for their microscopic detection, e.g. with
histological or fluorescent dyes. Cell morphology can be another criterion,
too. Additional studies with numbers of collected cells sufficient for
statistical analysis are necessary to study the presence and phylogenetic
affiliation of PAO in various freshwater systems and to elucidate their
ecological role in these systems.
Acknowledgement
We thank Peter Schmieder for his support with the NMR investigations
carried out at the Research Institute of Molecular Pharmacology, Berlin,
Germany. Christiane Herzog is acknowledged for her assistance with
chemical-analyses and Monika Degebrodt for running the sequencer.
Gabriele Friedemann is thanked for introducing SG into the PALM
MicroBeam technology.
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88
H ELLAND , I.P., B RAUNS M., F REYHOF , J.
3.3.2 Depth distribution of abundant benthic
invertebrates in Lake Stechlin
Tiefenverteilung von häufigen benthischen Wirbellosen im Stechlinsee
Key words: ecological gradient, oligotrophic lake, chironomidae, oligochaeta
Abstract
Benthic macroorganisms were collected every 5 m depth along an east-west
transect from 5 to 50 m, in the northern bay of Lake Stechlin in August
2006. From 18 taxonomic groups recorded, 10 groups were restricted to the
first 15 m water depth. Chironomids, oligochaets and Megacyclops copepods
are most abundant in all water depth. Species richness and the number of
macrobenthic organism declined with increasing water depth.
Zusammenfassung
Im August 2006 wurden Macrozoobenthos-Organismen alle 5 m entlang
eines ost-west Tiefengradienten von 5-50 m in der Nordbucht des
Stechlinsees untersucht. Von 18 nachgewiesenen Organismen-Gruppen
waren 10 auf die oberen 15 m Wassertiefe beschränkt. Chironomiden,
Oligochaeten und Megacyclops copepoden waren die häufigsten Organismen
in allen Tiefen. Die Arten-Diversität und die Abundanz der
Macrozoobenther nahmen mit zunehmender Tiefe ab.
3.3.2.1
Introduction
Benthic macroinvertebrates are of high importance in aquatic environments
as link between detrial deposits in the profundal zone and the higher trophic
levels. Many fish species are dependent on a benthic diet in shorter or longer
parts of their lives (Vander Zanden & Vadeboncoeur 2002), and zoobenthic
biomass has been looked upon as an index of the potential productivity of a
lake for fish (Rasmussen 1988). It has been suggested that the importance of
benthic energy pathways in lake food webs has been overlooked, and that
the focus on the pelagic area has been too strong (Vadeboncoeur et al. 2002).
Recently, there has been an increasing interest in analysis of how pelagic and
benthic habitats are interconnected (e.g. (Harrod & Grey 2006; Okun et al.
2005; Vander Zanden & Vadeboncoeur 2002)). In the littoral, the main food
source is attached algae and allochtonous detrial carbon of terrestrial origin,
and the benthic community usually is diverse and highly productive. In
contrast, the profundal zone may only offer sedimenting autochtonous
organic matter as food source (France 1995). Rasmussen & Kalff (1987)
found the production of profundal macroinvertebrates to correlate with the
trophic status of the lake, and that their biomass is regulated by the level of
chlorofyll a and phosphorus. Therefore, allochthonous material and nutrients
are more important in oligotrophic lakes than in more productive lakes
(Dermott 1988). In oligotrophic lakes surrounded by a dense forest
© IGB 2007
89
particularly leaf litter from the nearby vegetation is the important
allochtonous detrius material (Oertli 1993; Pieczynska 1993), which
influences the macroinvertebrate composition at first, and thereafter the
higher trophic levels in the lake.
Benthic macroinvertebrates may both be predators on smaller organisms
(e.g. cladocerans) and at the same time an important food source for fish,
and can therefore operate as key organisms in lacustrine ecosystems (Sagrario
& Balseiro 2003). The North German Lake Stechlin is largely dominated by
pelagic fishes of the genus Coregonus. While these feed mostly on planctonic
prey, Schulz et al. (2003) demonstrated that Lake Stechlin Corgeonus also take
a certain amount of benthic organisms. It could even be suggested, that
benthic organisms as an alternative to pelagic prey might have played a role
in the evolution of the endemic Lake Stechlin cisco Coregonus fontanae (Schulz
et al. 2006) and benthic food might be involved in the particular depth
distribution if this species (Helland et al. 2007). However, the benthic
macrofauna is poorly studied in Lake Stechlin. Therefore, it is the aim of this
study to describe the depth distribution of major benthic macroinvertebrates
to give a baseline to future studies on food availability for Lake Stechlin
fishes.
3.3.2.2
Lake Stechlin is a medium sized (4.25 km2), deep (max. depth 69 m)
oligotrophic lake in northern Germany (53°10’N 13°02’E). Invertebrate
sampling took place in August 2006 along an east-west transect in the
northern bay of the lake (Fig. 1). Within this transect, three replicated
invertebrate samples were taken at 20 sampling points from 5 to 50 m water
depth using an Ekman-Birge grab (HydroBios, Mondsee, Germany). Samples
were sieved in the field (500 µm mesh) and transported on ice to the
laboratory. Invertebrates were sorted live to major taxonomic groups at the
same day. Copepods were identified by A. Rychla (Neuglobsow). Individuals
were measured to the nearest mm using stereo-dissecting microscopes and
an object micrometer. The Shannon-Wiener-Index of Diversity was applied
to the full set of species data. The following four dominant groups of
benthic invertebrates, i.e. > 10 % frequency, were selected for detailed
analyses: annelids, white chironomids, red chironomids and copepods
(Megacyclops sp.).
90
Fig 1: Bathymetric map Lake Stechlin including marked sample transect.
3.3.2.3
Results
1040 individual animals from 18 taxonomic groups were caught (Table 1).
From these, 10 taxonomic groups were restricted to the first 15 m water
depth. There was a significant negative regression between the index of
diversity and water depth (Fig. 2). Table 2 shows the results of the regression
analysis between the abundance of benthic invertebrates and water depth. If
all macrobenthic organism are added together, there is a significant negative
regression between water depth and the abundance of benthic invertebrates
on the west side of the transect only. Within the four dominant taxonomic
groups, there were negative, significant regressions between water depth and
the number of white chironomids on both lake sides of the transect.
Oligochaets showed a significantly negative regression with water depth on
the western side and a significantly positive regression on the eastern side of
the tansect. The abundance of Megacyclops and red chironomids did not show
any clear depth gradient. Generally, species richness and the number of
macrobenthic organism declined with increasing water depth.
© IGB 2007
91
Tab 1: Benthic animals from three samples each water depth along a transect in Lake Stechlin.
Lakeside
east
Water depth (m)
5
10
15
11
2
5
72
Acari
Asellus
west
Bivalvia
20
3
Ceratopogonidae
25
35
40
45
50
1
4
29
19
12
30
Chironomidae White
4
30
10
1
3
2
1
Cladocera
1
Total
10
15
20
1
6
9
3
3
11
7
25
30
20
22
12
1
1
11
35
40
45
50
32
98
3
1
5
14
19
16
29
34
30
29
10
1
16
12
10
12
8
7
2
2
2
3
4
8
8
6
12
16
374
1
1
120
10
2
Gastropoda
4
3
Hirundinea
1
2
1
3
19
Megacyclops
5
1
2
Chironomidae Red
Ephemeroptera
30
4
Nematoda
7
11
22
2
7
1
8
3
2
2
6
8
26
13
1
4
2
2
2
1
Odonata
1
Oligochaeta
2
8
Ostracoda
1
6
1
4
9
8
2
13
14
7
1
21
1
Turbellaria
1
1
Total
24
174
64
21
43
22
45
5
26
33
7
1
13
6
2
4
7
1
Sialis
Trichoptera
103
30
20
2
3
13
1
5
7
193
22
8
1
3
3
2
1
4
5
42
96
112
95
66
1
3
2
42
43
28
18
11
23
39
1040
92
© IGB 2007
Tab 2: Regression of total number of individuals of the dominant taxonomic groups against water depth.
Lakeside
east & west
Significance (p) &
coefficient of regression (R)
p
east
R
west
p
R
p
R
-0.687
All species
0.002
-0.395
0.177
-0.253
<0.001
Oligochaeta
0.404
-0.110
0.033
0.390
0.010
-0.463
Megacyclops
0.072
-0.234
0.393
-0.162
0.117
-0.292
Red chironomids
0.207
-0.165
0.766
-0.058
0.148
-0.271
White chironomids
0.001
-0.501
0.031
-0.394
<0.001
-0.792
1.0
0.9
0.8
0.7
Index of 0.6
diversity 0.5
0.4
0.3
0.2
0.1
0.0
5
10
15
20
25
30
35
40
45
50
50
45
40
35
30
water depth (m)
Fig 2: Index of diversity calculated for benthic macroinvertebrates along a depth transect in Lake Stechlin.
25
20
15
10
5
93
3.3.2.4
Discussion
The far most dominant groups of macroinvertebrates found in Stechlinsee
were chironomids and oligocheata, a pattern which is frequently found in
lakes (e.g (Dinsmore et al. 1999; Lindegaard 1992; Oertli 1993). These were
the only organisms occurring at all sampled depths in our study. The
Megacyclops copepods, which were also abundant, were found from 10 to 50
metres, but were most abundant between 10 and 20 metres. Generally, the
abundance of benthic organisms declined with increasing water depth and
therefore, benthic organisms as a food resource are less profitable to exploit
in deeper waters. However, this does not mean, that benthic organisms
might not be a profitable prey in deep waters.
The most important factors found to shape littoral macroinvertebrate
communities are nutrient level, wind exposure, substrate type and vegetation
cover (Brodersen 1995; Tolonen et al. 2001). Most of the animal groups were
found only in the first 15 m water depths and the higher diversity in the
nearshore area might be related to the high amount of leaves and terrestrial
input from the dense forest around the lake. The differences found between
the eastern and western side might be due to wind and wave exposure. There
is a quite sharp slope at the shore at both sides of the transect and the depth
increases rapidly, which probably gives rather small amounts of macrophytes.
Macrophytes are expected to give macrozoobenthos substrate and food
(Rasmussen 1988). Yet, the littoral in Stechlinsee might have large amounts
of wood and terrestrial vegetation falling into or partly growing in the littoral
of the lake. Leaf litter can potentially be of high quality for
macroinvertebrates and give larger macroinvertebrate production than other
substrate types such as macrophytes (Oertli 1993). Chironomids are known
to be essential in the macroinvertebrate community and can account for as
much as 75-95% of the benthic secondary production in lakes surrounded by
wood (Lindegaard 1992; Oertli 1993). Chironomids are know to be an
important food source for many fish species, and they are therefore
important for the energy transfer through the food web in the lake system.
In Stechlinsee chironomids, ostracods, Trichoptera and Megacyclops have been
found in the diet of the two coregonid fish species Coregonus albula and
Coregonus fontanae (Schulz et al. 2003) but future studies need to demonstrate,
how important benthic organisms are as a food resource for Lake Stechlin
Coregonus and whether there are individual differences between fish that
exploit the benthic resource compared to the planctonic food resource.
Acknowledgement
We are very thankfull to Humboldt and Freie Universität students M. Albers,
C. Aßmann, K. Felsmann, C. Jessen, N. Jobstvogt, B. Stelbrink, M. Zadow
(all Berlin) who helped in the field and laboratory to collect and sort out the
samples. Copepods were identified by A. Rychla (Neuglobsow).
94
References
BRODERSEN, K. P. (1995): The Effect of Wind Exposure and Filamentous Algae
on the Distribution of Surf Zone Macroinvertebrates in Lake Esrom, Denmark.
Hydrobiologia, 297.2., 131-148.
DERMOTT, R. M. (1988): Zoobenthic Distribution and Biomass in the Turkey Lakes.
Canadian Journal of Fisheries and Aquatic Sciences, 45.107-114.
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relationships between profundal macroinvertebrate biomass and environmental
variables in boreal lakes of Alberta, Canada. Freshwater Biology, 41.1., 91-100.
FRANCE, R. L. (1995): Empirically estimating the lateral transport of riparian leaf
litter to lakes. Freshwater Biology, 34.3., 495-499.
HARROD, C., GREY, J. (2006): Isotopic variation complicates analysis of trophic
relations within the fish community of Plu beta see: a small, deep, stratifying lake.
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HELLAND, I. P., FREYHOF, J., KASPRZAK, P., MEHNER, T. (2007):
Temperature sensitivity of vertical distributions of zooplankton and planktivorous
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LINDEGAARD, C. (1992): The Role of Zoobenthos in Energy-Flow in Deep,
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OERTLI,
B.
(1993):
Leaf-Litter
Processing
and
Energy-Flow
Through
Macroinvertebrates in A Woodland Pond (Switzerland). Oecologia, 96.4., 466477.
OKUN, N., LEWIN, W. C., MEHNER, T. (2005): Top-down and bottom-up impacts
of juvenile fish in a littoral reed stand. Freshwater Biology, 50.5., 798-812.
PIECZYNSKA, E. (1993): Detritus and Nutrient Dynamics in the Shore Zone of
Lakes - A Review. Hydrobiologia, 251.1-3., 49-58.
RASMUSSEN, J. B. (1988): Littoral Zoobenthic Biomass in Lakes, and Its
Relationship to Physical, Chemical, and Trophic Factors. Canadian Journal of
Fisheries and Aquatic Sciences, 45.8., 1436-1447.
RASMUSSEN, J. B., KALFF, J. (1987): Empirical-Models for Zoobenthic Biomass in
Lakes. Canadian Journal of Fisheries and Aquatic Sciences, 44.5., 990-1001.
SAGRARIO, M. D. G., BALSEIRO, E. (2003): Indirect enhancement of large
zooplankton by consumption of predacious macroinvertebrates by littoral fish.
Archiv fur Hydrobiologie, 158.4., 551-574.
SCHULZ, M., FREYHOF, J., SAINT-LAURENT, R., OSTBYE, K., MEHNER, T.,
BERNATCHEZ, L. (2006): Evidence for independent origin of two springspawning ciscoes (Salmoniformes: Coregonidae) in Germany. Journal of Fish
Biology, 68.s1., 119-135.
SCHULZ, M., KASPRZAK, P., ANWAND, K., MEHNER, T. (2003): Diet
composition and food preference of vendace (Coregonus albula (L.)) in response
to seasonal zooplankton succession in Lake Stechlin. Archiv für Hydrobiologie,
Special Issues Advances in Limnology, 58.215-226.
TOLONEN, K. T., HAMALAINEN, H., HOLOPAINEN, I. J., KARJALAINEN, J.
(2001): Influences of habitat type and environmental variables on littoral
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152.1., 39-67.
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VADEBONCOEUR, Y., VANDER ZANDEN, M. J., LODGE, D. M. (2002):
Putting the lake back together: Reintegrating benthic pathways into lake food web
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96
Sustainable management of aquatic
ecosystems
Nachhaltiges Gewässermanagement
© IGB 2007
97
98
G ARCIA , X.-F., G ABEL , F., H OCHMUTH , H., B RAUNS , M., S UKHODOLOV ,
A., P USCH , M.
3.4.1 Do littoral habitats with high structural
complexity mitigate the impact of ship-induced
waves on benthic invertebrates?
Reduzieren litorale Habitate mit hoher struktureller Komplexität die
Auswirkungen schiffsinduzierten Wellenschlags auf benthische
Wirbellose?
Key words: shear stress, detachment rate, threshold, fractal dimension, inland
navigation
Abstract
Ship-induced waves constitute a major threat to macroinvertebrate communities
inhabiting littoral zones of lakes and rivers. However, factors influencing the
detachment of invertebrates by waves were never addressed nor quantified. Hence, we
investigated the interaction between structural complexity of littoral habitats and waveinduced hydraulic disturbance on invertebrates. In an experimental wave tank, five
species were exposed to waves of different shear stress (4.3 - 21.9 dyn/cm2) in five
littoral habitats, and in reed stands of four different densities, representing various
levels of structural complexity.
The number of detached invetebrate individuals depended significantly on the
applied shear stress. Detachment rate averaged for the five species was significantly
lower in habitats with a high degree of structural complexity, decreasing in the habitat
sequence sand, coarse woody debris, stones, reed and tree roots, and accordingly with
increasing reed densities. Response thresholds to hydraulic stress differed between
species according to the habitat, as species-specific fixing or hiding capabilities
matched specific physical habitat characteristics. Besides offering good sheltering
conditions for invertebrates, high structural complexity of the habitat also increased
dissipation of the waves’ kinetic energy.
Consequently, the adverse effects of boat traffic on littoral invertebrate
assemblages is drastically increased as soon as complex littoral habitats like tree roots
or dense reed belts disappear by wave action or adverse lakeshore management
practices.
Zusammenfassung
Schiffsinduzierter Wellenschlag stört die an See- und Flussufern lebenden
Wirbellosengemeinschaften in erheblichem Umfang. Bisher wurden aber die Faktoren,
die die Verdriftung der Invertebraten durch Wellen beeinflussen, weder benannt noch
quantifiziert. Daher wurden die Auswirkungen der Wechselwirkungen zwischen der
strukturellen
Komplexität
der
Uferlebensräume
und
der
welleninduzierten
hydrodynamischen Störung auf Wirbellose untersucht. In einem Wellenkanal wurden
in Experimenten Wellenhöhen mit unterschiedlicher Sohlschubspannung (4,3 – 21,9
dyn/cm²) erzeugt, die auf fünf Wirbellosenarten in fünf verschiedenen Habitattypen
sowie in Schilfbeständen mit vier unterschiedlichen Halmdichten einwirkten. Die
© IGB 2007
99
unterschiedlichen Habitattypen und die Schilfdichten stellten einen Gradienten der
strukturellen Habitatkomplexität dar.
Die Anzahl an verdrifteten Wirbellosenindividuen hing signifikant von der
einwirkenden Sohlschubspannung ab. Die über die fünf Wirbellosenarten gemittelte
Verdriftungsrate war in Habitaten mit einem hohen Grad an struktureller Komplexität
signifikant geringer. Sie nahm in der Reihenfolge Sand, Totholz, Steine und Schilf zu
Wurzeln hin ab, ebenso auch mit zunehmender Schilfdichte. Außerdem unterschieden
sich die Reaktions-Schwellenwerte der untersuchten Arten hinsichtlich des
hydrodynamischen Stresses in den einzelnen Lebensräumen, in Abhängigkeit von
Übereinstimmungen der artspezifischen Festhalte- oder Versteckfähigkeiten mit den
entsprechenden Möglichkeiten der getesteten Lebensräume. Somit bietet eine erhöhte
strukturelle Komplexität einerseits bessere Festhaltemöglichkeiten für Wirbellose, und
führt andererseits auch zu einer Dissipation der Wellenenergie.
Infolgedessen erhöhen sich die negativen Auswirkungen des schiffsinduzierten
Wellenschlags auf litorale Wirbellosengemeinschaften drastisch, wenn komplexe
Habitate, wie Wurzeln oder dichte Schilfbestände, aufgrund von Wellenschlag oder
uferbaulichen Maßnahmen verschwinden.
3.4.1.1
Introduction
Inland navigation by freight barges, passenger ships and recreational boats produces
ship-induced waves which are characterised by strong amplitudes, frequent
occurrences, short-term increase of flow velocity and which affect wind-sheltered
littoral zones as well (Bhowmik & Mazumder 1990, Rodriguez et al. 2002). As a
consequence, ship-induced waves are expected to be a major hydraulic disturbance for
organisms inhabiting the littoral zones of lakes, rivers and canals used as inland
waterways. To date, the impact of ship-induced waves on shore assemblages has been
documented by very few published studies. Bishop & Chapman (2004) provided
evidence that abundance of estuarine benthic invertebrates inhabiting intertidal
sediments were lower in boat-wash zones by comparison to non boat-wash zones.
Similarly, Holland (1986) observed an eggs mortality of 20 to 50% in fish communities
due to tows passing by on the Mississippi River. However, focusing on single
individuals, little is known so far about potential thresholds in the response of littoral
invertebrates to anthropogenic wave disturbance of increasing shear stress, or about
the interaction with habitat properties. In particular, the factors influencing the extent
to which invertebrates are detached by waves in specific littoral habitats have never
been addressed, either in natural or under experimental conditions. The only evidence
published so far comes from a related case with stream invertebrates exposed to
continuous flow. Flume experiments demonstrated that current-induced drift of lotic
invertebrate species increased with increasing flow velocities (Borchardt 1993, Imbert
1999).
High habitat structural complexity is known to increase biomass, abundance and
diversity in benthic invertebrate communities (O’Connor 1991, Schmude 1998, Beck
2000, Taniguchi et al. 2003, Taniguchi & Tokeshi 2004). Consequently, the complexity
of the 3-dimentional structure of the habitat is expected to also be a key component in
reducing hydraulic stress on benthic invertebrate. Already, Borchardt (1993) in his
experiments on current-induced drift showed that the proportion of drifting
individuals decreased when more and more woody debris was added to sand habitat. In
100
the current study, we investigated the resistance of invertebrate species to increasing
wave disturbance for habitats of different degrees of structural complexity, in order to
assess how physical characteristics of littoral habitats mitigate the adverse effect of
ship-induced waves on benthic invertebrates. Using two distinct experimental set-ups,
we mutually considered the nature (habitat-types) and the density of the habitat
structures, two complementary components of the habitat structural complexity. We
hypothesized that (i) the proportion of detached individuals directly depends on the
level of shear stress associated with the wave; (ii) the proportion of detached
individuals also depends on species-specific adaptations to certain habitats, and (iii) the
number of detached individuals decreases with higher habitat structural complexity.
3.4.1.2
Methods
In an experimental wave tank (L: 3 m, W: 0.80 m and H: 0.60 m) five invertebrate
species (Bithynia tentaculata, Calopteryx splendens, Dikerogammarus villosus, Gammarus roeseli
and Laccophilus hyalinus) were exposed to single waves of increasing strengths (shear
stress range: 4.3 - 21.9 dyn/cm2) in natural habitats representing various levels of
structural complexity. Two series of experiments were conducted. In the first series,
the five invertebrate species were exposed in five different littoral habitats [sand, coarse
woody debris (CWD), stones, reed, and tree roots]. In the second series, the same five
species were exposed in reed habitats of four different stem densities (45, 127, 175 and
250 stems/m²), depicting a comparable gradient of structural complexity than the five
habitats.
The structural complexity of the habitats was quantified by their fractal dimension
(FD), calculated following the Frontier’s grid method (Frontier 1987) on sizecomparable top-view digital pictures of the habitat trays. The frame of the habitat tray
was taken as the first square of the grid, which was progressively split into half-sized
finer grids until reaching a level of 4,096 squares. On each grid level the proportion of
squares entered with an edge of a habitat component was set into relation to the total
number of squares in one row. The slope of the log transformed relationship gave
value for the FD.
Prior experiments were conducted to test the stability and reproducibility of the
hydraulic conditions in the wave tank when producing waves. Hence, the 10 different
wave strength levels possibly produced were significantly different from each other
(ANOVA with Post-Hoc test, Scheffé procedure, N=10, p=0.023 at the lowest) and
reproducible in time (coefficient of variance: 0.36 - 2.17 %, N=10 per strength level).
Flow motion was approximately unidirectional, vertically and laterally uniform
(ANOVA, N=10 per test, p>0.05 for all tests) with almost null values of vertical and
lateral velocities, supporting the conditions of a laminar flow. Consequently, wave
strength was expressed by the bottom shear stress τ (dyn/cm2) caused by the wave at
the location of the habitat (1), calculated using the wave friction factor () formula
given by Dyer (1986) for laminar flow (2):
© IGB 2007
W
0.5 fUU b2
f
2
Q
UbAb
:
wave friction factor
density of water (1 g/cm 3 )
U b : maximum wave orbital velocity (cm/s)
(measured by an acoustic Doppler velocimeter, 50 Hz)
(2)
A b : maximum bottom wave amplitude (cm)
(measured by an acoustic wave sensor, 20 Hz)
Q:
water viscosity (~0.01 cm²/s)
(1)ρ:
101
The five habitats and species selected were common for the littoral zones of northeastern German lakes. Beside, species were also chosen to depict contrasted body
shapes and behaviors, which should influence their fixing and hiding capabilities. The
designing of the habitats in the wave tank (two trays of 0.115 m² area each) followed
spatial arrangements and densities commonly observed in natural conditions. The
habitat structural complexity increased in the following sequence: sand (FD=1), CWD
(1.30), stones (1.34), reed175 (1.39) and roots (1.80) for habitats and reed45 (FD=1.02),
reed127 (1.29), reed175 (1.39) and reed250 (1.45) for habitat densities. The energy lost by
the wave when passing through the habitat was quantified as the shear stress difference
in front and behind the habitat, for incoming waves of three different shear stress
levels (13.7, 16.4 and 19.8 dyn/cm2).
For each experiment (= one habitat-species combination), 20 individuals of similar
body size were exposed to three replicated waves per shear stress level, with a time
interval of 15 minutes. Wave strength was increased until 100% of the individuals were
dislodged or the maximum applicable shear stress reached. For each wave produced,
wave velocity, wave amplitude and the number of individuals detached from the
habitat (counted from video records) were recorded.
3.4.1.3
Results and discussion
For the five species exposed to waves, a similar pattern of increasing number of
detached individuals in relation to increasing shear stress was observed in sand, CWD,
stones (Fig. 1A) and in the four reed habitats differing in stem density (Fig. 1B). These
relationships could be well described by sigmoide regression models (Table 1) which
were all significant except for B. tentaculata on stones and reed45 and from C. splendens in
reed250. Conversely, such pattern was not observed in root habitat, the most complex
habitat, from which only few individuals of each species were detached by the
strongest waves. The strength of this relationship varied however according to the
species-habitat combination considered
Table 1. Regression coefficients (r²) and significance levels (*** p<0.001, ** p<0.01, *
p<0.05, n.s. non significant) of the sigmoid regression models describing the total number of
detached individuals in each habitat as a function of the shear stress caused by
experimental waves.
CWD
Reed250
0.81***
0.48*
0.76***
0.78***
0.64*
0.04ns
0.92***
0.96***
Stones
0.81***
0.52*
0.99***
0.02 n.s.
0.81***
0.66*
0.05 n.s.
0.97**
0.79***
0.86***
Dikerogammarus villosus
0.84***
0.06 n.s.
0.79***
0.56**
0.61**
0.92***
Gammarus roeseli
0.92***
-
0.71**
0.88***
0.87***
0.80***
0.94***
0.93***
Laccophilus hyalinus
0.85**
0.12 n.s.
0.99***
0.94***
0.99***
0.98***
0.89***
0.95***
Calopteryx splendens
102
Reed175
Sand
Bithynia tentaculata
Reed45
Reed127
Roots
(A)
(B)
Fig.1. Number of detached individuals as a function of the shear stress caused by
experimental waves. (A) in each habitat for C. splendens and G. roeseli, (B) for each
species in CWD and reed 250 . Plotted values represent mean number of detached individuals
(± SE) for three replicated waves.
The comparison of the total numbers of detached individuals averaged for the five
species (mean ± SE) showed that more individuals were detached in sand (130.2 ± 6.8)
than in CWD (67.5 ± 9.5), stones (60.5 ± 11.3), reed (48.6 ± 11.2) and roots (4.7 ±
1.6) (Fig. 2A). Total number of detached individuals was significantly different between
sand and all other habitats (ANOVA with Post-Hoc test, Scheffé procedure, N=75,
p<0.01) as well as between roots and all other habitats (p=0.002 at the lowest). No
significant differences of the total number of detached individuals were observed
between CWD, stones and reed (p>0.05 for the three tests). Similarly, less individuals
were detached when reed stem density increased (respectively: 83.1 ± 22.2, 71.9 ± 21.5,
48.6 ± 20.9 and 44.1 ± 19.6 - Fig. 2B). Significant differences were recorded between
reed densities of 45 - 127 stems/m² in one side and reed densities of 175 - 250
stems/m² in the other side (ANOVA, with Post-Hoc test, Scheffé procedure, N=60,
p<0.05). Obviously, sand habitat did not offer appropriate hiding or fixing spots for
any of the five species while the dense network of tiny and flexible branches
constituting the root bunch allowed every species, irrespectively its size or gripping
strategy, to enter the bunch and fix itself efficiently. More generally, the detachment of
invertebrates by wave-induced hydraulic disturbance is significantly reduced in
complex habitats, as more complex habitats provide more refuges and anchorage
points that enable individuals to resist drag forces imposed by peaks in flow velocity.
© IGB 2007
103
140
160
a
(A)
120
100
100
b
80
b
b
60
(B)
140
120
dasfier
Total number of detached individuals
160
a
a
b
80
b
60
40
40
20
c
20
0
0
Sand
CW D
Stones
Reed175
Reed45
Roots
Reed127
Reed175
Reed250
Fig. 2. Total number (mean ± SE for the five species) of detached individuals for (A) each
habitat and (B) each reed density. Bars with different letters indicate significant differences
among habitats.
Considering each species separately, strong disparities were observed in the total
number of detached individuals between habitats, revealing a species-specific response
to wave-induced hydraulic disturbance according to habitats (Tab. 2). Indeed, it is
obvious that the degree of detachment of invertebrates depends on how speciesspecific fixing or hiding capabilities matched specific physical habitat characteristics.
For example, the rough ridges of CWD provided good anchorage points for species
fixing themselves with big claws like C. splendens and D. villosus, but not for the snail B.
tentaculata, which needs smoother surfaces as reed stems to suck efficiently, neither for
G. roeseli and L. hyalinus which possess smaller claws (see Fig. 2B). Beside, the attraction
exerted by the habitat on the individuals also depends on how the size of the refuges
defined by the habitat structure matches the size of organism body (Taniguchi &
Tokeshi 2004).
Tab. 2: Total number (mean ± SE, N=3) of detached individuals for the cross combinations
of species and habitats studied.
CWD
Bithynia
tentaculata
Calopteryx
splendens
Dikerogammarus
villosus
Gammarus
roeseli
Laccophilus
hyalinus
80.0
± 1.5
29.7
± 1.2
29.0
± 0.6
74.7
± 0.9
124.3
± 1.5
Roots
8.0
± 0.6
0.3
± 0.3
0.3
± 0.3
0.0
± 0.0
14.7
± 0.9
Sand
124.3
± 3.2
166.3
± 0.3
100.7
± 1.4
100.8
± 2.5
151.7
± 1.8
Stones
Reed 45
Reed 127
Reed 175
Reed 250
22.3
± 0.9
65.0
± 2.6
9.0
± 1.2
79.0
± 1.7
127.3
± 2.0
16
±3
68
± 1.2
73.3
± 2.9
109.3
± 1.5
149
± 3.7
8
± 1.7
48
± 1.5
70.7
± 2.4
98.7
± 0.6
134
± 2.9
12.3
± 0.3
8.0
± 2.1
47.3
± 1.2
50.7
± 4.9
124.7
± 2.3
12.3
±3
3.7
± 0.9
40.3
± 1.5
49.3
± 0.3
115
± 1.2
In order to take into account this heterogeneity in species response, we tested using
a multiple classification analysis (MCA, Andrews et al. 1973), how far differences in
individuals detachment rates observed between habitats were influence by either
species or habitat. MCA examines the interrelationship between several predictor
variables and one dependant variable and provides the part of explained variance by
each predictor, both before and after taking into account the effects of all other
104
predictors. MCA revealed that 55.8% of the variance in maximum number of detached
individuals was explained by differences in habitats (value corrected from the influence
of the species factor) against 20.8% by differences between species (value corrected
from the influence of the habitat factor - r²model = 0.77, p<0.001, N=75). Similarly,
differences in reed density explained 76.6% of the overall variance in maximum
number of detached individuals against 17.8% explained by differences in species
(r²model = 0.94, p<0.001, N=60). In the latest, B. tentaculata and L. hyalinus were removed
as they were respectively few and always dislodged from reed habitats, thus not
contributing to any variance. Hence, despite contrasted species-specific responses
according to habitats, nature and density of the habitat have the strongest influence on
detachment rates in wave experiments
Consequently, the impact of the wave-induced hydraulic disturbance on
invertebrates was found to significantly decrease along the overall gradient of structural
complexity depicted by the different habitats (Spearman´s rho = - 0.99, p<0.001, N=8,
Fig. 4A). Comparable influences of habitat complexity in sheltering benthic
invertebrates against hydraulic disturbance have been similarly demonstrated for
Seratella ignita and Gammarus pulex exposed to high currents (Borchardt 1993). In this
study, the proportion of individuals drifted away decreased when more and more
woody debris was added to the sandy bottom of the circular flume.
Shear stress reduction (dyn/cm²)
12
d
(A)
12
10
10
8
8
6
4
a
b
c
(B)
6
b,c
4
a
a,b
b
Reed127
Reed175
b
2
2
0
0
Sand
CW D
Stones
Reed175
Roots
Reed45
Reed250
Fig. 3: Shear stress reduction (mean ± SE) for an incoming shear stress level of 22 dyn/cm².
(A) in the five habitats, (B) for the four reed densities .Bars with different letters are
significantly different.
In addition to provide fixing possibilities for the invertebrates, structural habitat
complexity also affects flow motion in the surroundings of the habitats. For all
habitats, shear stress recorded behind the habitat was significantly lower than in front
of the habitat (paired t-test, N=10 per test, p<0.001 at the lowest). Comparing the
shear stress reduction due to habitats, significant differences in shear stress reduction
were recorded between sand and stones, sand and reed and between roots and the
other habitats (ANOVA, Post-Hoc tests, Scheffé procedure, N=50, p=0.014 at the
lowest, Fig. 3A) as well as between reed45 and reed175 and reed250 (N=40, p=0.021 at the
lowest, Fig. 3B). Shear stress reduction was found to be significantly correlated with
the structural complexity of the habitat (Spearman´s r = 0.97, p<0.001, N=8 - Fig. 4B).
This result matches findings of Atilla et al. (2005) who found reduced flow velocities
and lower Reynold’s numbers behind more complex brushes than behind less complex
ones. From the perspective of flow mechanics, the structure of the habitat provides
obtrusions to the unidirectional flow which generates cross flow motions such as
turbulences. In turbulent flows, the kinetic energy of the flow is extracted by the larger
© IGB 2007
105
vortices from the mean flow, transferred by the cascade of turbulences towards the
smaller scales, where it finally dissipates into heat due to molecular viscosity (Tennekes
& Lumley 1972). Correspondingly, higher structural complexity provides more
obstacles to flow and dissipates a larger portion of kinetic energy.
Total number of detached individuals
140
(A)
Spearman r = - 0.99, p<0.001
120
100
80
60
40
20
0
1,0
1,2
1,4
1,6
1,8
2,0
Fractal dimension (FD)
Shear stress reduction (dyn/cm²)
10
(B)
Spearman r = 0.97, p<0.001
9
8
7
6
5
4
3
2
1
0
1,0
1,2
1,4
1,6
1,8
2,0
Fractal dimension (FD)
Fig.4. Relationships between the fractal dimension of the habitats and (A) the total number
(mean ± SE for the five species) of detached individuals, (B) the shear stress reduction
(mean ± SE for three incoming shear stress levels: 13.7, 16.4 and 19.3 dyn/cm²) caused by
the habitats.
3.4.1.4
Conclusion
In this study, experimental evidence on the ecological effect of artificial wave
disturbance was collected by systematically varying wave energy, habitat complexity
and species-specific characteristics under standardized conditions. The complex
interactions between species and their habitat preferences were taken into account by
using a set of natural habitats as well as species differing in body shapes and fixing
capabilities. Also, the nature and the density of habitat structures both contributing to
the overall habitat structural complexity were mutually considered.
High structural complexity of habitats proved to be related with good sheltering
conditions for invertebrates against hydraulic disturbance. This relationship could be
106
causally explained, as high structural complexity provided more refuges or anchorage
points for the invertebrates, and as it reduced substantially wave kinetic energy.
The conclusions drawn from this indoor experimental study most probably also
apply in natural conditions. Waves produced in the wave tank reached maximum flow
velocities up to 51 cm/s. However, 50% of the individuals were already detached at
shear stress values of 6-15 dyn/cm², which correspond to flow velocities of 19-42
cm/s. By comparison, flow velocities measured in the field on Lake Langer See and on
the River Spree (Berlin, Germany) ranged from a minimum of 21-44 cm/s for small
private boats to a maximum of 324 cm/s for freight barges and sight-seeing passenger
ships. Hence, the comparison of laboratory and field hydrodynamic conditions
indicates that the detachment of organisms may be even stronger in natural conditions
than demonstrated by our experiments, and probably the most important factor acting
on the invertebrate assemblages exposed to ship-induced waves, even for wave of low
energy.
Thresholds for ship-induced shear stress were nevertheless identified that were still
tolerated by most of the invertebrates studied. These thresholds were the lowest in
sand habitat (4-8 dyn/cm²), higher in the other habitats (14-16 dyn/cm²) and not
reached for roots at the maximum shear stress level we were able to produce in the
wave tank (21.9 dyn/cm²). It can be concluded that network habitats such as tree
roots, and to a certain extent also dense reed belts, provide efficient protection of
invertebrates against wave-induced disturbance. Consequently, complex habitats such
as tree roots and dense reed belts must be protected in order to preserve a diverse and
natural fauna in the littoral zone of inland waterways, as required by water policies.
References
ANDREWS, F.M., MORGAN, J.N., SONQUIST J.A., KLEM, L. (eds.) (1973): Multiple
Classification Analysis. Second edition. Ann Arbor: Institute for Social Research,
University of Michigan.
ATILLA, N., FLEEGER, J.W., FINELLI, C.M. (2005): Effects of habitat complexiy and
hydrodynamics on the abundance and diversity of small invertebrates colonizing
artificial substrates. Journal of Marine Research63: 1151-1172.
BECK, M. W. (2000): Seperating the elements of habitat structure: independent effects
of habitat complexity and structural complexity and structural components on
rocky intertidal gastropods. Journal of Experimental Marine Biology and Ecology
249: 29-49.
BHOWMIK N.G., MAZUMDER B.S. (1990): Physical forces generated by barge-tow
traffic within a navigable waterway. In: Hydraulic Engineering (Eds H.H. Chang &
J.C. Hill), pp. 604-609. American Society of Civil Engineers, New York, USA.
BISHOP, M.J., CHAPMAN, M.G. (2004): Managerial decisions as experiments: an
opportunity to determine the ecological impact of boat-generated waves on
macrobenthic infauna. Estuarine Coastal and Shelf Science 61: 613-622.
DYER, K.R. (1986): Coastal and estuarine sediment dynamics. Chichester: Wiley.
FRONTIER, S. (1987): Application of fractal theory to ecology. In P. Legendre & L.
Legendre (Eds.), Development in Numerical Ecology, NATO ASI Series Vol.
G4:335-378, Berlin, Springer.
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HOLLAND, L.E. (1986): Effects of barge traffic on distribution and survival of
ichthyoplankton and small fishes in the upper Mississippi River. T. Am. Fish. Soc.
115(1): 162-165.
O’CONNOR, N.A. (1991): The effects of habitat complexity on the macroinvertebrates
colonising wood subsrates in a lowland stream. Oecologia 85: 504-512.
RODRIGUEZ J.F., ADMIRAL D.M., LOPEZ F., GARCIA M.H. (2002): Unsteady bed
shear stresses induced by navigation: laboratory observations. Journal of
Hydraulic Engineering, 128, 515-526.
SCHMUDE, K.L. (1998): Efects of habitat complexity on macroinvertebrate
colonization of artificial substrates in north temperate lakes. Journal of Northa
American Benthological Society 17: 73-80.
TANIGUCHI, H., NAKANO, S., TOKESHI, M. (2003): Influences of habitat complexity
on the diversity and abundance of epiphytic invertebrates on plants. Freshwater
Biology 48: 718-728.
TANIGUCHI, H., TOKESHI, M. (2004): Effects of habitat complexity on benthic
assemblages in a variable environment. Freshwater Biology 49:1164-1178.
TENNEKES, H., LUMLEY, J.L. (1972): A first course in turbulence. Cambridge,
Massachusetts, MIT Press.
108
K OSCHEL , R., B EHRENDT , H., H UPFER , M.
3.4.2 Integrated protection of surface waters 1
Integrierter Gewässerschutz von Binnengewässern
Key words: ecotechnolgy, eutrophication, freshwater management,
protection of waters, water pollution
Abstract
Highly efficient measures for freshwater ecosystem protection require
complex actions. Surface waters are closely connected to their terrestrial and
atmospheric environment, and therefore, preventive protection of surface
waters begins in the catchment. Improvements and stabilisation of aquatic
ecsystems by reduction of point and diffuse loading (redevelopment) must
be balanced increasingly with structural optimisation of ecosystems
(restoration and ecotechnology), and must be based on a strategy of
“integrated management”. Limited financial resources for surface water
protection demand an optimal combination of the principles of emissions
and imissions.
Zusammenfassung
Binnengewässer sind empfindliche Indikatoren für Störungen der natürlichen
Stoffkreisläufe, weil sie sehr eng mit der terrestrischen Umgebung, dem
Grundwasser und der Atmosphäre verbunden sind. Zu den weltweit
häufigsten Gewässerproblemen, die die Nutzung der Ressource Wasser
erheblich beeinträchtigen, gehören die Eutrophierung, die Versauerung, die
Kontamination mit Schadstoffen und die Versalzung. Eine Beseitigung von
Gewässerschädigungen und ein effektiver Gewässerschutz erfordern
integrative Ansätze, zu dem verschiedene Fachdisziplinen einen Beitrag
leisten müssen. Da die Gewässer und die Einzugsgebiete wegen ihrer
vielfältigen Struktur ganz unterschiedlich auf Stressfaktoren reagieren und
Belastungen kompensieren können, scheint eine alleinige Orientierung auf
die Reduzierung von Emissionen auch mit Blick auf die begrenzten
finanziellen Mittel für den Gewässerschutz nicht sinnvoll. Stattdessen sollte
die gezielte Optimierung der Struktur ökologischer Systeme Bestandteil eines
modernen Gewässerschutzes sein. Dazu gehören im Einzugsgebiet eine
ressourcenschonende Bewirtschaftung landwirtschaftlicher Flächen und die
Revitalisierung von Pufferökosystemen, die als Stoffsenken in der
Landschaft wirken. Im Gewässer selbst können durch ökotechnische
Verfahren erwünschte Funktionen besonders gefördert werden. Für die
Durchführung solcher Optimierungsstrategien fehlen teilweise aber noch die
naturwissenschaftlichen Grundlagen und geeignete Vorhersageinstrumente.
Sehr große Defizite gibt es bei der ökonomischen Bewertung ökologischer
1
© IGB 2007
changed version after Koschel et al. 2005, Koschel et al. 2007
109
Gewässerfunktionen und bei der Erforschung sozio-ökonomischer
Konsequenzen, die ein langfristig angelegter Gewässerschutz erfordert.
3.4.2.1
Surface waters are our future
The surface waters are essential and precious resources worthy of protection.
They have to be regarded as i) economic goods – referring to their manifold
functions within landscape water budgets, ii) part of the food supply – as
drinking water, and iii) buffer and service systems – because of their high
biological diversity. These three aspects act in concert, and determine the
goals of integrated water protection and sustainable management of water
resources. World-wide, surface waters, soils, and atmosphere are considered
to be severely changed and destabilised by natural fluctuations and diverse
human uses (industry, municipal water supply, agriculture) as well as
unbalanced management (WBGU 1999). Standing and running waters are
especially susceptible to eutrophication, soil erosion, toxic loads, increase in
salinity, and acidification.
In addition, widespread disturbances of the natural chemical cycles have
emerged, and it is presently difficult to estimate the consequences for the
water resources. The multiple integrations of the ecosystems with natural
cycles can become strongly reduced, and may, in part, vanish. In the journal
»Nature«, the paper »The value of the world’s ecosystem services and natural
capital« was published in 1997 (Constanza et al. 1997). The authors tried to
evaluate the non-cost functions of ecosystems, and calculated the annual
services of lakes and rivers to amount to US$ 850,000 for one km-2 water
surface. Furthermore, the authors highlighted the meaning of surface waters
for water supply, self-purification, and recreation. According to their
evaluation, standing and running waters alone support communal services by
as much as US$ 1.7 trillion per year, a sum equal to 10% of the world’s gross
economic product. These values exemplify the importance of sustaining the
above mentioned non-cost services, and that from the economic point of
view, it is useful to counteract the degradation of ecosystems over time.
Surface waters not only suffer from external point sources emitting
nutrients and pollutants, but also from a variety of other anthropogenic
impacts. These influences comprise diffuse losses into aquatic ecosystems
especially from agriculture and from the atmosphere, and severe damage of
the surface water structure by construction work, excessive use, spatially
extended decreases in groundwater level, and leaks of petrol components in
catchments. At present, diffuse loading are increasing rather than decreasing,
and result from both former and present land use in catchments. The diffuse
losses cause problems for the protection of standing and running waters as
well as for estuaries and ocean via long-distance influences.
However, the »emission principle« has started to counteract the negative
developments of external loading, and refers to both point sources from
communal and industrial waste water treatments, and diffuse losses especially
due to agricultural activities. Nonetheless, the present external loading is still
about 10-fold higher than the geogenic background. In addition, long
residence times in groundwater delay the effects of reduced emissions on
110
diffuse loading for several decades. The application of emission-oriented
measures alone for the improvement of water quality has limited success.
Internal mechanisms may counteract a rapid and efficient improvement of
water quality, for example by nutrient and pollutant release from sediments,
alterations of the food web, and long residence times of the water bodies
(Hupfer & Kleeberg 2007). The nitrogen elimination in waste water
treatments exemplifies that in some cases, emission-oriented measures are
often not useful from the economic and ecological point of view. First,
nitrogen loading can efficiently be eliminated in the water body by natural
microbial nitrate reduction especially in combined lake-river systems, and
second, the decrease of nitrate emissions promotes phosphate mobilisation
from sediments. Thus, the measure is counterbalanced.
For these reasons, highly efficient measures for surface water protection
require complex and integrated actions (Figure 1). Improvements and
stabilisation of aquatic ecosystems by reduction of point and diffuse loading
(redevelopment), must be balanced with structural optimisation of
ecosystems (restoration and ecotechnology in surface waters and
catchments). This combined strategy will be elucidated by exemplifying
important problems and trends of the water quality of standing and running
waters in Germany.
RECREATION
outstanding
restricted
good
very low polluted
catchment area
(high evectiveness
of landscape)
unpolluted natural
oligotrophic to
slightly eutrophic
aquatic ecosystems
WATER QUALITY
poor
problem-free
degrated highly
eutrophic aquatic
ecosystems
problematic
DRINKING WATER,
BATHING, FISHING
highly polluted
catchment area
(slow evectiveness
of landscape)
Fig. 1: The influence of the terrestrial surroundings on water use and water quality (Koschel
et al. 1998).
3.4.2.2
Pollutant exposure in rivers, lakes, and coastal waters
Aquatic ecosystems are prone to numerous natural and anthropogenic stress
factors of a physical, chemical, and biologic nature, resulting from loading of
energy, waste waters, and bacteria. The most common problems in surface
waters, causing significant restrictions of their use, are loadings of nutrients
and pollutants. Pollutant loading can be evoked by a broad spectrum of
inorganic and organic chemicals. Anthropogenic sources of toxic metals
comprise ore processing, metal industry, road traffic in urban centres, the use
© IGB 2007
111
of herbicides, and emissions of gases rich in sulphur and nitrogen, the latter
of which lead to corrosion of metal surfaces.
Organic pollutants consist of pesticides, organic tensides, pharmaceutical
chemicals, and petrol components. Metals and organic chemicals, such as
polychlorinated biphenyls (PCB), become enriched in sediments and food
webs, and may exceed toxic concentrations. Chemicals that act as
pseudohormones, and influence the reproduction and development of
vertebrates, are released in high concentrations in urban areas; these
substances are defined as hormone-active substances or endocrine
disruptors. Synthetic-active substances are part of pharmaceuticals and
industrial chemicals (e. g. organo-chlor-pesticides, PCB, derivates of tensides,
and phtalates). For example, synthetic estrogens, which are part of
contraceptives and other hormone treatments, are released into the
environment via waste water and waste water treatments.
The emissions of gases containing sulphur and nitrogen cause acid rain,
which in turn promotes acidification of surface waters and soils in regions
with low chalk and low buffering capacity. This happens even at great
distances from the points of emissions. Acidified surface waters are often
clear and thus, apparently are of high water quality. However, the decrease in
pH is a reason for the extreme changes of their biocoenoses. Fish and other
animals cannot survive or reproduce. As a further consequence, toxic metal
ions (especially aluminium, copper, zinc, and lead) are increasingly released
from soils and sediments. Especially the north-east of North America and
Scandinavia are suffering from acidification. In Germany, the acidification
via atmospheric deposition is limited to some regions, such as in the
Bavarian Forest and the Black Forest. In addition, exploitation of natural
resources can render surface waters prone to extreme acidification. In
Germany, there are approximately 500 lakes created by coal mining on a
medium-term scale of 10 to 50 years. Most of these lakes are geogenically
strongly acidified during their generation. Coal mining leads to the oxidation
of minerals rich in sulphur (pyrite, marcasite) causing the release of acids.
3.4.2.3
Eutrophication
Eutrophication is the most common problem in surface waters.
Eutrophication is defined as the increasing intensity of primary production
(trophic state) of a surface water, which is due to increased availability and
uptake of nutrients. Since the middle of the last century, the extent of
eutrophication has been markedly increased by insufficiently treated waste
water, artificial use of nutrients in households (phosphorus in detergents),
and by run-off from agricultural areas. Thereby, the deterioration of lakes
has been significantly accelerated. As a consequence of eutrophication,
blooms of phytoplankton and macrophytes have undesired impacts and
severely restrict water uses. The water becomes turbid and changes its
colour, blooms of toxic cyanobacteria, loss of diversity, oxygen depletion,
generation of sulphide, high fish mortality, and nuisance by smell occur.
Thereby, several types of water uses, such as water supply, fishing, and
recreation become restricted. Additionally, in eutrophicated surface waters,
112
the effects of toxins can be synergistically reinforced, because these
ecosystems are partly destabilised.
In Germany, there are significant regional differences in the trophic state
of lakes. In Brandenburg and Mecklenburg-Vorpommern, 90% of 1,500
lakes were classified as mesotrophic or eutrophic, whereas in Bavaria and
Baden-Württemberg, less than 50% were of high trophic state. The reasons
for this difference are partly natural. The present and former loadings from
agriculture are reflected by a high portion of eutrophicated lakes. A major
problem due to eutrophication of inland waters results from the proximity of
intensely used agricultural areas to surface waters, and the intensification of
this, coupled with drainage and irrigation measures. Agriculture targets at
maximum plant production, however, high biomass production in surface
waters should be avoided because of its negative consequences.
The phosphorus (P) acts as a limiting factor and controls the degree of
eutrophication in most inland waters. Since the mid 1980s, the existing
dominant point emissions of P, were reduced by as much as 80% with the
introduction of P-free detergents. However, the diffuse emissions of P were
only slightly decreased. Small losses of P from the terrestrial catchment
usually mean a considerable charge of water ecosystems by P. For many
inland waters, loadings related to events such as rainfall the result in shortterm erosion. The slow P export via leaching, is a long-term problem
difficult to predict. At sites with a low sorption capacity near the
groundwater table, the long-term fertilisation of agricultural areas, especially
by manure, may cause complete saturation with P in the entire soil layer.
Scoumans et al. (1988) found that already at the end of the 1980’s, more than
10,000 ha of soils were saturated with P in the Netherlands. Similar
phenomena can be found also in other regions with low groundwater tables,
soils with low sorption capacity and extreme livestock densities (Behrendt &
Beockhold 1993). Also in rivers in the north-west of Germany, those
catchments which drain agriculturally farmed peat soils with extreme low
sorption capacity are very vulnerable to P leaching. The consequence of both
cases is that P-concentrations in small rivers can reach the order of
magnitude of municipal waste water.
Many running waters are suffering from eutrophication. For example,
during the last decades, a considerable increase in algal biomasses could be
detected in the low courses of the large German rivers. This was due to
waste water treatment strategies which primarily aimed to reduce organic
loadings, and neglected the elimination of mineral nutrients; thereby,
nutrients were emitted directly in available forms to surface waters (Behrendt
et al. 2003). Eutrophication sources of shallow coastal waters, such as
lagoons, show that the sources of eutrophication can be several 100
kilometres distant from the location where the eutrophication occurs. For
example, the River Oder contributes 15% of the total nutrient emissions to
the Baltic Sea, yet it forms a low portion (7%) of the catchment of the Baltic
Sea, it has however a high population density which contributes to the
sources of eutrophication (Behrendt & Dannowski 2005).
© IGB 2007
113
The change in nutrient loads of rivers could be reconstructed by the
modelling of emissions to, and the turnover within, surface waters, including
periods without measurements. Figure 2 represents the changes of P loads in
the River Oder during the last 50 years. Although a decrease in P load due to
the introduction of P-free detergents has already started, the present level of
P loading to the Baltic Sea by the River Oder exceeds the emissions in the
1960’s.
7000
6000
phosphorus load (t/a)
5000
4000
3000
2000
1000
0
1960 1965 1970 1975 1980 1985 1990 1995 2000
Fig. 2: Phosphorus loads of River Oder to the Baltic Sea (1960-2000) (Behrendt &
Dannowski 2003).
3.4.2.4
Strategies to control water ecosystems
Problems with surface waters are usually first perceived when there are
restrictions in water uses. Remedial actions aim to improve the state of
surface waters, while keeping costs reasonably low. Concerning the planning
and execution of measures, the practical question arises as to the degree to
which the development of the problem should be reversed.
The aim of the remediation is often the return to the natural or original
state. However, definition of this state is difficult. It should not mean the
state directly after generation of the surface water. What should be defined as
the original state? When humans did not yet decisively influence the
ecosystem, which usually means before the Neolithicum, at the end of the
Atlanticum, approximately 5,000 years ago? In those times, climate was
warmer than today, and in Central Europe, the catchments of the inland
waters were covered by a dense canopy of mixed oak tree forests (oak tree,
lime tree, elm tree). It is impossible to redevelop the climate of a landscape
and its surface waters, and it is almost impossible to change the cultivated
landscape of today into a non-cultivated forest landscape. Therefore, the
maximum aim of natural remediation measures should be the potential
natural state of surface waters. This reference state, the named ideal state, is
characterised by a state, which is close to that of preindustrial times. The
ideal state can be individually estimated for each water body by guidelines
and by palaeolimnological investigations, and is to be compared with the
actual state. The need for action is great if the actual state significantly differs
from the ideal state.
In contrast, the formulation of the aim of development for a lake or river
is arbitrary, but should be adapted to present and future human exploitation
and settling of the landscape, to ecological knowledge, technical progress and
114
financial capacities (Steinberg et al. 2002). The definition of the aim of
development is an iterative process that should be carried out in concert by
users, owners, experts, and politicians.
The charge limits of a water ecosystem are determined by its structure
and the structure of its environment. For example, the potential
decomposition of organic substances is much lower in regulated river
systems than in naturally structured water courses. Critical load models are
helpful for achieving qualitative aims of aquatic ecosystem management.
These models enable the user to describe qualitative states of an ecosystem,
depending on the charge and characteristics of the surface waters. This
means that a potential control strategy may include the optimisation of the
structure and processes within a lake, so that symptoms of excessive charge
can be minimised. The response to changes of charges often follows a sort
of hysteresis, in which eutrophicated lakes can persist in their state, despite
reductions of external loadings. Furthermore, sufficient decreases in external
loadings cannot always be achieved at suitable low costs, and remaining
loadings can be compensated for by internal measures. Modern protection of
surface waters should therefore consider a combination of external and
internal measures. Which external and internal methods and control
opportunities are available at present? There are many examples for a slow
reduction of diffuse nutrient emissions by »best management practice« and
by extensifying agricultural land use.
3.4.2.5
Optimisation of sinks and ecotechnology
Beside the reduction of nutrient emissions at their source, the restoration of
original nutrient retentions structures within the landscape, such as bogs,
ponds, and floodplains, represents the opportunity to reduce diffuse nutrient
emissions by internal links in terrestrial and aquatic ecosystems. Thereby, a
sustainable management of matter and water circulation is accomplished.
Intact ecosystems minimise losses of matter by short-circuiting cycles of
water, nutrients, and mineral substances (Ripl & Wolter 2001). Intact
ecosystems are sustainable. However, the consequent application of the
concept mentioned above would result in severe restrictions, or even losses,
of existing uses. External loading can and must also be reduced close to
surface waters by the construction of phosphorus elimination plant for the
purification of river water, or by the creation of buffer systems, such as
barriers and retention areas planted with Phragmites australis, if it is not
possible to create retention structures within the catchment.
Technical procedures can influence the physical, chemical, and biological
structure of surface waters. Reduction of available nutrients can be used to
reduce primary production within the water body, and hence improve its
trophic state. The desired improvement can be accelerated, and at the same
time external loadings can be decreased, if the P retention within the
sediments of lakes is increased by the use of substances for chemical
precipitation. Thereby, remaining loading could be compensated for or a
level of P concentration could be attained which allows positive feedback
and the efficient application of further measures. Biomanipulation is a
© IGB 2007
115
reasonable example for such measures. By biomanipulation, fish populations
are optimised. As a consequence of the resulting decline of the food web,
feeding pressure on undesired phytoplankton is increased, and the water
becomes clearer. However, global evaluation of such applications has
revealed that a certain level of P loading has to be accomplished in order to
achieve efficient biomanipulation. In conclusion, high efficiency of measures
in surface waters can be achieved by a combination of measures.
3.4.2.6
Need for action and research
- Using the ecological potential
Recent investigations showed that restoration measures oriented only
towards the reduction of emissions is questionable, especially considering the
limited financial resources in water protection. The vision that any loading
reduction has always a positive effects is no longer valid. Instead, the
capacities of ecosystems to withstand charges dependent upon their
structures has to be explored, and the manifold ecological functions and
services have to be used optimally. At present, detailed knowledge of the
functioning of surface water ecosystems and their reactions to anthropogenic
influences is insufficient. In particular, our understanding is lacking
considering that the state of aquatic ecosystems is a function of biological,
chemical, hydraulic, hydrological, meteorological, and physical influencing
factors, including their temporal and spatial changes. There is a need for an
efficient and integrated scientific instrument, which will enable us to analyse
the behaviour of ecosystems on a functional, process-oriented, and
reproducible basis. In addition, the trends in development of ecosystems
need to be calculable with a high degree of certainty (Figure 3).
character of ecosystems
energy - and
matter limitation
open dissipative systems
reflection in theory of management
M
minimize energy waste
close matter circulation
sensitive reaction to external
inputs (e.g. climate change)
homoeostatic
systems
multiple mediated
feedback systems
unexpected consequences
(e.g. toxical cyanobacteria)
adaptive,
self-organizing systems
ways of self-adaptation
(e.g. bistability)
Fig. 3: Theoretical principles of aquatic ecosystems, their reflection in the theory of aquatic
ecosystem management and the illustration of knowledge deficits (modified after Straskraba
1993).
The comprehensive and harmonised integration of applied external
measures (within the catchment), and internal measures (within the water
ecosystem), should be increasingly efficient, if the existing lack of knowledge
is minimised. Both the principles of emissions and imissions have to be
considered within integrated surface water protection.
116
- Acceleration of knowledge transfer in the water economy
Lewandowski et al. (2002) have revealed that the actual effects of lakeinternal measures were often far below those expected. In some instances
the applied scientific measures were useless. The research task should be to
improve and evaluate the scientific basis of lake-internal measures. In turn,
this knowledge should feed applicable decision support systems (Schauser et
al. 2003). The better the scientific basis, the more difficult it is to ignore the
state of the art (Figure 4). The slow publication of research results limits
knowledge transfer, and our knowledge of the environment needs to be
more publicly accessible.
Analysis of current state
Check-up
of targets
Identification of problems and
definition of targets for the water qualitity
Determination of acceptable nutrient
loading by using of lake models
Identification and quantification
of external and internal nutrient sources
Yes
Are measures in the catchment area
planned or already carried out?
Yes
Prediction
Can the external loading decrease below a
critical threshold within tolerable periods?
No
No
Yes
Is the expected adaptation time
after external measures acceptable?
No
Cause study
Long
water residence
time?
High
internal loading?
No
Yes
Yes
Yes
Yes
Internal measures may be possible
No
No
Yes
Internal measures are inefficient
Fig. 4: Decision making process prior to the application of ecotechnologies, demonstrating
procedures fpr increasing nutrient retention in a lake (Hupfer et al. 1997).
- Strengthening our knowledge base by case studies
Further reduction of emissions from point sources does not lead to a
remarkable decrease of external nutrient loading with acceptable costs. It
seems that mainly diffuse loading is an unsolved long-term problem, difficult
to identify, and to predict by existing methods.
Case studies from diverse geographical regions could help to analyse the
effects, and the course of nutrient loading, by changing land use. Little
knowledge exists on the locations and capacities of retention mechanisms in
© IGB 2007
117
relation to the total loading from catchment areas. For example, the risk of
rewetting bogs, which thereby might become P sources, is controversial,
because bog systems apparently react in different ways. Restoration of P
retention areas may lead to a restriction or decline of existing human uses,
which however, decreases public acceptance. The socio-economic problems
related to these consequences also have to be solved by related scientific
approaches. Holistic pilot studies could contribute to solving these problems
(»whole ecosystem experiments« as scientific method).
- Development of cost benefits analysis
There are great gaps in our knowledge of the economic evaluation of
ecological functions of surface water systems. In addition, by practical
applications it was shown that even sound scientifically-based management
measures are not always accepted and financially supported. Therefore, there
is a need for further supporting arguments. The inclusion of financial
efficiency should be considered as an important element of future strategies
for surface water protection. However, the scientific basis is incomplete.
These requirements become increasingly important, especially concerning
the implementation of the Water Framework Directive of the EU (WFD),
which aims to accomplish and evaluate a »good ecological state« for all
surface waters.
- Policy recommendations and reinforcement of basic research
Conversion of integrated protection of surface waters and the sustainable
development of the environment entails many new tasks and challenges for
surface water research. Therefore, we need scientifically well based and
defined ideals, which are oriented towards the main ecological and
hydrological functions of surface waters. The main function can be defined
as, the complexity of the food web extending from bacteria to fish
(information is stored in structures and genetic codes), the discharge rate of
water bodies, the matter circulation, the self-purification potential and the
close interrelationship between air (climate), land, and water. We need highly
developed instruments (models) for determining and predicting the
integrative impacts of anthropogenic and natural factors on the quality and
quantity of surface water ecosystems, which in turn should include both
socio-economic and global climate changes. We need an extended basis for
the economic evaluation of water as a resource. Modern integrated
protection of surface waters requires an efficient combination of the
principles of reconstruction, redevelopment, restoration, and ecologically
useful and sustainable water use. In advance, these requirements demand a
high degree of knowledge of the manifold and highly complex processes in
surface water ecosystems. Equally, there is a high need for basic research,
which should cover improved knowledge of biological, chemical, and
physical structures and their functions within surface water ecosystems, and
of the regulation of the manifold transport and transformation processes
extending from the catchment to the water bodies.
118
- Increase social acceptance
Integral surface water protection inevitably causes conflicts between
inhabitants, users of water and land, and owners. These conflicts can only be
solved on a long-term basis if environmental education is reinforced, and
new forms of public discussion are developed. There have to be
opportu¬nities created for politicians, employees of districts and
communities, and pressure groups to gain knowledge about the field of
surface water protection. Dissemination of information to the media can
contribute to making water problems perceivable and to highlight possible
actions. Conflicts should increasingly be solved in panels with the
participation of inhabitants and the public in the decision process.
Public interest and political pressure have sometimes meant that internal
measures in polluted lakes were carried out without the necessary preliminary
investigations. Often, these measures were not successful, and at the same
time, they exploited the scarce financial resources, which could have been
used for more efficient measures.
- Combine the principles of emissions and imissions
Surface waters are closely connected to their terrestrial environment, and
therefore, preventive protection of surface waters begins in the catchment.
Limited financial resources for surface water protection demand an optimal
combination of the principles of emissions and imissions (Benndorf et al.
2003). Many ecological and technical standards are oriented towards the
principle of zero emissions (such as those for toxic substances), the state of
the art of technology (for example four purification steps in waste water
treatments), or they are apparently arbitrary. In some cases, imissions of nontoxic substances could be tolerated, which are higher than the concentrations
permitted by directives and laws, if the ecosystem structure is created and
optimised accordingly. The latter can be accomplished by eco-technological
procedures. Therefore, the principle of zero emissions of any costs is not
recommended. Efficient protection of surface waters requires procedures
which are adapted to individual cases and regions.
References
BENNDORF, J., KOBUS, H., ROTH, K., SCHMITZ, G. (eds.) (2003): In: DEUTSCHE
FORSCHUNGSGEMEINSCHAFT: Wasserforschung im Spannungsfeld zwischen
Gegenwartsbewältigung und Zukunftssicherung (Water research in the discourse
of overcoming present problems and future security.), Wiley, Weinheim, 175 pp.
BEHRENDT, H., BOEKHOLD, A. (1993): Phosphorus saturation in soils and
groundwater. Land Degradation & Rehabilitation, 4, 233-243.
BEHRENDT, H., BACH, M., KUNKEL, R., OPITZ, D., PAGENKOPF, W.-G., SCHOLZ, G.,
WENDLAND, F. (2003): Quantifizierung der Nährstoffeinträge der Flussgebiete
Deutschlands auf der Grundlage eines harmonisierten Vorgehens. (Quantification
of nutrient emissions in the catchments of Germany using harmonized
procedures.) Text of the UBA, 82/03, 201 pp.
BEHRENDT, H., DANNOWSKI, R. (eds.) (2003): Nutrients and heavy metals in the
Odra River system, Weißensee Verlag, Berlin, 335 pp.
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CONSTANZA, R., D‘ARGE, R., DE GROOT, R., FARBER, ST., GRASSO, M., HANNON, B.,
LIMBURG, K., NAEEM, S., O’NEIL, R. V., PARUELO, J., RASKIN, R. G., SUTTON,
P., VAN DEN Belt, M. (1997): The value of the world’s ecosystem services and
natural capital. Nature, 387, 253-260.
HUPFER, M., GELBRECHT, J., SCHARF, B. & C. STEINBERG (1997): Konzeptionelle
Ansätze zur Steuerung des Phosphat-Haushaltes durch seeinterne Maßnahmen.
(Conceptual approaches to control the phosphorus budgets by lake-internal
measures.) Wasser und Boden, 49 (12), 8-13.
HUPFER, M., KLEEBERG, A. (2007): State and pollution of freshwater ecosystems –
warning signals of a changing environment. In: LOZAN, J. L., GRAßL, H., HUPFER,
P., MENZEL, L., SCHÖNWIESE, D. (eds): Global change: Enough water for all?
Hamburg, 126-132.
KOSCHEL, R., BRÜGGEMANN, R., KASPRZAK, P. (1998): Ökotechnologien zur
Sanierung und Restaurierung von Standgewässern. (Ecotechnologies to
reconstruct and restore standing waters.) Spektrum der Wissenschaften, 9, 97-100.
KOSCHEL, R., BEHRENDT, H., HUPFER, M. (2005): Integrierter Gewässerschutz für
Binnengewässer: Maßnahmen zum nachhaltigen Umgang mit der Ressource
Wasser. (Integrated protection of surface waters for the sustainable use of the
resource water.) In: WGL (eds.): Zwischenruf, 2, 4-15.
KOSCHEL, R., BEHRENDT, H, HUPFER, M. (2007): Surface waters under stress factors
and their controlling by integrated measures. In: LOZAN, J. L., GRAßL, H.,
HUPFER, P., MENZEL, L., SCHÖNWIESE, D. (eds): Global change: Enough water
for all? Hamburg, 89-94.
LEWANDOWSKI, J., SCHAUSER, I., HUPFER, M. (2002): Bedeutung von Vor- und
Nachuntersuchungen in der Seentherapie. (The importance of pre- and postinvestigations in lake therapy.) Wasser & Boden, 54 (9), 21-25.
RIPL, W., WOLTER, K.-D. (2001): Stoffstrommanagement nach dem EnergieTransport-Reaktions-Modell (ETR-Modell) (Management of substance flow
according to the energy-transport-reactions-model). Wasser & Boden, 53(10), 4-9.
SCHAUSER, I., LEWANDOWSKI, J., HUPFER, M. (2003): Decision support for the
selection of an appropriate in-lake measure to influence the phosphorus retention
in sediments. Wat. Res., 37, 801-812.
STEINBERG, C., WEIGERT, B., MÖLLER, K., JEKEL M. (eds.) (2002): Nachhaltige
Wasserwirtschaft. Entwicklung eines Bewertungs- und Prüfsystems (Sustainable
water economy. Development of a system for evaluating and testing.). Initiativen
zum Umweltschutz, 36, Schmidt Verlag Berlin, 311. pp.
STRASKRABA, M. (1993): Ecotechnology as a new means for environmental
mangement. Ecol. Engineering, 2, 311-331.
WISSENSCHAFTLICHER
BEIRAT
DER
BUNDESREGIERUNG
GLOBALE
UMWELTVERÄNDERUNGEN (WBGU) (1999): Welt im Wandel – Erhaltung und
nachhaltige Nutzung der Biosphäre. Jahresgutachten 1999. (Global change –
conservation and sustainable use of the Biosphere.). Annual Report, Springer,
Berlin 482 pp.
120
M EINELT , T., B URNISON , B. K., P LAYLE =, R., P IETROCK , M.,
W IENKE , A., S TEINBERG , C. E. W.
3.4.3
Dissolved organic matter (DOM) modulates the
cadmium accumulation in zebrafish (Danio
rerio) embryos
Huminstoffe beeinflussen die Cadmium-Akkumulation in Zebrabärblingsembryonen (Danio rerio)
Key words: cadmium, accumulation, DOM, egg compartments, zebrafish
Abstract
We conducted experiments to investigate factors influencing the
accumulation of cadmium 109Cd into zebrafish (Danio rerio) embryos. The Cd
accumulation was affected by 1) concentration, 2) time, 3) presence of
dissolved organic material (DOM), 4) different origin of DOM and 5)
different parts of fish eggs. The zebrafish eggs showed a steady increase in
Cd-accumulation with time and concentration. DOM concentrations over 15
ppm carbon (C) decreased Cd uptake significantly. Both DOM-samples, the
brown water marsh (LM) and an eutrophic pond (SP), at 16.9 ppm C,
reduced the Cd-accumulation in the chorion, perivitelline liquid and the
embryo. Cd was mainly accumulated in the egg’s outer shell chorion (61%)
and only small amounts passed through the chorion into the perivitelline
liquid (38%) and embryo (1%). The accumulation of Cd into the egg
components was decreased by 41% (chorion), 56% (perivitelline liquid) and
53% (embryo), in the presence of LM-DOM, compared with the control
group. Similarly, the presence of SP-DOM reduced the Cd accumulation by
27% (chorion), 63% (perivitelline liquid) and 59% (embryo), respectively,
compared with the controls.
Zusammenfassung
Mittels radioaktiv markiertem Cadmium 109Cd wurden Faktoren untersucht,
welche die Cd-Akkumulation modifizieren. Die von uns untersuchten
Parameter waren 1) Cd-Konzentration im umgebenden Testwasser, 2)
Expositionszeit, 3) Präsenz und Konzentration (in ppm Kohlenstoff) von
Huminstoffen (HS), 4) Herkunft der HS und 5) verschiedene
Fischeikompartimente. Die Zebrafischeier zeigten eine mit der CdKonzentration und Expositionszeit stetig steigende Cd-Akkumulation. HSKonzentrationen >15 ppm Kohlenstoff verringerten die Cd-Akkumulation
signifikant. Die Präsenz beider verwendeten HS, Luther Marsh (LM) und
Sanctuary Pond (SP), in Konzentrationen von 16,9 ppm Kohlenstoff
reduzierten die Cd-Akkumulation im Chorion, in der Perivitellinen
Flüssigkeit und im Embryo. Cd wurde hauptsächlich im Chorion (61%)
akkumuliert. Nur kleinere Cd-Mengen passierten diese Barriere und
akkumulierten sich in der Perivitellinen Flüssigkeit (38%) bzw. im Embryo
(1%). Die Cd-Akkumulation in den einzelnen Kompartimenten der
© IGB 2007
121
Zebrabärblingseier wurde durch LM-HS um 41% (Chorion), 56%
(Perivitelline Flüssigkeit) bzw. 53% (Embryo) reduziert. Bei SP-HSExposition verringerte sich die Cd-Akkumulation um 27% (Chorion), 63%
(Perivitelline Flüssigkeit) bzw. 59% (Embryo) verglichen mit der Kontrolle.
3.4.3.1
Introduction
Both the uptake of Cd and its toxicity to fish have been intensively studied
(John et al. 1987), and are known to be affected by several water parameters,
particularly the concentrations of calcium (Ca2+, Michibata et al. 1986) and
dissolved organic matter (DOM, Playle 1998, Playle et al. 1993a, 1993b,
Richards et al. 1999). The amount of metal which can be complexed to
DOM depends on pH, ionic strength, metal concentration and some DOM
characteristics (Petersen et al. 1987). A number of studies have shown that
DOM can either increase or decrease the toxicity of metals to freshwater
organisms (Playle et al. 1993a, Penttinen et al. 1995, Richards et al. 1999,
Meinelt et al. 2001). Hammock et al. (2003) studying the accumulation of
different metals in Chinook salmon (Oncorhynchus tshawytscha) eggs noted e. g.
reduced Cd-concentrations in the egg chorion and yolk in the presence of a
humic acid (Aldrich®) compared to control. According to Michibata (1981)
and Beattie & Pascoe (1978), most of the total Cd detectable in eggs of
medaka (Oryzias latipes) and trout (Oncorhynchus mykiss), is bound to the
chorion. The present study we tested the effects of exposure time, and metal
and DOM concentration on uptake and quantitative distribution of 109Cd in
the presence of two different DOM.
3.4.3.2
Rearing of the parental fish, production of eggs, test water
Production of eggs and rearing of embryos is described in Meinelt et al.
(2001). The investigations were carried out using standardized test water
according to EN ISO 7346-3 (1996). To minimize Ca2+ interference, the
calcium content of the water was reduced to a tenth of the nominal
reconstituted water-Ca concentration. Thus the reconstituted water
contained Ca2+ 0.2 mmol L-1, Mg2+ 0.5 mmol L-1, K+ 0.077 mmol L-1, Na+
0.77 mmol L-1; dissolved oxygen was 7.0 ± 0.5 mg L-1, pH between 7.47 –
7.97, and temperature 22 ± 0.2°C.
Dissolved organic matter (DOM)
DOM was isolated from two natural waters of different trophic states and
with different DOC concentrations as described by Burnison et al. (2006).
Luther Marsh (LM) yielded mainly allochthonous DOM and Sanctuary Pond
(SP) mainly autochthonous DOM.
Exposure time experiment
To examine the effect of exposure time on accumulation of 109Cd in
zebrafish eggs, ten fertilized eggs were transferred into a 1.5 mL
microcentrifuge tube with cap containing 350 µL reconstituted water
containing 109Cd (Amersham Biosciences, specific activity = 41.6 MBq/µg)
with a radioactivity of 3000 kBq. After exposure times of 15, 30, 45, 60, 120,
180, 240, and 300 minutes, respectively, an excessive amount of “cold” Cd
122
(as CdCl2 x H2O, 500 ng) was added to each tube to block free binding sites
at the chorion and, thus, limiting further uptake of 109Cd. After rinsing the
eggs with reconstituted water, the eggs were transferred to glass scintillation
vials, and 10 mL of scintillation cocktail (Ultima Gold, Packard Instrument
Co.) were added. The radioactivity of the eggs was determined using a liquid
scintillation counter (Tri-Carb 4430, Packard Instrument Co.) The exposures
were run in duplicate.
Metal concentration experiment
To examine the effect of metal concentration on accumulation of 109Cd, ten
fertilized eggs were placed into Petri dishes (Falcon Tight-Fit Lid, 50 mm,
Fisher Scientific) containing 2 mL of reconstituted water with one of four
different 109Cd concentrations. The 109Cd concentrations were calculated on
the basis of the radioactivity present in each solution, and the specific activity
of the radioisotope. The duplicate Cd-concentrations were 7.02/7.03,
14.0/13.8, 33.2/33.7, and 63.7/64.0 nM. After an exposure time of four
hours, “cold” Cd was added to each solution, followed by rinsing the eggs
with reconstituted water, addition of the scintillation cocktail and
determination of radioactivity (see above).
DOM concentration experiment
Twenty fertilized eggs were placed into a Petri dish and exposed to 20.3 nM
109Cd mixed in 6 mL of either reconstituted water containing no added
carbon (control), or with 5, 10, 15, 20 ppm C, LM DOM. After 8 hours
exposure, the eggs of each group were rinsed three times with reconstituted
water to remove free 109Cd, and 10 mL of the scintillation cocktail (Ultima
Gold, Packard Instrument Co.) were added to the eggs to determine their
radioactivity using the liquid scintillation counter (see above). The
experiment was run in triplicate.
Dissection experiments
Twenty fertilized eggs each containing a 24-hour-old embryo were placed
into a Petri dish and exposed to two ml Cd solution (20.3 nM 109Cd) mixed
with six ml of either reconstituted water containing no added carbon
(control), 16.9 ppm C of LM- or 16.9 ppm C of SP-DOM. After a four-hour
exposure, the eggs of each group were rinsed three times with reconstituted
water to remove free 109Cd, and then transferred into Petri dishes containing
3 mL of reconstituted water. An aliquot (100 µL) was transferred from each
of the three dishes into separate scintillation vials and measured for
radioactivity to ensure that no free 109Cd remained. The intact eggs were
carefully dissected into their components (chorion, embryo, perivitelline
liquid [Fig. 1]) by means of a stereomicroscope and two sharpened
microforceps. The thin chorion shells were transferred into 1.5 mL
microtubes and were centrifuged at 2,800 rpm. The supernatant was carefully
returned into the respective Petri dish that still contained the embryos. The
chorion pellets were washed three times again and transferred into
scintillation vials. Embryos were pipetted into scintillation vials by means of
wide bore Eppendorf tips to protect the fragile embryos from mechanical
© IGB 2007
123
damage. Any fluid carried over along with the embryos was carefully put
back into the Petri dish using a micropipette. Finally, this fluid, consisting of
perivitelline liquid and reconstituted water washes, was transferred into
Chorion
Perivitelline
Embryo
250 µm
Fig. 1: Microscopic structure of zebrafish egg
separate scintillation vials. Ten mL of the scintillation cocktail were added
each to chorion-pellets, embryos and perivitelline liquid/reconstituted water
preparations and radioactivity was measured using the liquid scintillation
counter (see above). The experiment was run in triplicate.
Statistical analysis
Statistical analysis was conducted by using of SPSS 9.0.1 (SPSS Inc. 1999)
using standard procedures. Analyses of variance (ANOVA) were used for
the dissection experiments, the unpaired t-test were used to analyze the data
of the DOM experiments. Significance level was set at p= 0.05. The
statistical methods used are outlined in Lozan & Kausch (2004).
3.4.3.3
With increasing exposure time, the total amount of 109Cd in the eggs
increased (Fig. 2). A positive correlation between exposure time and amount
of 109Cd taken up by the zebrafish eggs was found (r= 0.82). In the
concentration experiments, a positive correlation between metal
concentration in the test medium and amount of 109Cd taken up by the
zebrafish eggs was found (r = 0.92, Fig. 3). With increasing concentrations of
DOM (LM) from 10 - 20 mg L-1 C there was a significant reduction in Cd
accumulation in the fish eggs compared to the control (Fig. 4). Exposure to
both LM-DOM as well as SP-DOM at concentrations of 16.9 mg L-1 C led
to a significantly (p < 0.01) reduced amount of Cd detectable in the eggs
(Fig. 5). However, no significant difference between LM- and SP-DOM (p=
0.813) was detected.
In the presence of LM-DOM, the accumulation of Cd into the zebrafish
egg decreased by 41% in the chorion, 56% in the perivitelline liquid and 53%
in the embryo, compared with control group eggs. Similarly, in the presence
of SP-DOM, Cd accumulation decreased by 27% (chorion), 63%
(perivitelline liquid) and 59% (embryo), compared with the controls (Fig. 6).
Cd accumulation in perivitelline liquid was significant lower in DOM-groups
compaired to the controls (p< 0.0001), wheras there were no significant
differences in Cd accumulation in embryo and chorion compaired to
124
controls (p= 0.487, p= 0.159). The Cd content of zebrafish eggs increased
significantly with time and Cd concentration of the surrounding medium. We
Cadmium Uptake (picomol/g)
50
40
2
R = 0.66
30
20
10
0
0
50
100
150
200
250
300
Time (min)
Fig. 2: Time dependent cadmium uptake by zebrafish eggs
160
Cadmium Uptake (picomol/g/hr)
140
120
2
R = 0.93
100
80
60
40
20
0
0
10
20
30
40
50
60
70
Cadmium Concentration (nM)
Fig. 3: Concentration dependent cadmium uptake by zebrafish eggs
found a steady increase in Cd accumulation over 300 minutes. In Atlantic
salmon (Salmo salar), Rombough & Garside (1982) found a rapid Cd uptake
by embryos, with dose-dependent saturation levels which were reached
within 24 h and persisted until hatching. Thus the time point of reaching
saturation depends strongly on external factors. Species-specific endogenous
factors may also affect Cd uptake in fish eggs (see below). When Cd is
© IGB 2007
125
accumulated in fish eggs, it may be detected in the different components at
different concentrations. Typically most of the Cd is associated with the
chorion (Peterson & Martin-Robichaud 1986), which in rainbow trout
(Oncorhynchus mykiss) keeps 98% of the total Cd, (Beattie & Pascoe 1978), in
medaka (Oryzias latipes) 94.6% (Michibata 1981) and Chinook salmon
(Oncorhynchus tshawytscha) 93% (Hammock et al. 2003). In our experiments we
found that only 61% of the Cd was bound to the chorion of the zebrafish
eggs.
Cadmium Uptake (picomol/g/h)
250
200
*
*
15
20
150
100
50
0
Control
5
10
DOC (mg/L)
Fig. 4: Influence of different concentrations of Luther Marsh DOM on Cd-accumulation in
zebrafish eggs. Error bars represent standard deviation (n = 3) and the asterisks denote a
significant difference compared to the control at the p < 0.05 level.
Fish species may be a major reason for the variation in Cd retention by
the chorion, because the thickness of the chorion varies widely among
species. Chinook salmon eggs are up to 10 mm in diameter and show a
chorion thickness of up to 50 µm. In contrast, diameter of the zebrafish eggs
is about 1 mm with a chorion thickness of about 3.5 µm, which is thus more
than 14 times thinner than the Chinook salmon egg chorion. Calculating the
volume of the Chinook salmon egg, their chorion comprises a 1,400 times
higher volume compared to the zebrafish chorion. According to Rombough
(1985) the chorion potentially modulates the toxicities of metals since metal
ions must penetrate the chorion, before they exert toxic effects on the
embryo. Since the chorion is rich in negatively charged glutamic acid, metal
cations probably bind selectively to such anionic sites (Rombough 1985). In
this respect, thick eggs like that of salmon contain high amounts of glutamic
acid which has a much higher retention capacity for Cd than do thin
126
zebrafish eggs, with presumably low amounts of glutamic acid, and hence a
lower retention capacity for Cd.
In the presence of DOM, the accumulation of Cd in the zebrafish eggs
was significantly lower than the control, 53% for LM and 58% for SP,
respectively. The reduction in Cd accumulation is also reflected by a
specifically lowered Cd content in the different egg components. If DOM
was present, the allocation of Cd in the chorion declined to 41% (LM) and
26% (SP), compared to the control, in perivitelline liquid 56% (LM) and 63%
(SP) compared the controls, while in the embryo only 53% (LM) and 59%
(SP) compared to DOM-free control remained. We hypothesize that formed
DOM-Cd complexes were unable to penetrate the chorion thus binding to
its surface. Therefore, the amount of Cd, capable of penetrating the egg
chorion is lowered in presence of DOM.
Cadmium Upake (pmol/g/h)
1200
1000
800
*
*
Luther Marsh
Sanctuary Pond
600
400
200
0
Control
Fig. 5: Effect of different DOM sources (16.9 mg L -1 C) on Cd-accumulation in zebrafish
eggs. Error bars represent standard deviation (n= 3) and the asterisk denotes a
significant difference compared to the control at the p< 0.05 level.
Both DOM sources lowered the amount of Cd accumulated in egg
components compared to control. However, only Cd-accumulation in
perivitelline liquid was highly significant different between DOM-groups and
controls. Although the two water bodies from which the respective DOM
were isolated differ in total content, origin and formation of their DOM, the
capacity to prevent passage of Cd through the chorion of zebrafish eggs was
very similar. Several recent ecotoxicological studies have consistently
identified that watersoluble and ionizable humic materials are relatively small
(~0.5 kDa) and, when considering a single source, are very regular in
structure (Reemtsma & These 2003, Cooper et al. 2004, Hatcher et al. 2004,
Seitzinger et al. 2005). Additionally, these authors consistently state that, if
higher molecular masses than ~0.5 kDa do occur, the building blocks are
© IGB 2007
127
bridged by several intramolecular mechanisms, whereby one major
mechanism is the bridging of two- or polyvalent cations, such as Cd2+ or
Ca2+. From uptake studies with 14C-labelled microcystins by zebrafish
embryos (Wiegand et al. 1999), it was shown that even these substances with
molecular masses of approximately 1.4 kDa can be taken up. This molecular
mass, however, may be considered the upper threshold, and larger molecules
will not pass this barrier.
Control
Luther Marsh
Sanctuary Pond
700
Cadmium Uptake (pmol/g/h)
Cadmium Uptake (pmol/g/h)
800
600
500
400
*
300
20
18
16
14
12
10
8
6
* *
4
2
0
Embryo
*
*
200
100
0
Chorion
Perivitelline liquid
Embryo
Fig. 6: Cadmium accumulation in the chorion, perivitelline liquid and embryo in the
presence of different DOM sources (16.9 mg L -1 C). Error bars represent standard
deviation (n= 3) and the asterisk denotes a significant difference compared to the control
at the p < 0.05 level.
In all exposure groups only 1% of the total measured Cd was bound to
the embryos. In the perivitelline fluid 38% (control), 31% (LM) and 24%
(SP) of the total bound Cd was found. Thus, the accumulation in the
respective egg components varies with the DOM source, too. However, Cd
accumulated in the eggs was highest in the controls followed by SP and LM.
Thus, the developing embryo was typically well protected from Cd pollution
in the surrounding water by the chorion and this protection is enhanced in
presence of DOM.
Cd-accumulation in fish eggs is affected by several parameters like, Cdconcentration, exposure time, the presence of DOM. In particular, the
presence of DOM, beside other factors like Ca2+-content and egg shell
thickness, protects the developing fish embryos from Cd intoxication. Most
of the Cd is bound to the egg chorion with even less in the presence of
128
DOM. Concentration of DOM as well as the source, and, thereby the
chemical characterization of the DOM, must be take in consideration while
estimating ecotoxicological effects of Cd on fish populations.
Acknowledgement
The project was financially supported by the DLR, Germany and
Environment Canada.
Dedicated to the memory of Dr. Richard C. Playle (1956-2005), an excellent
scientist, colleague and good friend.
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130
P OYNTON , S. L., S AGHARI F ARD , M. R., B LEISS , W., J ØRGENSEN , A.,
W EISHEIT , C., M EINELT , T., R ENNERT , B., C HENG , J., K IRSCHBAUM ,
F., K NOPF , K.
3.4.4 Towards improved management of infection in
aquaculture: strategies arising from the hostparasite
interactions
in
rainbow
trout
Oncorhynchus mykiss and the pathogenic
flagellate Spironucleus salmonis
Wege zu einem verbesserten Management von Infektionskrankheiten
in der Aquakultur: Strategien basierend auf der Wirt-Parasit Interaktion
zwischen der Regenbogenforelle Oncorhynchus mykiss und dem
pathogenen Flagellaten Spironucleus salmonis
Key words: diplomonad, Spironucleus salmonis, diagnosis, rainbow trout, Oncorhynchus
mykiss, SSU rRNA gene, ultrastructure, encystment, susceptibility, life cycle
Abstract
Intensive aquaculture of rainbow trout, Oncorhynchus mykiss, provides an environment
in which parasites can rapidly be transmitted. Among the common protozoan
pathogens affecting farmed rainbow trout in Germany are diplomonad flagellates
found in the lumen of the intestine. To provide new tools for management of the
infections, we undertook studies to characterise the parasite, improve understanding of
the life cycle, and develop a new test to predict host susceptibility. Ultrastructural
studies confirmed the flagellate as Spironucleus salmonis, characterised by a smooth
surface and a caudal projection. The sequence of the small subunit (ssu) rRNA gene
and the microhabitat preference distinguish S. salmonis from other piscine
diplomonads. Recognition of distinct stages in the transformation of active
trophozoites into immobile resistant cysts, sometimes clustered in colonies, suggest
new treatment targets. We have successfully modified a plasma incubation test, initially
used for flagellates in the blood, and adapted for use with S. salmonis from the
intestinal lumen. We can assess the effect of the plasma from different fish species on
S. salmonis by using a combination of lysis, cytotoxicity, and time that the flagellates
survived in the inoculation. Preliminary data shows a good correction between in vitro
results and host susceptibility based on epizootiological data.
Zusammenfassung
Die intensive Aquakultur der Regenbogenforelle, Oncorhynchus mykiss, schafft
Bedingungen, unter denen sich Parasiten sehr schnell ausbreiten können. Zu den bei
kultivierten Regenbogenforellen in Deutschland gewöhnlich auftretenden einzelligen
Krankheitserregern gehören diplomonade Flagellaten im Darmlumen der Fische. Um
neue Verfahren zum Management der Infektionskrankheit zur Verfügung zu stellen,
führten wir Untersuchungen zur Charakterisierung des Parasiten und zu einem
besseren Verständnis dessen Entwicklungszyklus durch und entwickelten einen neuen
Test, der Aussagen zur Empfänglichkeit eines Wirtes zulässt. Ultrastrukturelle
Untersuchungen bestätigten, dass es sich bei dem Flagellaten um die Art Spironucleus
© IGB 2007
131
salmonis handelt, welche durch eine glatte Oberfläche und einen caudalen Fortsatz
charakterisiert ist. Die Sequenz des ssu rRNA Gens sowie das bevorzugte
Mikrohabitat unterscheiden S. salmonis von anderen Diplomonaden in Fischen. Die
Beobachtung spezieller Entwicklungsstadien während der Transformation von aktiven
Trophozoiten zu enzystierten und manchmal kolonienbildenden Dauerstadien gibt
Hinweise auf neue Behandlungsmöglichkeiten. Wir haben erfolgreich einen
ursprünglich für Blutflagellaten verwendeten Plasma-Inkubationstest modifiziert und
für die Verwendung mit S. salmonis angepasst. Mit der Beobachtung von Lyse,
Zytotoxizität und Überlebensdauer der Flagellaten lässt sich der Effekt des Plasmas
unterschiedlicher Fischarten auf S. salmonis bestimmen. Erste Daten zeigen eine gute
Übereinstimmung der in vitro Ergebnisse mit epizootiologischen Untersuchungen zur
Wirtsspezifität von S. salmonis.
3.4.4.1
Introduction
Parasites as economic constraints in aquaculture
Intensive aquaculture provides conditions in which parasites can florish, since fish are
held at high stocking densities, and parasites can easily be transmitted from one fish to
another. When parasite diseases occur in aquaculture, they can cause significant loss of
stock via morbidity, and acute and chronic mortality, especially when husbandry
standards are poor.
In Germany, rainbow trout, Oncorhynchus mykiss is the principal farmed species,
with the production of some 25,000 tonnes per year placing Germany among the top
10 producers of rainbow trout worldwide (Brämick 2004, FAO 2004). Among the
commonly reported pathogens of rainbow trout in Germany, are diplomonad
flagellates (Spironucleus spp.), found in the intestine and associated with weight loss and
death of young fish (Roberts & Schlotfeldt 1985, Schäperclaus et al. 1990, Schlotfeldt
& Aldermann 1995, Woo & Poynton 1995, Uldal & Buchmann 1996, Buchmann &
Bresciani 2001). Despite their common occurrence, these protozoans are poorly
characterised, and many aspects of the host-parasite interactions are unknown.
Diplomonad flagellates
In the trout, these small flagellates, approximately 10 µm long, are commonly found
swimming in the intestinal lumen. This motile feeding stage, known as the trophozoite,
can reproduce by longitudinal binary fission. Outside of the fish, the resistant cyst
stage passes through the water, awaiting ingestion by a fish. When the cyst reaches the
intestine, excystment occurs to release a trophozoite, thus the life cycle is completed
(Woo & Poynton 1995).
The literature is replete with taxonomic confusion over the true identity of the
diplomonads in trout in Germany, and authors have commonly referred to them as
Octomitus intestinalis truttae (Schmidt 1919) or Hexamita salmonis (Sanzin 1965,
Schäperclaus et al. 1990, Schlotfeldt 1991), although Spironucleus is probably the correct
genus (Poynton et al. 2004).
Diagnosis, managing, and predicting infections
Accurate identification of pathogens is a key element of effective monitoring and
management of diseases. For diplomonad flagellates, we now recognise that while light
132
microscopy is helpful in confirming the presence of diplomonad flagellates,
transmission electron microscopy (TEM) is essential for identification to genus
(Brugerolle et al. 1973, Poynton & Sterud 2002). For identification to species, a
comprehensive approach using ultrastructure and molecular characterisation is needed
(Poynton & Sterud 2002). The ultrastructure alone is insufficient, since organisms that
look the same may be differentiated based on sequence data from the ssu rRNA gene
(Jorgensen & Sterud 2004, 2006). Furthermore, aspects of the relationship with the
host are also important for characterisation of species (Poynton & Sterud 2002).
For management of diplomonad infections in aquaculture, another key element is
effective treatment of infections. Although the trophozoites can be treated with the
drug metronidazole, which is usually given in the feed (Stoskopf 1993, Woo &
Poynton 1995), this drug is not licenced for use in the EU (Buchmann & Bresciani
2001). To the best of our knowledge, there are no treatments targeted at the cyst stage
of the parasite, and the mechanisms for transformation of trophozoites to cysts are
poorly documented.
With increasing concern about transmission of parasites and diseases between
farmed and wild stock, it is important to recognise the range of hosts that a particular
parasite can infect, and among these, the species in which disease is likely to occur.
Susceptibility to infection by piscine diplomonads is currently determined by
conducting experimental infections (Kent et al., 1992; Uzmann et al., 1965); however
this is expensive and time consuming. In contrast, susceptibility to infection for some
other flagellates can be determined based upon the innate immunity of the host, via in
vitro testing using an incubation of host plasma and cultured parasites (Bower & Woo
1977; Wehnert & Woo 1980; Belosevic & Faubert 1987).
Aims of our study
To improve management of diplomonad infections in farmed rainbow trout we are
focussing our attention on three aspects: (1) comprehensive characterisation of the
parasite using ultrastructural, molecular, and ecological approaches, (2) improved
understanding of the life cycle, via documentation of the transformation of
trophozoites to cysts, and (3) development of a plasma incubation test to predict host
susceptibility to infection.
3.4.4.2
Rainbow trout infected with diplomonads were collected from a farm near Berlin, and
held at the Institute until the time of examination. Most of the fish were juveniles, 10 –
20 cm total length.
Characterisation
Diplomonads were processed in situ, and as cell suspensions, for the scanning and
transmission electron microscopy studies (Saghari Fard et al. 2007). Particular features
of taxonomic interest were the cell surface and the architecture of the posterior end
(SEM), and the accessory cytoskeleton and cytoplasmic organelles (TEM). Our
molecular characterisation focussed on sequencing of the small subunit (ssu) rRNA
gene (Saghari Fard et al. 2007). For ecological characterisation, we considered the
microhabitat preference of the diplomonads in the intestine of the fish, and
© IGB 2007
133
documented the occurrence and density of the diplomonads, and the pH, in four
regions of the intestine (pyloric, anterior, mid, and posterior) (Weisheit 2004).
Life cycle
The stages in the process of transformation of trophozoites to cysts were observed in
organisms maintained in in vitro culture. Primary cultures were maintained in minimal
essential medium (MEM) supplemented with calf serum, sodium bicarbonate solution,
and antibiotics (Uldal 1996). The culture flasks were incubated at 10 ºC in the dark.
For photography, samples were preserved in 3% glutaraldehyde in 0.1 M N-cacodylate
buffer (pH 7.4).
Predicting susceptibility
We modified an in vitro plasma incubation technique previous used to determine
susceptibility to the kinetoplastid hemoflagellates Cryptobia catastomi and Trypanoplasma
salmositica (Bower & Woo 1977, Wehnert & Woo 1980). The basic premise of the test
is that the plasma of susceptible hosts is relatively benign in its action on the
flagellates, whereas plasma from resistant hosts is damaging, resulting in lysis and or
cytotoxicity.
Our initial studies were aimed at protocol development, and determination of
parameters indicative of between-species differences in susceptibility to S. salmonis. We
used rainbow trout as the susceptible host, and carp Cyprinus carpio and Atlantic
sturgeon Acipenser sturio as resistant hosts (Cheng 2006). A 384-well tissue culture plate
was used for our tests. The wells were loaded with culture medium, fresh plasma was
added in 1:2 serial dilution (and tested from 1:4 to 1:2,048), and known numbers of
trophozoites were added. Control wells contained medium and trophozoites, but no
plasma. Experiments were conducted in triplicate. After setting up the inoculation,
wells were examined at 5, 30, 60 and 120 minutes, and lysis and cytotoxicity were
recorded (assessed as killed or missing cells and abnormal movement respectively).
3.4.4.3
Results
Characterisation
The pyriform trophozoite had a tapered posterior end, bearing a small caudal
projection between the emerging posterior flagella (Fig. 1A - C); occassionally a
vacuole was seen discharging through the surface (Fig. 1A). Bands of microtubules
radiated out from around the flagellar pocket, lobed nuclei were intertwined, and there
was a region of dense free ribosomes at the posterior end of the body. The ssu rRNA
gene sequence clearly distinguished S. salmonis from three other Spironucleus species
from fish, and a 1405 bp sequence used for phylogenetic analysis showed S. salmonis
was a sister taxon to S. vortens (Saghari Fard et al. 2007). The diplomonads were at
significantly higher occurrence and density in the pyloric region of the intestine than
elsewhere. However microhabitat preference was not closely related to the pH profile
(Weisheit 2004).
134
C
B
Fig. 1: Scanning electron micrographs of trophozoites of Spironucleus salmonis from
rainbow trout Oncorhynchus mykiss. A. Unadorned body surface (an important diagnostic
feature), the dark circular area is a discharging digestive vacuole. B. Tapered posterior of
body. C. A species-specific feature, the small projection between the two emerging posterior
flagella (from Saghari Fard et al. 2007).
Life cycle studies
Transformation of individual swimming trophozoites into colonies of immobile cysts
could occur very rapidly. The process began by the flagella of trophozoites attaching
to digesta or to each other (Fig. 2A), and ended with large aggregations or colonies of
encysted flagellates (Fig. 2B). The attaching trophozoites changed their shape from
pyriform to spherical, flagella could no longer be seen, and a cyst wall was formed.
A
B
Fig. 2: Attachment, colony formation and encystment of Spironucleus salmonis. A. Single
trophozoite recently attached to digesta; note that typical pyriform shape is retained. B.
Colony, note that the cells have changed shape from pyriform to spherical. Colony has
approximately 15 cells.
Integration of ten different parameters was investigated, and led to the development of
a successful protocol for quantifying lysis and cytotoxicity (Cheng 2006). The survival
of the trophozoites generally decreased with plasma concentration increase, and with
duration of the incubation, for each of the three fish species. Data is shown for
rainbow trout in Fig. 3. For determining the harmful effects of the plasma on the
© IGB 2007
135
trophozoites, a combination of three criteria were considered: lysis (lytic titre),
cytotoxicity, and time that the trophozoites remained alive in the plasma incubation.
Preliminary data showed that plasma from sturgeon was more harmful to the
trophozoites than was plasma from carp or rainbow trout, and that the trophzoites
survived for the longest time in plasma from rainbow trout.
1.0
Survival of trophozoites
0.8
control
1:8
1:32
1:128
1:512
0.6
0.4
0.2
0.0
5
30
60
120
Time post inoculation (min)
Fig. 3: Changes in survival of trophozoites in different plasma concentrations and at different
times (rainbow trout, preliminary data). A survival score of 1.0 indicates that all the
trophozoites survived. (From Cheng 2006)
3.4.4.4.
Discussions
Characterisation
Our ultrastructural studies provided the first accurate identification of the genus and
species of the diplomonad infecting rainbow trout in Germany (Saghari Fard et al.,
2007). We observed a novel feature of taxonomic significance, namely the small caudal
projection, and also proposed some new aspects of functional morphology based on
the intertwined and multi-lobed apices of the nuclei. Recognition of the distinct
sequence of the ssu rRNA gene, confirms the importance of the complimentary
molecular approach to taxonomy of diplomonads, and provides valuable information
for development of molecular probes for diagnosis. Our study of the microhabitat
preference and pH is the first to investigate physiochemical factors and microhabitat
of piscine diplomonads.
Life cycle
We were able to observe the transformation of trophozoites to cysts in vitro, and
believe that this is a good model for studying what happens in vivo, since cysts have
been reported for S. salmonis (Moore 1922, Davis 1926), and colonies of cysts are
known for other diplomonads (Wood & Smith 2005). Identification of the
environmental triggers prompting the transformation (presumably encountered in vivo
when the trophozoites pass from the fish into the water), would be an important next
step in understanding the process, and may lead to recognition of new targets for
treatments based on inhibition of encystment. This would be an important new
approach, since present treatments target the trophozoites in the fish, rather than the
cysts which transmit the infection.
136
We have successfully modified a plasma incubation test originally devised for
kinetoplastids in the blood (Bower & Woo 1977, Wehnert & Woo 1980) for a new
application with diplomonad flagellates from the lumen of the intestine.
Demonstration of the dose-response effect of the plasma was an essential prerequisite
to further development of the plasma incubation test. Our preliminary data on
between-species susceptibility shows promise, since our plasma incubation tests
suggest the same patterns of susceptibility to S. salmonis as seen from epizootiological
data. Further development of our new test will involve testing large numbers of
individual fish of different species, and naive and exposed individuals of the most
susceptible species, the rainbow trout. Exploration of the mechanisms of the innate
immunity that are manifest in the test is also planned.
Recommendations
Recognition of distinct sequences in the ssu rRNA gene offers the possibility for
development of molecular probes for different piscine diplomonad species, which
could supplement ultrastructural diagnosis, and would be more accurate. Development
of new treatments can include agents that inhibit the transformation of trophozoites
to resistant cysts, thus offering a crucial alternative to the present situation, where the
effective treatment against trophozoites is not permitted for use in many countries.
Development of the plasma incubation test holds considerable promise for predicting
host susceptibility to S. salmonis, and would be a cheaper and less expensive approach
than the present tests, which require experimental infections.
Acknowledgement
We are pleased to thank Mr. Matthias Kunow, Fisherman, for assistance with
collecting rainbow trout and maintaining them at the Leibniz-Institute of Freshwater
Ecology and Inland Fisheries, Berlin (IGB). Ms. Anorte Marko (Molecular
Parasitology, Humboldt University, Berlin) graciously undertook initial sample
processing of electron microscopy samples. Mr. Michael Delannoy from Johns
Hopkins University, School of Medicine, Baltimore, and Ms. Else Engeland from the
National Veterinary Institute, Oslo also processed some TEM samples. For our
ultrastructure and molecular investigations, we were most fortunate to have had the
assistance of Dr. Erik Sterud, of the National Veterinary Institute in Oslo. We also
thank Ms. Magdalena Sieber and Ms. Ute Hentschel from IGB, and Ms. Cathy Rada of
the Department of Molecular and Comparative Pathobiology, Johns Hopkins
University School of Medicine, Baltimore, for their assistance with obtaining literature
for us. We are grateful to our colleagues from IGB: Prof. Werner Kloas for support,
Dr. Klaus Kohlmann for advice on the molecular aspects of the study, and Mr. Jörn
Gessner for providing blood samples from sturgeon. We gratefully acknowledge the
Nachwuchsförderung des Landes Berlin (NaFöG) for the award of a Ph.D.
scholarship to Mr. M. Reza Saghari Fard, the Amt für Ausbildungsförderung for Bafög
to Ms. Claudia Weisheit, and the Deutsche Forschungsgemeinschaft for the award of a
Mercator Visiting Professorship to Dr. Sarah Poynton.
© IGB 2007
137
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Trans. Amer. Fish. Soc., 94, 53-61.
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© IGB 2007
139
OGUNJI, J., SUTTER, D., RENNERT, B., KLOAS, W., SCHULZ, C.
3.4.5 Growth performance and body composition of
carp (Cyprinus carpio) fed diets containing
housefly maggot meal (magmeal)
Wachstum und Körperzusammensetzung von Karpfen (Cyprinus
carpio) denen Futtermittel mit Fliegenmadenmehl verabreicht wurden
Key words: housefly maggot meal, fishmeal, cyprinus carpio, growth
performance
Abstract
In order to evaluate housefly maggot meal (magmeal) as feed ingredient for
carps (Cyprinus carpio) juveniles triplicate groups were fed with five
isonitrogenous feeds (crude protein: 401 – 418 g kg-1) with varying protein
sources. Fishmeal based protein content of diets was substituted with 0 (diet
C), 150 (diet A1), 450 (diet A2), 670 (diet A3), and 860 g kg-1 (diet A 4)
magmeal. Carp juveniles were fed a fixed ration at a level of 15 % body
weight in 6 portions per day. Highest individual weight gain, specific growth
rate and best feed conversion ratio were observed in carp fed diet A1
followed by fish fed diet A2 and diet C without any significant differences.
Higher magmeal inclusion in diets A3 and A4 decreased fish growth
performance significantly and also the body lipid concentration. Dietary
inclusion of magmeal up to the level of 450 g kg-1 would improve optimal
growth performance of carp. In such a combination magmeal is able to
supply above 50 % crude protein needed in the carp diet.
Zusammenfassung
Kommerzielles Fischfutter basiert im Allgemeinen auf Fischmehl als
Proteinquelle. Jedoch ist Fischmehl eine teure und wenig umweltfreundliche
Proteinquelle. Deshalb wird nach Alternativen gesucht. Eine davon könnte
Fliegenmadenmehl sein. Ziel der Untersuchungen war, Fliegenmadenmehl
als Bestandteil im Futter für junge Karpfen (Cyprinus carpio)zu testen. Dazu
wurden junge Karpfen in jeweils drei Wiederholungen mit fünf Futtermitteln
gefüttert, die nahezu gleiche Proteingehalte (401- 418 g kg-1) von
unterschiedlichen Proteinquellen aufwiesen. Der Fischmehlanteil wurde im
Futter A1 durch 150 g kg-1, in Futter A2 durch 450 g kg-1, in Futter A3 durch
670 g kg-1 und in Futter A4 durch 860 g kg-1 Fliegenmadenmehl ersetzt.
Futter C enthielt kein Fliegenmadenmehl und diente als Kontrolle. Den
Karpfen wurden täglich Futtermengen in Höhe von 15 % ihrer Körpermasse
in 6 Portionen verabreicht. Den besten Zuwachs, die höchste spezifische
Wachstumsrate und den niedrigsten Futteraufwand wies Futter A1 auf. Es
folgten die Futtermittel A2 und C. Die Unterschiede waren statistisch nicht
signifikant. Höhere Anteile an Fliegenmadenmehl in den Futtermitteln A3
und A4 verringerten das Wachstum der Karpfen signifikant. Der
Körperfettgehlt nahm ebenfalls ab. Es wird geschlussfolgert, dass ein Anteil
140
des Fliegenmadenmehls bis zu 450 g kg-1 das Wachstum der Karpfen
verbessert. So können über 50 % des Rohproteins im Karpfenfutter aus
Fliegenmadenmehl abgedeckt werden.
3.4.5.1
Introduction
Commercial aqua feed has been traditionally based on fish meal as a main
protein source due to its high protein content and balanced amino acid
profile. In addition to its excellent supply of essential fatty acid (EFA),
mineral and vitamins (Tacon 1993) fishmeal is also very palatable and highly
digestible to most fresh water and marine fishes (Watanabe et al. 1997).
Rapid increase in aquaculture industry all over the world demands fish meal
in greatly higher quantity. Although the production of fish meal and fish oil
remained constant over the last two decades at around 6200 – 7000 t/a
relative amount used in fishfeed increased from 15 % in 1980 up to 43 % in
2002 (FAO 2002). These facts have made fish meal an expensive protein
source for feed formulation in aquaculture (El-Sayed et al. 2000). As a
consequence alternative protein sources for aquaculture fish food are being
sought after.
Housefly maggot meal (magmeal) as a protein source in fish diets has
been evaluated in tilapia and catfish species respectively (Adesulu &
Mustapha, 2000; Fasakin et al. 2003; Ajani et al. 2004). No trial so far has
been reported with carp. It has been shown that magmeal is of high
biological value and that the percentage of crude protein ranges from 40 to
61.4 % dry matter (dm). It is also rich in phosphorus, trace elements and B
complex vitamins (Teotia & Miller, 1973; Spinelli et al. 1979; Ajani et al.
2004). Examination of the comparative amino acid profiles of fish and fly
larvae protein showed that no essential amino acid was limiting (Spinelli et al.
1979). Ajani et al. (2004) and Fashina-Bombata & Balogun (1997) reported
that magmeal can replace up to 100 percent of fish meal in the diets of Nile
tilapia (Oreochromis niloticus).
The objective of this study is to assess the growth performance and body
composition of carp (Cyprinus carpio) fed diets containing housefly maggot
meal (magmeal).
3.4.5.2
Culture system
Experimental fish were reared in two recirculation systems each comprising
of nine tanks (individual volume: 28 x 28 x 51.5 cm) and a filtration unit with
a sedimentation chamber for settlement of particulate matter and a biological
filter. Mean and standard deviation (±) of water temperature, pH, and O2content (measured with WTW multi 340 I, Weilheim, Germany) during the
experiment were similar in all recirculation systems: 25.95 °C (± 0.52, System
A), 25.95 °C (± 0.52, System B), 25.95 °C (± 0.52, System C); 7.66 (± 0.42),
7.57 (± 0.48), 7.65 (± 0.35) and 8.46 mg l-1 (± 1.19), 8.55 mg l-1 (± 0.94), 8.51
mg l-1 (± 0.79). The average concentration of total ammonia during the
experiment was 0.25 mg l-1.
© IGB 2007
141
Experimental diets
Formulation and chemical composition of experimental diets are shown in
Table 1 and 2. Five isonitrogenous diets were formulated to yield a content
of around 41 % crude protein dry mattter (dm) using fishmeal and magmeal
as major dietary protein sources. Fishmeal concentration in the diets
decreased with increasing concentration of magmeal. Diet C, formulated
with the highest inclusion level of fish meal and without magmeal served as
the control. Though 10 g kg-1 of chromic oxide was included in all diets, no
fish faeces were collected for digestibility determination as it was initially
planned. Silicate gel was used to balance the nutrient content of the diets. All
dry diet components, including vitamin and mineral mixture, were
thoroughly mixed with oil. Water was added and the feed pressed into pellets
of 1 mm diameter. The wet pellets were dried for 3 days at room
temperature and stored at -2 °C until used.
Table 1: Ingredients used for experimental diet formulation [g kg-1]
Diets
Feed Stuff
1
C
A1
A2
A3
A4
FishMeal
620
520
300
150
-
Magmeal
-
150
450
670
860
Soymeal
-
-
-
-
-
Wheat Flour
160
150
130
100
100
Fish Oil
70
60
30
-
-
Canola Oil
80
60
30
20
10
Vit./Min Mix 2
20
20
20
20
20
Silicate gel
40
30
30
30
-
Chromic Oxide
10
10
10
10
10
1
C = Control; 2Vitamin and Mineral mix (Spezialfutter Neuruppin - VM BM 55/13 Nr. 7318) supplied
per 100 g of dry feed : Vitamin A 12000 I.E; Vitamin D3 1600 I.E; Vitamin E 160 mg; Vitamin K3 6.4
mg; Vitamin B1 12 mg; Vitamin B2 16 mg; Vitamin B6 12 mg Vitamin B12 26.4 mg; Nicotinic acid
120 mg; Biotin 800 mg; Folic acid 4.8 mg; Pantothenic acid 40 mg, Inositol 240 mg; Vitamin C 160
mg; Antioxidants (BHT) 120 mg; Iron 100 mg; Zink 24 mg; Manganese 16 mg; Cobalt 0.8 mg; Iodine
1.6 mg; Selenium 0.08 mg
Experimental fishes and feeding trial
Experimental fish were obtained from Warmwasserfischzucht Jäntschwalde,
three days after hatching. They were brought to the facilities of Institute of
Freshwater Ecology and Inland Fisheries Berlin Germany, where the carps
were reared and acclimatized for six weeks. Prior to the commencement of
growth trial, ten carps each with an initial average body weight of 0.74 g were
randomly distributed in fifteen tanks. Experimental diets were assigned to
the carps in triplicate tanks respectively in a way that all feeding groups were
represented in the two recirculation systems evenly. The fish were given
restricted ration at a level of 15 % body weight in 6 portions at 8.00, 10.00,
12.00, 14.00, 16.00, 17.30 hours respectively per day. Bryant & Matty (1981)
suggested that carp fry (100 mg to 3g) required 10 – 15 % body weight per
142
day for optimum growth at water temperatures of 24 °C. This feeding level
was reduced to 10 % body weight after three weeks when fish failed to
consume their total ration. The fish were weighed every two weeks and
quantity of food adjusted accordingly. Experimental tanks were cleaned
regularly, and the trial lasted for 43 days (Molnar et al. 2006).
Sample collection
At the end of the experiment, four fish from each tank were randomly taken.
The fish were weighed before the length of each fish was taken and liver
excised and weighed. The rest 6 fish in all the tanks respectively were killed,
individually weighed and measured before they were homogenised and
freeze dried at a temperature of – 54 °C. Twenty fish samples sacrificed and
homogenised at the beginning of the experiment were also freeze dried
before being analysed for initial whole body composition.
Table 2: Proximate nutritional and amino acid composition (g kg-1 dry matter) of experimental diets,
values are means of duplicate determinations.
Proximate composition
Diets
C
A1
A2
A3
A4
Dry Matter (Dm)
953
951
954
945
927
Crude protein (Cp)
417
418
410
411
401
Crude lipid (Cl)
205
215
217
219
255
Crude ash
181
170
163
160
126
NFE 1
198
197
210
210
218
Gross Energy (MJ kg-1) 2
21.61
22.01
22.13
22.24
23.57
P/E ratio 3
19.30
18.99
18.53
18.48
17.01
Alanine
47.1
47.0
45.8
37.8
38.2
Arginine*
25.2
29.2
26.1
25.8
28.2
Aspartic acid
34.2
63.5
65.1
58.1
62.1
Glutamic acid
122.1
123.0
119.7
98.4
103.2
Histidine*
23.3
21.0
30.2
25.2
30.8
Isoleucine*
33.1
32.7
33.4
28.3
29.5
Leucine*
16.9
18.5
16.8
14.1
14.4
Lysine *
25.7
26.8
26.4
22.0
23.4
Phenylalanine*
36.1
34.5
40.7
39.9
44.7
Serine
26.4
26.8
26.2
21.4
21.8
Taurine
12.8
13.4
10.9
13.7
10.6
Threonine*
18.0
19.0
19.3
13.3
14.0
Tryptophan*
2.2
2.9
1.9
3.0
1.6
Tyrosine
4.4
2.4
3.5
3.6
4.5
Valine*
28.3
28.1
29.9
25.9
27.7
Total
455.80
488.80
495.90
430.50
454.70
Amino Acids
1
Nitrogen free extract + fibre, (NFE) = 100 - (% protein + % fat + % ash); 2Calculated by: Crude
protein = 23.9 MJ kg-1 Crude lipids = 39.8 MJ kg-1, NFE = MJ kg-1 (Schulz et al., 2005); 3P/E = Protein
to energy ratio in g protein / MJ gross energy; *Essential amino acids
© IGB 2007
143
Chemical analysis
The freeze-dried samples of fish and experimental diets were analyzed for
proximate composition. Every analysis was carried out in duplicate and fish
samples per tank. Protein (N x 6.25) was analysed using a Kjeltec System
(Tecator) and crude fat using a Soxtec System HT (Tecator) with petroleum
ether as the solvent. Ash was determined by burning in a muffle furnace at
550 °C for 10 hours. Gross energy was calculated using the following values:
crude protein = 23.9 kJ g-1, crude lipids = 39.8 kJ g-1 and NFE = 17.6 kJ g-1
(Schulz et al. 2005). To estimate the amino acid concentrations of the
experimental diets, 5 mg of the freeze-dried samples were hydrolyzed with
6N HCl at 110 °C for 24 hours. No protecting reagents were added to avoid
destruction of sulphur amino acids that methionine values determined were
very insignificant and are not reported here. Other analytical procedures for
amino acids followed the description of Ogunji & Wirth (2001).
Statistical analysis
All data were subjected to one-way analysis of variance (ANOVA). The
significance of difference between means was determined by Duncan’s
multiple range test (P < 0.05) using SPSS for Windows (Version 12). Values
are expressed as means ± SE.
3.4.5.3
Results
Growth performance and food utilisation
The effect of magmeal diets on growth performance and feed utilisation of
Cyprinus carpio are shown in Table 3. During the experiment no mortality was
recorded. Reduction of fishmeal from 620 g kg-1 (supplying 411.7 g kg-1
crude protein) in control diet to 530 g kg-1 (supplying 351.9 g kg-1 crude
protein) and 300 g kg-1 (supplying 199.2 g kg-1 crude protein) respectively, by
substituting with 150 g kg-1 magmeal (supplying 69.8 g kg-1 crude protein) in
diet A1 and 450 g kg-1 magmeal (supplying 209.52 g kg-1 crude protein) in
diet A2 improved final fish weight gain, specific growth rate (SGR), food
conversion ratio (FCR) and hepatosomatic index (HIS), but no significant
differences were observed (p> 0.05). No significant differences in FCR and
HIS were also observed when magmeal was included in the carp diet at a
level of 670 g kg-1 (supplying 312 g kg-1 crude protein) to diet A3. At this
level however SGR decreased significantly. Diet A4 with magmeal as sole
protein source yielded a significant lowest fish growth performance. Fish fed
control diet recorded the highest condition factor (Cf 1.76).
144
Table 3: Mean and standard error (±) of growth performance parameter of Cyprinus carpio fed
experimental diets; values are mean of triplicate feeding groups; within each line values with different
superscript letter differ significantly (p< 0.05).
Parameters
Diets
C
A2
A3
A4
Initial weight (g)
0.73±0.01
a
0.73±0.01a
0.74±0.01a
0.75±0.01a
Final weight (g)
7.90±0.36ab 9.44±0.55a
8.59±0.66a
6.35±0.53ab 4.38±0.28c
Weight gain (g)
7.17±0.09ab 8.70±0.54a
7.86±0.63a
5.60±0.63b
3.63±0.37c
Diet fed (g fish -1 )
9.57±0.13a
10.49±0.35a 9.76±0.49a
8.32±0.44b
6.99±0.25c
b
2.15±0.08c
1.96±0.18b
SGR
1
A1
2.79±0.02
a
a
0.75±0.01
2.92±0.05
a
2.87±0.07
a
2.53±0.07
FCR2
1.34±0.02a
1.21±0.04a
1.25±0.04a
1.50±0.08a
HSI 3
2.52±0.14a
2.40±0.10a
2.15±0.14a
2.31±0.12a
2.47±0.21a
Cf 4
1.76±0.02a
1.69±0.03a
1.61±0.02b
1.56±0.02b
1.59±0.04b
Survival (%)
100
100
100
100
100
1
Specific growth rate (% day-1) = (InW 2 - InW1/ T2 -T1) × 100
2
Food conversion ratio = total diet fed (g)/live weight gain (g);
3
Hepatosomatic Index = [liver weight (g)/total fish weight (g)] * 100, based on a sub-sample of n = 12
per experimental group
3
Condition factor = W2 * L2 -3 * 100
(L = total length)
Body composition
Whole body crude protein, crude lipid and crude ash content increased in all
experimental groups when compared to the initial status (Table 4). The crude
protein varied between 131.6 g kg-1 (A4) and 133.6 g kg-1 (A3) without
significant differences (p> 0.05) between all feeding groups. Carps fed
control and A1 diets recorded highest body crude fats which decreased
significantly with increasing dietary magmeal inclusion. Ash concentration in
carps fed diet C (19.3 g kg-1) was significantly lower than in other groups (p<
0.05). No significant difference in body ash contents was observed between
fish fed diet A1 to A4 (P < 0.05).
Table 4: Mean and standard error (±) of initial and final composition of carp (whole fish) fed
experimental diets; values are expressed as g kg
-1
of original matter (o.m.); within each line values
with different superscript letter differ significantly (p<0.05).
Components
Initial status
3.4.5.4
C
Diets
A2
A1
a
A3
A4
a
Moisture
824.5±0.03 730.9±0.34 734.0±0.31 754.8±0.09b 767.5±0.11c 767.7±0.37 c
Crude protein
118.5±0.01 133.2±0.09a 132.4±0.20a 132.8±0.14a 133.6±0.10a 131.6±0.08a
Crude lipid
24.3±0.02
a
a
b
106.9±0.35 100.7±0.20 79.3±0.08
Crude ash
19.3±0.00
19.3±0.07
NFE
13.5±0.00
9.7±0.15a
a
21.8±0.10
b
11.2±0.09a
21.3±0.06
b
11.8±0.08a
63.3±0.07c
68.2±0.33c
b
22.5±0.04b
12.8±0.10a
10.0±0.08a
22.7±0.24
Discussion
In this study a complete replacement of fishmeal with magmeal in carp diet
(diet A4) adversely affected growth performance (SGR 2.15; FCR 1.96)
compared to the control. In contrast 100 % replacement has been reported
for tilapia Oreochromis niloticus without any growth inhibition (Ajani et al. 2004
Fashina-Bombata & Balogun 1997). Since the amino acid dietary
composition meets the requirement for carp, such reduced growth
© IGB 2007
145
performance when magmeal completely substitute fishmeal may be due to
inefficient utilisation of magmeal protein by carp resulting from low
digestibility. Magmeal used for diet formulation contained an acid detergent
fibre (ADF) concentration of 137.8 g kg-1. Most fish can tolerate up to 8 %
fibre in their diets, but higher concentrations (8 to 30 %) depress growth
(Edwards et al. 1977, Hilton et al. 1983, Poston 1986). According to Schwarz
& Kirchgeßner (1982) carp is not able to digest fibre. Fasakin et al. (2003)
reported that the reduction in growth performance of African catfish fed
full–fat maggot meal may be, among other reasons due to low protein
digestibility of magmeal.
The weight gain and SGR of carp improved as fish meal was replaced in
experimental diets with magmeal up to an incorporation level of 450 g kg-1
(diet A2). There seem to be a form of nutrient fortification when fishmeal is
combined with magmeal in the diet of carp up to a certain level. It is
however; unclear the particular nutrients that were improved giving the fact
that the dietary amino acid composition seem similar (Table 2). Adesulu &
Mustapha (2000) reported that the levels of some essential amino acids in
magmeal were higher than that in fish meal and soybean meal. Examination
of the comparative amino acid profiles of fishmeal and fly larvae protein in
rainbow trout showed that no essential amino acid was limiting (Spinelli et al.
1979). The condition factor (Cf 1.76) of carps fed control diet in this study
however, was highest though not significantly different from diet A1.
Fishmeal is considered the most desirable animal protein ingredient in
aquaculture diets (Muzinic et al. 2006). Yerli & Zengin (1996) reported a
condition factors for the total, male and female of C. carpio between 1.45 –
2.08 and 1.74 – 2.47 respectively. Balik et al. (2004) determined that the
condition factor of both sexes of silver crucian carp increased gradually with
age.
The FCR of carps fed diets A1 – A3 containing various percentages of
magmeal were not significantly different, ranging from 1.21 (diet A1) to 1.50
(diet A3). De Silva & Anderson (1995) suggested that low FCR values
indicate an improved feed outcome. Values as low as 1.0 have been reported
although, generally they range between 1.2 and 1.5 for fish fed carefully
prepared diets. As such incorporation of magmeal in carp diets, above the
level 450 g kg-1 (supplying 209.5 g kg-1 dietary protein) (diet A2; FCR 1.25)
and below 670 g kg-1 (supplying 312 g kg-1 dietary protein) (diet A3; FCR
1.5) would seem to enhance optimal growth performance of carp and
provide outstanding economic advantage. This may allow for less expensive
diet formulations for carps and reduce diet cost for producers, thereby
increasing profitability. According to Fashina-Bombata and Balogun (1997)
the replacement of fish meal by magmeal is economically feasible. The cost
of harvesting and processing one kilogramme of magmeal is less than 20 %
of cost of 1 kilogramme of fish meal.
Whole body analysis shows that the level of magmeal in the experimental
diets did not influence the HSI. The HSI in all feeding groups was not
significantly different indicating that the proportion of lipid and
carbohydrate incorporated into all experimental diets was optimal for carp
146
utilisation. Hemre et al (1989) suggested that fish even convert carbohydrate
to lipid which are stored in the liver and thus affect the liver index.
In this study the dietary lipid content (205 g kg-1; diet C – 255 g kg-1; diet
A4) increased with elevated magmeal incorporation due to the high
concentration of lipid in magmeal (258.2 g kg-1). The whole body moisture
composition increased with increasing dietary lipid while the body crude lipid
decreased. In contrast, Weathrup et al. (1997) and Ozoria et al. (2006)
observed increased lipid deposition in fish body when fed diets containing
high lipid content. The low body crude lipid of fish fed diet A3 and A4 in
this study may be attributed to the effect of low protein to energy ratio of
the two diets since higher amount of energy per gram protein will normally
result in lipid incorporation. The dietary lipid may have been used as energy
source.
Acknowledgement
The authors are grateful to the Alexander von Humboldt Foundation (AvH)
Germany, for the award of a Post Doctoral Research Fellowship under
which this work was performed and also are highly indebted to Frau Dr. C.
Kijora of Institute of Animal Science, Humboldt-Universität zu Berlin for
allowing us run the protein analysis in her laboratory.
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MEHNER, T. (2006): Individual variability of diel vertical migrations in
European vendace (Coregonus albula) explored by stationary vertical
hydroacoustics. Ecology of Freshwater Fish, 15, 146-153.
MEHNER, T. (2006): Prediction of hydroacoustic target strength of vendace
(Coregonus albula) from concurrent trawl catches. Fisheries Research,
79, 162-169.
MEMIS, D., KOHLMANN, K. (2006): Genetic characterization of wild
common carp (Cyprinus carpio L.) from Turkey. Aquaculture, 258, 257262.
METCALF, J. S., MORRISON, L. F., KRIENITZ, L., BALLOT, A., KRAUSE, E.,
KOTUT, K., PÜTZ, S., WIEGAND, C., PFLUGMACHER, S., CODD, G. A.
(2006): Analysis of the cyanotoxins anatoxin-a and microcystins in
Lesser Flamingo feathers. Toxicological & Environmental Chemistry,
88(1), 159-167.
NOLTE, A., FREYHOF, J., TAUTZ, D. (2006): When invaders meet locally
adapted types: rapid moulding of hybrid zones between two species of
sculpins (Cottus, Pisces). Molecular Ecology, 15, 1983-1989.
OEHLMANN, J., SCHULTE-OEHLMANN, U., BACHMANN, J., OETKEN, M.,
LUTZ, I., KLOAS, W., TERNES, T. (2006): Bisphenol A induces
superfeminization in the ramshorn snail Marisa cornuarietis
(Gastropoda: Prosobranchia) at environmentally relevant concentrations.
Environmental Health Perspectives, 114, 127-133.
OHLBERGER, J., STAAKS, G., HÖLKER, F. (2006): Swimming efficiency and
the influence of morphology on swimming costs in fishes. Journal of
Comparative Physiology B - Biochemical Systemic and Environmental
Physiology, 176, 17-25.
OPITZ, R., HARTMANN, S., BLANK, T., BRAUNBECK, T., LUTZ, I., KLOAS, W.
(2006): Evaluation of histological and molecular endpoints for enhanced
detection of thyroid system disruption in Xenopus laevis tadpoles.
Toxicological Sciences, 90, 337-348.
OPITZ, R., TRUBIROHA, A., LORENZ, C., LUTZ, I., HARTMANN, S., BLANK,
T., BRAUNBECK, T., KLOAS, W. (2006): Expression of sodium-iodide
symporter mRNA in the thyroid gland of Xenopus laevis tadpoles:
developmental expression, effects of antithyroidal compounds, and
regulation by TSH. Journal of Endocrinology, 190(1), 157-170.
OPITZ, R., LUTZ, I., NGUYEN, N., SCANLAN, T., KLOAS, W. (2006): Analysis
of thyroid hormone receptor betaA mRNA expression in Xenopus laevis
tadpoles as a means to detect agonism and antagonism of thyroid
hormone action. Toxicology and Applied Pharmacology, 212, 1-13.
PAUL, A., STÖSSER, R., ZEHL, A., ZWIRNMANN, E., STEINBERG, C. E. W.
(2006): Nature and abundance of organic radicals in natural organic
156
matter: Effect of sample pH and irradiation. Environmental Science &
Technology, 40, 5897-5903.
PENNING, H., CASPER, P., CONRAD, R. (2006): Carbon isotope fractionation
during acetoclastic methanogenesis ny Methanosaeta concilii in culture
and a lake sediment. Applied and Environmental Microbiology, 72,
5648-5652.
PFLUGMACHER, S., PIETSCH, C., RIEGER, W., STEINBERG, C. E. W. (2006):
Dissolved natural organic matter (NOM) impacts photosynthetic oxygen
production and electron transport in coontail Ceratophyllum demersum .
Science of the Total Environment, 357, 169-175.
PFLUGMACHER, S., JUNG, K., LUNDVALL, L., NEUMANN, S., PEUTHERT, A.
(2006): Effects of cyanobacterial toxins and cyanobacterial cell-free
crude extract on germination of Alfalfa (Medicago sativa) and induction
of oxidative stress. Environmental Toxicology and Chemistry, 25, 23812387.
PFÜTZNER, B., MEY, S., SCHEFFLER, E., NÜTZMANN, G. (2006): A modelbased analysis of the basin water balance in a catchment in the north-east
of Berlin, Germany. Hydrologie und Wasserbewirtschaftung, 50, 12-19.
PIETSCH, C., KRAUSE, E., BURNISON, B. K., STEINBERG, C. E. W.,
PFLUGMACHER, S. (2006): Effects and metabolism of the phenylurea
herbicide isoproturon in the submerged macrophyte Ceratophyllum
demersum L. Journal of Applied Botany and Food Quality-Angewandte
Botanik, 80, 25-31.
POYNTON, S. L. (2006): Regional Review on Aquaculture Development. 2.
Near East and North Africa - 2005. FAO Fisheries Circular, 1017,2, 179.
PREUßEL, K., STÜKEN, A., WIEDNER, C., CHORUS, I., FASTNER, J. (2006):
First report on cylindrospermopsin producing Aphanizomenon flosaquae (Cyanobacteria) isolated from two German lakes. Toxicon, 47,
156-162.
SCHAUSER, I., CHORUS, I., LEWANDOWSKI, J. (2006): Effects of nitrate on
phosphorus release: comparison of two Berlin lakes. Acta Hydrochimica
et Hydrobiologica, 34, 325-332.
SCHAUSER, I., HUPFER, M., BRÜGGEMANN, R. (2006): Process analysis with
a phosphorus diagenesis model (SPIEL). Ecological Modelling, 190, 8798.
SCHMIDT, K., PFLUGMACHER, S., STAAKS, G., STEINBERG, C. E. W. (2006):
The influence of tributyltin chloride and polychlorinated biphenyls on
swimming behavior, body growth, reproduction, and activity of
biotransformation enzymes in Daphnia magna. Journal of Freshwater
Ecology, 21, 109-120.
SCHULTE-OEHLMANN, U., ALBANIS, T., ALLERA, A., BACHMANN, J.,
BERNTSSON, P., BERESFORD, N., CARNEVALI, D., CICERI, F., DAGNAC,
T., FALANDYSZ, J., GALASSI, S., HALA, D., JANER, G., JEANNOT, R.,
JOBLING, S., KING, I., KLINGMÜLLER, D., KLOAS, W., KUSK, O.,
LEVADA, R., LO, S., LUTZ, I., OEHLMANN, J., OREDSSON, S., PORTE, C.,
RAND-WEAVER, M., SAKKAS, V., SUGNI, M., TYLER, C., VAN AERLE, R.,
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BALLEGOOY, C., WOLLENBERGER, L. (2006): COMPRENDO:
Focus and approach. Environmental Health Perspectives, 114, 98-100.
SCHULZ, C., GÜNTHER, S., WIRTH, M., RENNERT, B. (2006): Groth
performance and body composition of pike perch (Sander lucioperca)
fed varying formulated and natural diets. Aquaculture International, 14,
577-586.
SCHULZ, M., KÖHLER, J. (2006): A simple model of phosphorus retention
evoked by submerged macrophytes in lowland rivers. Hydrobiologia,
563, 521-525.
SCHULZ, M., FREYHOF, J., SAINT-LAURENT, R., OSTBYE, K., MEHNER, T.,
BERNATCHEZ, L. (2006): Evidence for independent origin of two springspawning ciscoes in Germany (Salmoniformes: Coregonidae). Journal of
Fish Biology, 68 (Suppl A), 119-135.
SCHULZE, T., BAADE, U., DÖRNER, H., ECKMANN, R., HAERTEL-BORER, S.,
HÖLKER, F., MEHNER, T. (2006): Response of the residential fish
community to introduction of a new predator type in a mesotrophic lake.
Canadian Journal of Fisheries and Aquatic Sciences, 63, 2202-2212.
SCHULZE, T., DÖRNER, H., HÖLKER, F., MEHNER, T. (2006): Determinants
of habitat choice in a large planktivorous fish. Journal of Fish Biology,
69, 1136-1150.
SINDILARIU, P.-D., FREYHOF, J., WOLTER, C. (2006): Habitat use of juvenile
fish in the lower Danube and the Danube Delta: implications for
ecotone connectivity. Hydrobiologia, 571, 51-61.
SLECHTOVA, V., BOHLEN, J., FREYHOF, J., RAB, P. (2006): Molecular
phylogeny of the Southeast Asian freshwater fish family Botiidae
(Teleostei: Cobitoidea) and the origin of polyploidisation in their
evolution. Molecular Phylogenetics and Evolution, 39, 529-541.
STEINBERG, C. E. W., KAMARA, S., PROKHOTSKAYA, V., MANUSADZIANAS,
L., KARASYOVA, T., TIMOFEYEV, M., JIE, Z., PAUL, A., MEINELT, T.,
FARJALLA, V., MATSUO, A., BURNISON, K., MENZEL, R. (2006):
Dissolved humic substances – ecological driving forces from the
individual to the ecosystem level? Freshwater Biology, 51, 1189-1210.
STELBRINK, B., FREYHOF, J. (2006): Reduction of scales and head canals in
Pomatoschistus canestrinii (Ninni, 1883) (Teleostei, Gobiidae).
Verhandlungen der Gesellschaft für Ichthyologie, 5, 71-77.
STIEF, P., HÖLKER, F. (2006): Trait-mediated indirect effect of predatory
fish on microbial mineralization in aquatic sediments. Ecology, 87, 31523159.
STÜKEN, A., RÜCKER, J., ENDRULAT, T., PREUßEL, K., HEMM, M.,
NIXDORF, B., KASTEN, U., WIEDNER, C. (2006): Distribution of three
alien cyanobacterial species (Nostocales) in Northeast Germany:
Cylindrospermopsis raciborskii, Anabaena bergii and Aphanizomenon
aphanizomenoides. Phycologia, 45, 696-703.
SUKHODOLOV, A., FEDELE, J., RHOADS, B. (2006): Structure of flow over
alluvial bedforms: an experiment on linking field and laboratory
methods. Earth Surface Processes and Landforms, 31, 1292-1310.
SURES, B., LUTZ, I., KLOAS, W. (2006): Effects of infection with Aguillicola
crassus and simultaneous exposure with Cd and 3,3`,4,4`,5VAN
158
pentachlorobiphenyl (PCB 126) on the levels of cortisol and glucose in
European eel (Anguilla anguilla). Parasitology, 132, 281-288.
TANG, K., HUTALLE, K. M., GROSSART, H.-P. (2006): Microbial abundance,
composition and enzymatic activity during decomposition of copepod
carcasses. Aquatic Microbial Ecology, 45, 219-227.
TANG, K., GROSSART, H.-P., YAM, E. M., JACKSON, G. A., DUCKLOW, H.
W., KIØRBOE, T. (2006): Mesocosm-scale study of particle dynamics and
associated microbial processes. Marine Ecology-Progress Series, 325, 1527.
TIMOFEYEV, M. A., SHATILINA, Z. M., KOLESNICHENKO, A. V.,
KOLESNICHENKO, V. V., PFLUGMACHER, S., STEINBERG, C. E. W.
(2006): Natural organic matter (NOM) promotes oxidative stress in
freshwater amphipods Gammarus lacustris Sars and Gammarus tigrinus
Sexton. Science of the Total Environment, 366, 673-681.
TOTSCHE, O., FYSON, A., STEINBERG, C. E. W. (2006): Microbial Alkalinity
Production to Prevent Reacidification of Neutralized Mining Lakes.
Mine Water and the Environment, 25, 204-213.
TOTSCHE, O., FYSON, A., STEINBERG, C. E. W. (2006): Characterization of
acidic mining lakes by titration curves. Verhandlungen - Internationale
Vereinigung für Theoretische und Angewandte Limnologie, 29, 13561358.
TOTSCHE, O., FYSON, A., KALIN, M., STEINBERG, C. E. W. (2006): Titration
Curves A Useful Instrument for Assessing the Buffer Systems of Acidic
Mining Waters. Environmental Science and Pollution Research, 13, 215224.
URBATZKA, R., LUTZ, I., OPITZ, R., KLOAS, W. (2006): Luteinizing
hormone, follicle stimulating hormone, and gonadotropin releasing
hormone mRNA expression of Xenopus laevis in response to endocrine
disrupting compounds affecting reproductive biology. General and
Comparative Endocrinology, 146, 119-125.
VOIGT, K., BRÜGGEMANN, R., PUDENZ, S. (2006): Information quality of
environmental and chemical databases exemplified by high production
volume chemicals and pharmaceuticals. Online Information Review
30[1], 8-23.
WAGNER-DÖBLER, I., THIEL, V., EBERL, L., ALLGAIER, M., BODOR, A.,
MEYER, S., EBNER, S., HENNIG, A., PUKALL, R., SCHULZ, S. (2006):
Discovery of complex mixtures of novel long-chain quorum sensing
signals in free-living and host-associated marine alphaproteobacteria.
ChemBioChem, 6, 2195-2206.
WICHELS, A., WUERTZ, S., DOEPKE, H., SCHUETT, C., GERDTS, G. (2006):
Bacterial diversity in the breadcrumb sponge Halichondria panicea
(Pallas). FEMS Microbiology Ecology, 56, 102-108.
WIESE, B., PALANCAR, M. C., ARAGON, J. M., SANCHEZ, F., GIL.R. (2006):
Modelling the Entreperias reservoir. Water Environment Research, 78,
781-791.
WILHELM, S., HINTZE, T., LIVINGSTONE, D. M., ADRIAN, R. (2006): Longterm response of daily epilimnetic temperature extrema to climate
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forcing. Canadian Journal of Fisheries and Aquatic Sciences, 63, 24672477.
WOLTER, C. (2006): First record of river gudgeon Romanogobio belingi in
the River Havel, Brandenburg, Germany. Lauterbornia, 56, 91-94.
WUERTZ, S., NITSCHE, A., GESSNER, J., KIRSCHBAUM, F., KLOAS, W. (2006):
IGF-I and its role in maturing gonads of female sterlet, Acipenser
ruthenus Linnaeus, 1758. Journal of Applied Ichthyology, 22, 346-353.
WUERTZ, S., LUTZ, I., GESSNER, J., LOESCHAU, P., HOGANS, B.,
KIRSCHBAUM, F., KLOAS, W. (2006): The influence of rearing density as
environmental stressor on cortisol response of Shortnose sturgeon
(Acipenser brevirostrum). Journal of Applied Ichthyology, 22, 269-274.
WUERTZ, S., GAILLARD, S., BARBISAN, F., CARLE, S., CONGIU, L., FORLANI,
A., AUBERT, J., KIRSCHBAUM, F., TOSI, E., ZANE, L., GRILLASCA, J.
(2006): Extensive screening of sturgeon genomes by random screening
techniques revealed no sex-specific marker. Aquaculture, 258, 685-688.
YANG, J., HE, S., FREYHOF, J., WITTE, K.-E., LIU, H. (2006): Phylogeny of
the Gobioninae inferred from complete mitochondrial cytochrome b
gene sequences (Teleostei: Cyprinidae). Hydrobiologia, 553, 255-266.
ZAK, D., KLEEBERG, A., HUPFER, M. (2006): Sulphate-mediated
phosphorus mobilization in riverine sediments at increasing sulphate
concentration, River Spree, NE Germany. Biogeochemistry, 80, 109-119.
ZIMMERMANN-TIMM, H., SCHÖNBORN, W., KOSCHEL, R. (2006): Anita
Lange - A veteran of Limnology. Limnologica, 36, 1.
160
4.2 Non-reviewed papers, books, book chapters
and reports
Artikel in nichtreferierten Zeitschriften, Bücher, Buchbeiträge und
Berichte
ARLINGHAUS, R. (2006): Der unterschätzte Angler. Kosmos Verlag,
Stuttgart, 168 S.
ARLINGHAUS, R., LEWIN, W.-C. (2006): Dokumentierte und vermutete
Auswirkungen einer intensiven Angelfischerei und Ausblick für das
Management. In: Leibniz-Institut für Gewässerökologie und
Binnenfischerei (ed.): Integrierter Gewässerschutz für Binnengewässer:
Maßnahmen zum nachhaltigen Umgang mit der Ressource Wasser.
Leibniz-Institut für Gewässerökologie und Binnenfischerei, Stechlin, 5576.
BLANK, B., MEIßNER, R., NEEF, T., STRAUCH, G., NÜTZMANN, G. (2006):
Investigating heterotrophic denitrification in shallow groundwater of the
Schaugraben catchment, NE Germany. In: KOVAR, K., HRKAL,
Z.,.BRUTHANS, J. (eds.): Hydrology and Ecology: The
Groundwater/Ecology connection, 137-140.
BRAUNS, M., HILT, S., GARCIA, X.-F., PUSCH, M., GRÜNERT, U., MISCHKE,
U., KÖHLER, J. (2006): Praxistest zur Bewertung von Makrozoobenthos,
Makrophyten und Phytoplankton in fünf Berliner Seen und einem
Fließgewässer im Rahmen der Umsetzung der EUWasserrahmenrichtlinie. Bericht im Auftrag der Senatsverwaltung für
Stadtentwicklung, 1-115.
BRÜGGEMANN, R., CARLSEN, L (eds.) (2006): Partial Order in
Environmental Sciences and Chemistry. Springer, Berlin.
BRÜGGEMANN, R., CARLSEN, L. (2006): Introduction to partial order theory
exemplified by the Evaluation of Sampling Sites. In: BRÜGGEMANN, R.,
CARLSEN, L. (eds.): Partial Order in Environmental Sciences and
Chemistry. Springer, Berlin, 61-110.
BRÜGGEMANN, R., CARLSEN, L., LERCHE, D., SØRENSEN, P. (2006): A
Comparison of Partial Order Technique with three Methods of MultiCriteria Analysis of Chemical Substances. In: BRÜGGEMANN, R.,
CARLSEN, L. (eds.): Partial Order in Environmental Sciences and
Chemistry. Springer, Berlin, 237-256.
BRÜGGEMANN, R., RESTREPO, G., VOIGT, K. (2006): Evaluation of the
Pollution State in Baden-Wuerttemberg by a Local Analysis. In:
STUDZINSKI, J., HRYNIEWICZ, O. (eds.): Development of Methods and
Technologies of Informatics for Process Modeling and Management.
Polish Academy of Sciences, Systems Research Institute, Warsaw, 121135.
BRÜGGEMANN, R., RESTREPO, G., VOIGT, K. (2006): Structure-FateRelationships of Organic Chemicals. In: VOINOV, A., JAKEMAN, A.J.,
RIZZOLO, A. E. (eds.): Proceedings of the iEMSs Third Biennial
Meeting: "Summit on Environmental Modelling and Software", 1-6.
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BRÜGGEMANN, R., SIMON, U., NÜTZMANN, G. (2006): Analyzing water
management strategies in urban regions by directed graphs. In:
STUDZINSKI, J., HRYNIEWICZ, O. (eds.): Modeling concepts and decision
support in environmental systems. Polish Academy of Sciences, Warsaw,
System research, 111-124.
BRUNKE, M. (2006): Meio- und Makrofauna der überströmten Sohle. In:
PUSCH, M., FISCHER, H. (eds.): Stoffdynamik und Habitatstruktur in der
Elbe. Weissensee, Berlin, 181-190.
BRUNKE, M. (2006): Mikrofauna. In: PUSCH, M., FISCHER, H. (eds.):
Stoffdynamik und Habitatstruktur in der Elbe. Weissensee, Berlin, 139144.
BRUNKE, M., GRAFAHREND-BELAU, E., PUSCH, M. (2006): Bedeutung von
Totholz für das Makrozoobenthos. In: PUSCH, M., FISCHER, H. (eds.):
BRUNKE, M., GUHR, H. (2006): Auswirkungen der Schifffahrt. In: PUSCH,
M., FISCHER, H. (eds.): Stoffdynamik und Habitatstruktur in der Elbe.
Weissensee, Berlin, 286-294.
BRUNKE, M., PUSCH, M. (2006): Prozesse und Biozönosen an der
überströmten Flusssohle - Einleitung. In: PUSCH, M., FISCHER, H. (eds.):
ENGELHARDT, C., GOLOSOV, S., CASPER, P., HUPFER, M., KIRILLIN, G.
(2006): Seiche-induced convection in upper sediments. In: RUEDA, F.
(ed.): Physical processes in natural waters, 59-68.
FISCHER, H., PUSCH, M. (2006): Auswirkungen wasserbaulicher Eingriffe auf
das Zoobenthos und die mikrobiellen Stoffumsetzungen. In: PUSCH, M.,
FISCHER, H. (eds.): Stoffdynamik und Habitatstruktur in der Elbe.
FISCHER, H., PUSCH, M. (2006): Überblick über die untersuchten
Flussabschnitte. In: PUSCH, M., FISCHER, H. (eds.): Stoffdynamik und
Habitatstruktur in der Elbe. Weissensee, Berlin, 27-29.
FISCHER, H., WILCZEK, S. (2006): Bakterien und deren Stoffumsetzungen.
In: PUSCH, M., FISCHER, H. (eds.): Stoffdynamik und Habitatstruktur in
der Elbe. Weissensee, Berlin, 147-154.
FISCHER, H., WILCZEK, S., BRUNKE, M. (2006): Kohlenstoffumsatz. In:
FREYHOF, J., HUCKSTORF, V. (2006): Conservation and management of
aquatic genetic resources: a critical checklist of German freshwater
fishes. Berichte des IGB, 23, 113-126.
GARCIA, X.-F., BRAUNS, M., PUSCH, M. (2006): MakrozoobenthosBesiedlung in unterschiedlichen Buhnenfeldtypen. In: PUSCH, M.,
GESSNER, J., LUDWIG, A., DIEKMANN, M. (2006): Störe: Implikationen für
Schutz und Management. Fischer & Teichwirt, 2006, 63-64.
162
GUHR, H., SCHWARTZ, R. (2006): Stoffliche Belastungen. In: PUSCH, M.,
HAMANN, E., NÜTZMANN, G. (2006): Conceptual reactive transport
modelling of a sewage water based contamination in an urban
groundwater system. In: KOVAR, K., HRKAL, Z.,.BRUTHANS, J. (eds.):
Hydrology and Ecology: The groundwater/ecology connection, 203-207.
HIRT, U. (2006): Quantifying of tile drainage areas in a catchment as a base
for the modelling of water and matter fluxes. In: MOUCHEL, J.-M.,
BARLES, S. (eds.): Man and river systems. Interactions among Rivers,
their watersheds, and the sociosystem, 111-114.
HUPFER, M. (2006): Eutrophierungsverminderung durch
Gewässertechnologien- Irrweg oder Herausforderung für Wissenschaft
und Praxis. 4. Stechlin-Forum, 4, 21-28.
KASPRZAK, P., REESE, C., KOSCHEL, R., SCHULZ, M., HAMBARYAN, L.,
MATHES, J. (2006): Glacial relicts in NE-German lakes: Habitat
characteristics of Eurytemora lacustris (Copepoda, Calanoida). Berichte
des IGB, 23, 151-160.
KIRILLIN, G., GOLOSOV, S., ENGELHARDT, C. (2006): Observation of a
cyclonic gyre produced by internal surge in a small deep lake . Berichte
des IGB, 23, 55-64.
KIRSCHBAUM, F. (2006): Erstmalige Zucht eines Vertreters der
Nilhechtgattung Petrocephalus (P. soudanensis) induziert durch
Imitation von Hochwasserbedingungen. In: GREVEN, H., RIEHL, R.
(eds.): Biologie der Aquarienfische. Tetra Verlag GmbH, Berlin, 65-72.
KIRSCHBAUM, F., KIRSCHBAUM, M. (2006): Ablaichen von zwei
Messerfischen der Gattung Brachyhopopomus (B. pinnicaudatus, B.
brevirostris) im Aquarium induziert durch Imitation von
Hochwasserbedingungen. In: GREVEN, H., RIEHL, R. (eds.): Biologie
der Aquarienfische. Tetra Verlag GmbH, Berlin, 74-80.
KIRSCHBAUM, F., SCHUGARDT, C. (2006): Fortpflanzungsstrategien und
entwicklungsbiologische Aspekte bei südamerikanischen Messerfischen
(Gymnotiformes) und afrikanischen Nilhechten (Mormyridae) vergleichende Betrachtungen. In: GREVEN, H., RIEHL, R. (eds.):
Biologie der Aquarienfische. Tetra Verlag GmbH, Berlin, 81-116.
KLEEBERG, A., GELBRECHT, J. (2006): Risikoabschätzung der Belastung der
Müggelspree aus exponierten Gleithängen nach MakrophytenEntfernung. Im Auftrag des Landesumweltamtes Brandenburg (LUA),
1-16.
KLEEBERG, A., HUPFER, M. (2006): Experimental studies on sediment and
phosphorus resuspension in the lowland River Spree, NE Germany.
Berichte des IGB, 23, 79-88.
KLEEBERG, A., HUPFER, M. (2006): Re- und Immobilisierung von Phosphor
unter alternierenden Milieubedingungen. BMBF-Verbundprojekt
„Feinsedimentdynamik und Schadstoffmobilität in Fließgewässern" Förderkennzeichen 02WF0469, 1-59.
KNAUS, U., WIRTH, M., RENNERT, B., SCHULZ, C. (2006): Einfluss einer
partiellen Substitution von Fischöl durch Leinöl und Sojaöl auf das
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Wachstum und die Körperzusammensetzung von Zandern (Sander
lucioperca, L). Fischerei & Fischmarkt in Mecklenburg-Vorpommern, 6,
39-40.
KNAUS, U., WIRTH, M., RENNERT, B., SCHULZ, C. (2006): Einfluss einer
partiellen Substitution von Fischöl durch Leinöl und Sojaöl auf das
Wachstum und die Körperzusammensetzung von Zandern (Sander
lucioperca, L). Fischer & Teichwirt, 57, 174-175.
KÖHLER, J. (2006): Einfluss von Talsperren und durchflossenen Seen auf die
Wasserqualität im Spreegebiet. In: MÜLLER, D., SCHÖL, A., BERGFELD,
T., STRUNCK, Y. (eds.): Staugeregelte Flüsse in Deutschland.
Schweizerbart, Stuttgart, Limnologie aktuell, Band 12, 213-225.
KOSCHEL, R., BEHRENDT, H., HUPFER, M. (2006): Integrierter
Gewässerschutz in Binnengewässern. In: IGB Berlin, A. L. G. S. (ed.): 4.
Stechlin-Forum. Integrierter Gewässerschutz für Binnengewässer:
Maßnahmen zum nachhaltigen Umgang mit der Ressource Wasser, 1120.
KOSCHEL, R., BEHRENDT, H., HUPFER, M. (2006): Surface waters under
stress factors and their controlling by integrated measures. In: LOZAN, J.
L., GRAßL, H., HUPFER, M., MENZEL, L., SCHÖNWIESE, C. D. (eds.):
Global Change: Enough Water for all? Wissenschaftliche Auswertungen,
Hamburg, 89-94.
KOSCHEL, R., GONSIORCZYK, T., KASPRZAK, P., KRIENITZ, L., WAUER, G.
(2006): Ergebnisbericht 2005 zum Vorhaben
Nachhaltigkeitsuntersuchung der Restaurierung Tiefwarensee.
Nachhaltigkeitsuntersuchung der Restaurierung Tiefwarensee, VE15:157,
1-65.
KOSCHEL, R., KASPRZAK, P., KRIENITZ, L. (2006): Ergebnisbericht 2005
zum Vorhaben Trophieentwicklung Tollensesee und Lieps:
Langzeitentwicklung und Grundlagen zur Sanierung und Restaurierung.
Trophiesituation und Langzeitentwicklung Tollensesee und Lieps,
VE15:160, 1-71 + Tabellen.
KOSCHEL, R., KASPRZAK, P., KRIENITZ, L., GONSIORCZYK, T., SCHULZ, M.
(2006): Ergebnisbericht 2005; Trophiesituation und Langzeitentwicklung
trophischer Kriterien im Feldberger Haussee. Trophiesituation und
Langzeitentwicklung trophischer Kriterien im Feldberger Haussee,
VE15:159, 1-67 + Tabellen.
KOSCHEL, R., ROßBERG, R., TESCH, E. (eds.) (2006): Integrierter
Gewässerschutz für Binnengewässer: Maßnahmen zum nachhaltigen
Umgang mit der Ressource Wasser. Berlin.
LEWIN, W.-C., ARLINGHAUS, R., MEHNER, T. (2006): A brief overview on
biological impacts of recreational angling: insights for management and
conservation. Berichte des IGB, 23, 161-172.
LUO, W., PFLUGMACHER, S., WALZ, N., KRIENITZ, L. (2006): Experimental
bristle induction in Micractinium (Chlorophyta): an example of
interaction between grazer and phytoplankton. Berichte des IGB, 23,
103-112.
MEINELT, T. (2006): Betrachtungen zum Wettangeln. Angeln und Fischen,
12, 3.
164
MEINELT, T. (2006): Dorsch - Kapitale sind das Kapital. Kutter & Küste, 21,
64-66.
MEINELT, T. (2006): Große Fische müssen geschont werden oder vom Sinn
und Unsinn von Höchst- und Mindestmaßen. Fischer & Angler in
Sachsen, 3, 80.
MEINELT, T. (2006): Große Fische müssen geschont werden oder vom Sinn
und Unsinn von Mindestmaßen. Angeln und Fischen, 2, 3.
MEINELT, T. (2006): Weidgerechte Angelfischerei. Ethische Betrachtung
einer Passion von Franz Menzebach und Armin Göllner, Buchrezension.
Angeln und Fischen, 10, 3.
MEINELT, T. (2006): Zum Zurücksetzen großer Fische…. Angeln und
Fischen, 9, 3.
MEINELT, T., ARLINGHAUS, R. (2006): Zur unterschätzten Bedeutung großer
Tiere im Fischereimanagement. Angeln und Fischen, 6, 2.
MEINELT, T., STÜBER, A., BRÄUNIG, I. (2006): Weitere Ergebnisse bei der
Anwendung von Peressigsäure (Wofasteril E400 und Wofasteril E250)
zur Bekämpfung von Fischschimmel (Saprolegnia parasitica) - Erste
Erfahrungen bei der Erbrütung von Regenbogenforellen. Fischer &
Teichwirt, 57, 12-14.
MORSCHEID, H., MÄHLMANN, J., HILT, S. (2006): Wiederbesiedlung von
Flachseen mit submersen Makrophyten: Entwicklung einer
Handlungsanweisung. In: Deutsche Gesellschaft für Limnologie (ed.):
Erweiterte Zusammenfassung der DGL-Tagung, 130-133.
NÜTZMANN, G., HOLZBECHER, E., WIESE, B. (2006): Inverse modeling tool
visual CXTFIT for one-dimensional transport, sorption and degradation
processes during bank filtration. In: STUDZINSKI, J., HRYNIEWICZ, O.
(eds.): Modeling concepts and decision support in environmental
systems. Polish Academy of Sciences, Warsaw, System research, 11-24.
OHLBERGER, J., STAAKS, G., HÖLKER, F. (2006): Influence of morphology
on swimming costs in fishes . Berichte des IGB, 23, 127-138.
PFLUGMACHER, S., PEUTHERT, A., CHAKRABATI, S. (2006): Cyanobacterial
toxins and oxidative stress responses in aquatic macrophytes. Berichte
des IGB, 23, 31-40.
PUSCH, M. (2006): Szenarien und Entscheidungshilfen. In: Pusch, M.,
Fischer, H. (eds.): Stoffdynamik und Habitatstruktur in der Elbe.
PUSCH, M., FISCHER, H. (2006): Einleitung. In: PUSCH, M., FISCHER, H.
(eds.): Stoffdynamik und Habitatstruktur in der Elbe. Weissensee,
Berlin, 1-6.
PUSCH, M., FISCHER, H. (2006): Zusammenfassung und Ausblick. In: PUSCH,
PUSCH, M., FISCHER, H. (eds.) (2006): Stoffdynamik und Habitatstruktur in
der Elbe. Weissensee Verlag, Berlin.
PUSCH, M., FISCHER, H., SCHWARTZ, R. (2006): Synthese der Auswirkungen.
© IGB 2007
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PUSCH, M., SCHWARTZ, R., FISCHER, H. (2006): Prozesse und Biozönosen in
den Buhnenfeldern - Einleitung. In: PUSCH, M., FISCHER, H. (eds.):
Stoffdynamik und Habitatstruktur in der Elbe. Weissensee, Berlin, 83-86.
RESTREPO, G., BRÜGGEMANN, R. (2006): Ranking regions using cluster
analysis, Hasse diagram technique and topology. In: VOINOV, A.,
JAKEMAN, A. J., RIZZOLO, A. E. (eds.): Proceedings of the iEMSs Third
Biennial Meeting: "Summit on Environmental Modelling and Software",
1-6.
SAUER, W., KRÜGER, A., ENGELHARDT, C. (2006): Artificial vs natural
flooding regime of a polder in the Lower Odra Valley: sediments and
loads. In: STUDZINSKI, J., HRYNIEWICZ, O. (eds.): Modelling concepts
and decision support in environmental systems, 57-68.
SCHUGARDT, C., KIRSCHBAUM, F. (2006): Erstmaliges Ablaichen der zwei
Nilhechtarten Mormyrus sp. und Marcusenius mento unter
Aquarienbedingungen induziert durch Imitation von
Hochwasserbedingungen. In: GREVEN, H., RIEHL, R. (eds.): Biologie
SCHUGARDT, C., KIRSCHBAUM, F. (2006): Fortpflanzung und Entwicklung
von Polypterus senegalus. In: GREVEN, H., RIEHL, R. (eds.): Biologie
SCHWARTZ, R. (2006): Entstehung und Gliederung des Flusslaufs. In: PUSCH,
SCHWARTZ, R., BRUNKE, M., FISCHER, H. (2006): Sedimentdynamik. In:
SCHWARTZ, R., KOZERSKI, H.-P. (2006): Sedimentation in Buhnenfeldern.
SUKHODOLOV, A., SUKHODOLOVA, T. (2006): Evolution of mixing layers in
turbulent flow over submersible vegetation: field experiments and
measurement study. In: FERREIRA, R. L. M., ALVES, E. C. T., LEAL, J. G.
A. B., CARDOSO, A. H. (eds.): River Flow 2006. Taylor &
Francis/Balkema, London, UK, 1, 525-534.
SUKHODOLOV, A., SUKHODOLOVA, T., BUNGARTZ, H. (2006): Turbulence in
natural streams. In: STUDZINSKI, J., HRYNIEWICZ, O. (eds.): Modeling
concepts and decision support in environmental systems. Polish
Academy of Sciences, Warsaw, System research, 41-56.
SUKHODOLOVA, T., SUKHODOLOV, A. (2006): Field-scale experiment on the
flow dynamics over submerged macrophytes. Berichte des IGB, 23, 6578.
SUKHODOLOVA, T., SUKHODOLOV, A., KOZERSKI, H.-P., KÖHLER, J. (2006):
Longitudinal dispersion in a lowland river with submersible vegetation.
In: FERREIRA, R. L. M., ALVES, E. C. T., LEAL, J. G. A. B., CARDOSO, A.
H. (eds.): River Flow 2006. Taylor & Francis/Balkema, London, UK, 1,
631-638.
VENOHR, M., BEHRENDT, H. (2006): Nitrogen retention in surface waters:
application and inter-comparison of empirical and conceptual models.
166
In: MOUCHEL, J.-M., BARLES, S. (eds.): Man and river systems.
Interactions among Rivers, their watersheds, and the sociosystem, 260263.
VENOHR, M., BEHRENDT, H. (2006): Spatial distribution of nitrogen
emissions and retention and their influence on the resulting load.
Berichte des IGB, 23, 141-150.
VOIGT, K., BRÜGGEMANN, R. (2006): Information Systems and Databases.
In: BRÜGGEMANN, R., CARLSEN, L. (eds.): Partial Order in
Environmental Sciences and Chemistry. Springer, Berlin, 328-351.
VOIGT, K., BRÜGGEMANN, R. (2006): Method of Evaluation by Order
Theory Applied on the Environmental Topic of Data-Availability of
Pharmaceutically Active Substances. In: STUDZINSKI, J., HRYNIEWICZ,
O. (eds.): Development of Methods and Technologies of Informatics
for Process Modeling and Management. Polish Academy of Sciences,
Systems Research Institute, Warsaw, 107-120.
VOIGT, K., PUDENZ, S., BRÜGGEMANN, R. (2006): ProRank - a Software
Tool used for the Evaluation of Environmental Databases. In: VOINOV,
A., JAKEMAN, A. J.,.RIZZOLO, A. E. (eds.): Proceedings of the iEMSs
Third Biennial Meeting: "Summit on Environmental Modelling and
Software", 1-6.
WAUER, G., CASPER, P., GONSIORCZYK, T., KOSCHEL, R. (2006):
Restaurierung des Tiefwarensees, Mecklenburg-Vorpommern, von 20012005 mit der Fällmittelkombination NaAl(OH)4/Ca(OH)2:
Auswirkungen auf die Sedimentbeschaffenheit und interne P-Retention.
In: Deutsche Gesellschaft für Linmnologie (ed.): Erweiterte
Zusammenfassungen, 109-113.
WILCZEK, S. (2006): Extrazelluläre Enzymaktivitäten freier und angehefteter
Bakterien. In: PUSCH, M., FISCHER, H. (eds.): Stoffdynamik und
Habitatstruktur in der Elbe. Weissensee, Berlin, 79-82.
WINKLHÖFER, K., LESZINSKI, M., STEINBERG, C. E. W. (2006):
Industriebetriebe an der Oberspree und ihre Auswirkungen auf die
biotische Beschaffenheit des Flusses im frühen 20. Jahrhundert. In:
FRANK, S., GANDY, M. (eds.): Hydropolis - Wasser und die Stadt der
Moderne. Campus, Frankfurt New York, 117-145.
WOLTER, C. (2006): Bedeutung von Auen für die Fischfauna und ihre Rolle
im ökologischen Monitoring. Dokumentationen zu den WRRLSeminaren der GRÜNEN LIGA, 17-19, 65-69.
WOLTER, C. (2006): Die fischökologische Bedeutung von Flussauen und ihre
Berücksichtigung bei der fisch-basierten Gewässer-Zustandsbewertung.
Artenschutzreport, 19, 45-49.
WOLTER, C. (2006): Vorkommen und Verbreitung des Stromgründlings
Romanogobio belingi (Slastenenko, 1934) in der unteren Oder.
Nationalpark-Jahrbuch Unteres Odertal, 2006, 48-54.
WÖRNER, U., BRUNKE, M. (2006): Vertikale Wechselwirkungen zwischen
Pelagial und Sediment im Buhnenfeld. In: PUSCH, M., FISCHER, H. (eds.):
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4.3 Degrees
Abschlüsse
4.3.1 Bachelor and Master Theses
Bachelor- und Diplomarbeiten
AULHORN, M. (2006): Einfluss eines cynobakteriellen Rohextraktes auf
verschiedene Spinatvarietäten: Korrelation von Keimung und Wachstum
mit dem antioxidativen Stoffwechsel. Humboldt Universität zu Berlin,
120 S.
BAHRTH, C. (2006): Gene expression of superoxide dismutase isoforms in
Ceratophyllum demersum after exposure to cyanobacterial toxinsimplications for oxidative stress. Universität Konstanz, 88 S.
BEHREND, A. (2006): Einfluss des cyanobakteriellem Toxins Microcystin auf
die Proteinexpression in Daphnia magna. Humboldt Universität zu
Berlin, 110 S.
BOEKHOFF, S. (2006): Sukzession und Diversität von Eubakterien und
Pilzen während des Laub-Abbaus im Bodensee-Litoral. Universität
Konstanz, 57 S.
BRÜCKNER, S. (2006): Characterisation of Actinobacteria populations in
lakes of the Mecklenburg-Brandenburg Lake District. Hochschule
Bremen, 82 S.
FALLER, M. (2006): Möglichkeiten und Grenzen der Erfassung potamaler
Fische in großen Strömen mittels nächtlicher Elektrobefischungen.
Humboldt-Universität zu Berlin, Landwirtschaftlich-Gärtnerische
Fakultät, 72 S.
FREUDENBERG, P. (2006): Unterschiede zwischen organisierten und
nichtorganisierten Anglern im urbanen Raum: Eine sozioökonomische
Analyse am Beispiel Berlins. Humboldt-Universität zu Berlin, 76 S.
GABEL, F. (2006): Impact of ship-induced waves on benthic invertebrates
colonising lake shore habitats - An experimental study. Westfälische
Wilhelms-Universität Münster, 70 S.
HALLERMANN, J. (2006): Auswirkungen eines simulierten Angelvorgangs auf
Mortalität und Wachstum von untermaßigen Zandern (Sander
lucioperca): die Rolle der Luftexposition. Humboldt-Universität zu
Berlin, 53 S.
HÜHN, D. (2006): Letale und subletale Auswirkungen von Fangen-undZurücksetzen: Meta-Analyse verfügbarer Literatur und Empfehlungen
für das angelfischereiliche Management in Deutschland. HumboldtUniversität zu Berlin, 92 S.
JAROSCH, A. (2006): Oxidativer Stress in Cyanobakterien in Daphnia magna:
Vergleich der enzymatischen Reaktion mit deren Regulation auf
Genebene. Humboldt-Universität zu Berlin, 120 S.
JÄHRLING R. (2006): Habitat choice and activity patterns of juvenile eastern
freshwater cod (Maccullochella ikei) in an artificial environment.
Fakultät, 77 S.
168
MÜLLER, M. (2006): Metabolismus von PCB52 im Nematoden
Caenorhabditis elegans und Charakterisierung der dabei induzierten
Glutathion S-Transferase. Freie Universität Berlin, 99 S.
NEUMANN, F. (2006): Diagenetische Veränderungen partikulärer
Phosphorbindungsformen in Seesedimenten unter dem Einfluss von
Makrozoobenthos. Universität Potsdam, 78 S.
RAPP, T. (2006): Toxische Wirkung von Konservierungsmitteln in
Angelfuttermitteln: der Einfluss von Benzoesäure und Kaliumsorbat auf
die Eientwicklung beim Zebrabärbling (Danio rerio). HumboldtUniversität zu Berlin, 84 S.
SCHOMAKER, C. (2006): Vergleichende Erfassung und Bewertung der
Fischgemeinschaftsstruktur in abgetrennten und temporär
angeschlossenen Auegewässern des Nationalparks "Unteres Odertal".
Fakultät, 87 S.
WEISHEIT, C. (2006): Konditionierung von Karpfen (Cyprinus carpio) durch
Huminstoffe verschiedener Herkunft. Humboldt-Universität zu Berlin,
92 S.
4.3.2 PhD Theses
Doktorarbeiten
ALLGAIER, M. (2006): Diversität und Dynamik von
Bakteriengemeinschaften in vier ausgewählten Seen der
Mecklenburgischen Seenplatte. Universität Oldenburg, 132 S.
BLANK, B. (2006): Qualitative und quantitative Charakterisierung des
Nitratabbaus im oberflächennahen Grundwasser des SchaugrabenEinzugsgebietes. Humboldt Universität zu Berlin, 146 S.
GRESKOWIAK, J. (2006): Reactive transport processes in artificial recharged
aquifers - field and modelling studies. Humboldt Universität zu Berlin,
131 S.
MEYER, V. (2006): Die Bedeutung von Ciliaten für die Juvenilentwicklung
und reproduktion von Copepoden sowie ihre trophischen Interaktionen
im Tiefenchlorophyllmaximum eines mesotrophen Sees. IGB, 1-165 S.
SCHULZE, T. (2006): Changes in structure and function of the fish
community in a mesotrophic lake ecosystem after stocking a non-native
top predator. Universität Potsdam, Institut für Biochemie und Biologie,
140 S.
SENADEERA, K. P. G. W. (2006): Effects of catchment characteristics and
land use practices on water quality of Kotmale, Victoria, Randenigala
and Rantambe reservoirs using GIS. University of Jayewardenepura, Sri
Lanka, 402 S.
VENOHR, M. (2006): Modellierung der Einflüsse von Temperatur, Abfluss
und Hydromorphologie auf die Stickstoffretention in Flusssystemen.
Mathematisch-Naturwissenschaftliche Fakultät II der HumboldtUniversität zu Berlin, 193 S.
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WAUER, G. (2006): Der Einfluss von Fällmittelkombinationen auf die PRetention in Sedimenten geschichteter Seen. Humboldt-Universität zu
Berlin, 123 S.
WIESE, B. (2006): Spatially and temporally scaled inverse hydraulic
modelling, multi-tracer transport modelling, and interaction with
geochemical processes at a highly transient bank filtration site.
Humboldt Universität zu Berlin, 195 S.
ZIPPEL, M. (2006): Modellgestützte Bilanzierung der unterirdischen
Wasserressourcen Berlins - die Grundwassersituation im weiteren
Einzugsgebiet des Müggelsees. Freie Universität Berlin, 156 S.
4.3.3 Pre-Professional Theses
Habilitationen
HILT, S. (2006): Toleranz und Leistung aquatischer Makrophyten in
nährstoffreichen Gewässern. Humboldt-Universität zu Berlin, 47 S.
170
4.4 Lectures at Universities
Vorlesungen an Universitäten
ADRIAN, R.:
- Freie Universität Berlin, Vom Experiment über die Auswertung zur
Publikation, 3 SWS (WS)
ARLINGHAUS, R.:
- Humboldt-Universität zu Berlin, Landwirtschaftlich-Gärtnerische
Fakultät, Management of Fish Communities, 4 SWS (WS 2005/2006)
CASPER, P., GROSSART, H.-P.:
- Humboldt-Universität zu Berlin, Mikrobiologisch-limnologisches
Praktikum, 4 SWS (SS 2006)
- Technische Universität Dresden, Mikrobiologisch-limnologisches
Praktikum, 2 SWS (SS 2006)
FREYHOF, J.:
- Universität Potsdam, Ökologie und Diversität der Fische, 1 SWS (SS
2006)
- Humboldt-Universität zu Berlin, Versuchsplanung und Auswertung
freilandbiologischer Daten, 2 SWS (SS 2006)
GELBRECHT, J.:
- Humboldt-Universität zu Berlin, Wasserchemie, 4 SWS (WS 2005/2006)
GROSSART, H.-P.:
- Universität Osnabrück, 1 week course: "Aquatic Microbial Ecology"
Field station Eilat in cooperation with K.-H. Altendorf, 2 SWS (WS
2005/2006)
- Universität Kalmar, 1 week course: "Impact of viruses on bacteria
colonizing aggregates"University of Kalmar, Sweden in cooperation with
L. Riemann, 2 SWS (SS 2006)
- Universität Oldenburg, Planktology class (2 weeks, including 1 week
cruise on board of the RV Heincke), physics, chemistry, marine
environmental studies, and biology, 3 SWS (WS 2005/2006)
HILT, S.:
- Humboldt-Universität zu Berlin, Taxonomisch-ökologisches Praktikum,
4 SWS (SS 2006)
HÖLKER, F.:
- Universität Bremen, Introduction into system analysis, 1 SWS (WS
2005/2006)
- Universität Potsdam, Biodiversität und Ökologie der Fische, 1 SWS (SS
2006)
HUPFER, M.:
- Humboldt-Universität zu Berlin, Biogeochemische Stoffkreisläufe in
Seen, 2 SWS (WS 2005/2006)
KIRSCHBAUM, F.:
- Humboldt-Universität zu Berlin, Systematics and Evolution of Fishes, 4
SWS (WS 2005/2006)
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KIRSCHBAUM, F., SCHULZ, C.:
- Humboldt-Universität zu Berlin, Biologie, Ökologie und Nutzung
tropischer Fischgemeinschaften/ Tropical Fish Communities, 2 SWS
(WS 2005/2006)
KLOAS, W.:
- Humboldt-Universität zu Berlin, Oberseminar: Hormonphysiologie, 1
SWS (WS 2005/2006)
- Humboldt-Universität zu Berlin, Vergleichende Endokrinologie, 2 SWS
(WS 2005/2006)
KNOPF, K.:
- Humboldt-Universität zu Berlin, Fish Pathology II (Parasitology), 4 SWS
(WS 2005/2006)
KOHLMANN, K.:
- Humboldt-Universität zu Berlin, Genetics and Breeding of Fishes, 4 SWS
(SS 2006)
MEHNER, T.:
- Technische Universität Dresden, Fischökologie Blockkurs, 2 SWS (WS
2005/2006)
MEINELT, T.:
- Humboldt-Universität zu Berlin, Environmental stress in fishes, 3 SWS
(SS 2006)
NÜTZMANN, G.:
- Humboldt Universität zu Berlin, Hydrologische Modelle I, 2 SWS (WS
2005/2006)
- Humboldt-Universität zu Berlin, Hydrologische Modelle, 2 SWS (WS
2005/2006)
- Humboldt Universität zu Berlin, Einführung in die Hydrologie, 2 SWS
(SS 2006)
PFLUGMACHER, S.:
- Humboldt-Universität zu Berlin, Biochemische Regulation im
aquatischen Ökosystem, 2 SWS (WS 2005/2006)
aquatischen Ökosystem (Fachkurs), 4 SWS (WS 2005/2006)
aquatischen Ökosystem (Fachkurs), 2 SWS (WS)
aquatischen Ökosystem (Oberseminar), 2 SWS (SS)
PUSCH, M.:
- Universität Potsdam, Aquatische Ökologie II - Fließgewässerökologie, 2
SWS (SS 2006)
RENNERT, B.:
- Humboldt-Universität zu Berlin, Special Aquaculture, 2 SWS (WS
2005/2006)
- Humboldt-Universität zu Berlin, Special Aquaculture, 2 SWS (WS
2005/2006)
WIEDNER, C., DITTMANN, E.:
- Humboldt Universität zu Berlin, Molekulare Ökologie Praktikum, 4 SWS
(SS 2006)
172
WIEGAND, C.:
- Humboldt-Universität zu Berlin, Methoden der BiochemischMolekularen Ökotoxikologie, 2 SWS (WS 2005/2006)
- Humboldt-Universität zu Berlin, Aktuelle Fragen der Ökotoxikologie, 2
SWS (WS 2005/2006)
- Humboldt-Universität zu Berlin, Biochemisch Molekulare
Ökotoxikologie, 2 SWS (SS 2006)
- Humbolt-Universität zu Berlin, Biochemische Ökotoxikologie, Laborund Freilanduntersuchungen (Fachkurs), 4 SWS (SS 2006)
WILHELM, S.:
- Universität Potsdam, Tutorium zur Ökologie II, 1 SWS (WS 2005/2006)
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4.5 Memberships in Scientific or Editorial
Boards
Verantwortliche Positionen in Fachgesellschaften oder Gremien
ARLINGHAUS, ROBERT:
- Fisheries Management and Ecology, Editorial Board Member
- European Inland Fisheries Advisory Commission of the FAO,
Working Party on Recreational Fisheries, Head
- European Inland Fisheries Advisory Commission of the FAO,
Subcommission IV Social and Economic Issues, Rapporteur
- European Anglers Alliance, Scientific Advisory Committee
CASPER, PETER:
- International Journal of Lakes & Rivers, Editorial Board Member
- Beiträge zur angewandten Gewässerökologie Norddeutschlands,
Editorial Board Member
GESSNER, JÖRN:
- World Sturgeon Conservation Society, Board of Directors, Secretary
General
- Gesellschaft zur Rettung des Störs - Society to Save the Sturgeon (Acipenser sturio L.) e.V., Vorstandsmitglied
- International Sturgeon Research Centre, Malaspina University College,
Scientific Committee, Member
- ICES Working Group on International Transfers of Marine Organisms,
Member
- HELCOM Habitat, PG Restoration of Baltic Sturgeon, Chairman
GROSSART, HANS-PETER:
- Aquatic Microbial Ecology, Reviewing Editor
- Scientific World (online publisher), Editorial Board Member
HILT, SABINE:
- DGL-Arbeitskreis Flachseen, Leitung
HUPFER, MICHAEL:
- Limnologica, Advisory Board Member
- Lake Restoration Center, University of Southern Denmark, Advisory
Board Member
KASPRZAK, PETER:
- International Review of Hydrobiology, Advisory Board Member
- Präsidium der Deutschen Gesellschaft für Limnologie (DGL), Beisitzer
KIRSCHBAUM, FRANK:
- Aqua Geographia, Advisory Board Member
- Zeitschrift für Fischkunde, Advisory Board Member
- Journal of Ichthyology and Aquatic Biology, Advisory Board Member
- Gesellschaft zur Rettung des Störs - Society to Save the Sturgeon (Acipenser sturio L.) e.V., Advisory Board Head
- Studiengang Fisheries Science and Aquaculture, Prüfungsausschuss
174
KLOAS, WERNER:
- General and Comparative Endocrinology, Associated Editor
- Environmental Research, Editorial Board Member
- Journal of Applied Ichthyology, Editorial Board Member
- OECD ad hoc Expert Group: Endocrine Disruptor Task Force for
Amphibians
KOHLMANN, KLAUS:
- Fachbeirat für Aquatische Genetische Ressourcen, BMVEL,
Stellvertretender Vorsitzender
- Environmental Biotechnology, Editor
KOSCHEL, RAINER:
- International Association of Theoretical and Applied Limnology (IVL),
Nationaler Repräsentant
- Institut für Angewandte Gewässerökologie GmbH, Seddin,
Gründungsmitglied und Vorstandsmitglied
- Limnologica, Elsevier Verlag, Managing Editor
- Beiträge zur angewandten Gewässerökologie Norddeutschlands, CoEditor
KRIENITZ, LOTHAR:
- Algological Studies, Editorial Board Member
- Phycologia, Co-Editor
- Süßwasserflora von Mitteleuropa, Co-Editor
MEHNER, THOMAS:
- ASLO Committee on Education, Committee Member
MEINELT, THOMAS:
- Präsidium des Deutschen Anglerverbandes e.V. (DAV), Referent für
Umwelt und Gewässer
- Gemeinsamer Fachbeirat Gewässerökologie des DAV und der
Naturfreunde Deutschlands, Sprecher
PFLUGMACHER, STEPHAN:
- Environmental Toxicology and Chemistry, Editorial Board Member
- Journal of Applied Phycology, Editorial Board Member
POYNTON, SARAH L.:
- Acta Protozoologica, Editorial Board Member
- Food and Agriculture Organization of the United Nations, Regional
Reviewer for Aquaculture
PUSCH, MARTIN:
- Annales de Limnologie – International Journal of Limnology, Co-Editor
WALZ, NORBERT:
- International Review of Hydrobiology, Executive Editor
WOLTER, CHRISTIAN:
- Landesfischereibeirat Berlin, Vorsitzender
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175
4.6 Projects and grants
Projekte und Stipendien
EU Projects
EU-Projekte
BEHRENDT, H.: EUROHARP: Towards European harmonized procedures
for quantification of nutrient losses from diffuse sources (FKZ: EVK1CT-2001-00096-Euroharp); 2002-2006.
BEHRENDT, H.: Strengthening the Implementation for Nutrient Reduction
and Transboundary Cooperation in the Danube River Basin (FKZ:
RER/03/G31); 2006-2007.
KIRSCHBAUM, F.: CRAFT: Analyse des Genom nach Sexmarkern mittels
AFLP (Amplified Fragment-Length Polymorphism) und RAPD
(Random Amplification of Polymorphic DNA) (FKZ: Q5CR-200272183 CRAFT); 2003-2006.
KLOAS, W.: COMPRENDO: Comparative Research on Endocrine
Disrupters (FKZ: ECK1-CT-2002-00129-Comprendo); 2002-2006.
KLOAS, W.: EASYRING: Environmental Agent Susceptibility Assessment
Utilising Existing and Novel Biomarkers as Rapid Non-Invasive Testing
Methods (FKZ: QLK4-CT-2002-02286 Easyring); 2003-2006.
KLOAS, W.: EMSG43 Endocrine disrupting effects in fish induced by
parasites (FKZ: CEFIC-LRI Grant EMSG43); 2006-2009.
KRIENITZ, L.: Potential and risk of mass developments of the
cyanobacterium Arthrospira, an important food resource in tropical
inland waters (FKZ: UNESCO 1-DE-09); 2005-2006.
STAAKS, G.: TECHNEAU: technology enabled universal access to safe water
(FKZ: EU contract 018320); 2006-2008.
SUKHODOLOV, A.: NATO GRANT ESP.NUKR.EV 982416 (FKZ:
ESP.NUKR.EV 982416); 2006
176
DFG Projects
DFG-Projekte
ADRIAN, R., GERTEN, D. (PIK): Phase shifts within lake plankton
communities in response toward climate warming: Implications for the
match/mismatch of species interactions (Aquashift)
(FKZ: AD 91/12-1); 2004-2007.
ARLINGHAUS, R., WOLTER, C.: Adaptive Dynamik und Management
gekoppelter sozial-ökologischer Systeme am Beispiel der Angelfischerei
(ADAPTFISH); 2006-2009.
BUNGARTZ, H., GROSSART, H.-P.: Untersuchungen zum Einfluss der
Aggregatbildung in Flüssen auf die Transportdynamik von
Schwebstoffen (FKZ: BU 1442/1-1+ 1-2); 2004-2007.
GROSSART, H.-P., KRIENITZ, L.: Dynamik von Bakterien-Algen
Interaktionen: Ein Schlüssel zum Verständnis von Nährstoffkreisläufen
in aquatischen Systemen (FKZ: GR 1540/8-1 + 8-2); 2005-2007.
GROSSART, H.-P.: AQUASHIFT Effects of climate variability on interactions
between cyanobacteria and associated microheterotrophs-consequences
for development of toxic cyanobacterial blooms (FKZ: GR 1540/11-1);
2006-2009.
KIRILLIN, G., ENGELHARDT, C., CASPER, P.: Untersuchung der
dreidimensionalen Zirkulationsströmung im Stechlinsee
(FKZ: KI 853/2-1); 2004-2006.
KIRILLIN, G., BEHRENDT, H.: Climatic impact on temperature and mixing
regime of polymictic lakes and its consequences for lake ecosystems
(FKZ: KI 583/3-1); 2005-2007.
KOZERSKI, H.-P.: Systematische Untersuchung der Retentionswirkung von
Makrophyten durch Partikelsedimentation im strömenden Wasser
(FKZ: KO 1352/6-1 + 6-2); 2004-2006.
KRIENITZ, L.: Gattungs- und Artkonzept bei Chlorella und Micractinium
(Chlorophyta, Chlorellaceae): Genotyp versus phaenotypischer Variabilität
unter dem Einfluss von Kairomonen (FKZ: KR 1262/8-1 + 8-2);
2003-2006.
MEHNER, T., FREYHOF, J.: The impact of climate variability on recruitment,
life history, and physiology of sympatric pairs of ciscoes (Teleostei:
Coregonus spp.) in lakes (FKZ: ME 1686/5-1 + 5-2); 2004-2006.
MENZEL, R.: Systematische Untersuchungen zur Xenobiotika- und
Huminstoff induzierten Genexpression (FKZ: ME 2056/2-1); 20042006.
MENZEL, R.: Systematische Untersuchungen zur Xenobiotika- und
Huminstoff induzierten Genexpression im Nematoden Caenorhabitis
elegans (FKZ: ME 2056/2-2); 2006-2007.
SUKHODOLOV, A.: A Fluid Dynamics Laboratory in the Field: a study on
shallow mixing layers at confluent and recirculating river flows under yet
simplified conditions (FKZ: SU 405/2-1); 2006-2008
© IGB 2007
177
Federal institution projects
Bundesprojekte
BEHRENDT, H., KLOAS, W., BRÜGGEMANN, R.: Auswirkungen des Globalen
Wandels auf Nähr- und Schadstoffeinträge und Stoffrückhalte im
Elbegebiet und auf den ökologischen Zustand der Oberflächengewässer
(GLOWA-Elbe II, FKZ: 01LW0313); 2004-2007.
BEHRENDT, H.: Quellen der Nährstoffeinträge und –Frachten im
Flusseinzugsgebiet der Weichsel (FKZ: DLR, DPF 05/330); 2005-2006.
BEHRENDT, H.: Entwicklung eines szenariofähigen Managementtools für
Stoffeinträge in Oberflächengewässer im Rahmen der internationalen
Berichtspflichten (UBA/Uni Karlsruhe, FKZ: 20524204); 2005-2007.
BEHRENDT, H.: Integriertes Wasserressourcen-Management in Zentralasien:
Modellregion Mongolei (MoMo) Teilprojekt : Landnutzung und
Nährstoffbilanzen (FKZ: 0330762D MoMo); 2006-2009.
GELBRECHT, J.: Twinning Prpojekt zu "Capacity Building Environment":
Arbeitsplanung und Abrechnungsverfahren (FKZ: TR02/EN/01
Twinning NATURA); 2004-2006
GESSNER, J.: Untersuchung zur Ökologie Atlantischer Störe als
Voraussetzung zur Wiederherstellung der ursprünglichen
Fischartendiversität großer Fließgewässer (BMBF); 2004-2006.
GESSNER, J., KIRSCHBAUM, F.: Maßnahmen zur Arterhaltung und
Bestandsaufbau der Atlantischen Störe in Nord- und Ostsee; Wiss.
Begleitung "Haltung der Elterntierbestände und versuchsweiser Besatz
(BfN/Gesell. Z. Rettung des Störs, e.V. Z1.3-892 11-6/05); 2005-2008.
HUPFER, M.: Verbundprojekt Feinsedimentdynamik und Schadstoffmobilität
in Fließgewässern, TP 11: Mikrobielle Re-und Immobilisierung von
Phosphor unter alternierenden Milieubedingungen (FKZ: 02WF0469);
2004-2006.
HUPFER, M.: Entnahme von Sedimentkernen, in situ und Labormessungen
(FKZ: Z6-00313 1035); 2006-2007.
KIRSCHBAUM, F.: Genetische Populationsstruktur, Zuchtplan u. künstliche
Vermehrung einer süßwasseradaptierten Zuchtgruppe des Europäischen
Störes (Acipenser sturio) als Voraussetzung einer erfolgreichen
Wiedereinbürgerung (0330718 Störe); 2005-2007.
KLOAS, W.: Amphibien-Metamorphose-Assay – Validation Phase II
(20467454/01 UBA); 2004-2006.
KLOAS, W.: Bewertung und Regulation von Umwelthormonen TV 03:
Fortsetzung der Validierung des 21-d-Amphibien-Metarmorphose-Assay
(FKZ: Z6-97 411-14/41); 2006-2007.
PFLUGMACHER, S., WIEGAND, C.: Verbundprojekt: Minimierung der
Eutrophierung im Chaosee, China-Provinz Anhui, TP2: Entwicklung
umweltbiotechnischer Verfahren (02 WT 0529); 2005-2007.
178
Other projects
Andere Projekte
ARLINGHAUS, R.: Ermittlung der Aalentnahme durch die Angelfischerei in
Binnen-und Küstengewässern von Mecklenburg-Vorpommern
(Landesforschungsanstalt für Landwirtschaft und Fischerei
Mecklenburg-Vorpommern); 2005-2008.
ARLINGHAUS, R.: Vorbereitung, Methodik und Auswertung der
Anglerbefragung für die Region Nordwestmecklenburg und die
Auswertung der Partnerregionen im Interreg-III b-Projekt Sustainable
management of angling tourism in Natura 2000 and other sensitive areas
(LMS, Befragung/Ausw.); 2006-2007.
BEHRENDT, H.; Analyse von Agrar- und Umweltmaßnahmen im Bereich des
landwirtschaftlichen Gewässerschutzes vor dem Hintergrund der EGWasserrahmenrichtlinie in der Flussgebietseinheit Weser
(Bundesforschungsanstalt für Landwirtschaft/Institut für ländliche
Räume); 2005-2008.
BEHRENDT, H., KÖHLER, J.: Entwicklung eines Bewertungsverfahrens für
Phytoplankton in Fließgewässern (LAWA-Projekt-Nr. O11.06); 20032006.
BEHRENDT, H.: Erarbeitung eines Modellprototyps für die Berechnung von
Nährstoffeinträgen auf der Basis einer neuen Gebietsuntergliederung
und Mitarbeit bei der Modellentwicklung für ein Eintragsmodell für
prioritäre Stoffe (Univ. Karlsruhe); 2006-2007.
GELBRECHT, J.: Pilotprojekt Altarmanschluss und Renaturierung der
Müggelspree; Vertrag über das Monitoring, (LUA Brandenburg);
2005-2007.
GELBRECHT, J.: Untersuchung der Phosphorfreisetzung aus
wiedervernässten Mooren im Peenetal (Land Mecklenburg –
Vorpommern); 2003-2007.
GESSNER, J.: Anschaffung und Transport eines Elterntierbestandes an Stören
im Rahmen der Wiedereinbürgerung in der Oder (Land Brandenburg);
2004-2006.
GESSNER, J: Aufbau eines Elterntierbestandes des baltischen Störs A.
Oxyrinchus (M-0523-U); 2006-2007.
GINZEL, G.: Wiederbewässerung der Rieselfelder um Hobrechtsfelde
(Berliner Forsten); 2003-2006.
HORNER, C., NÜTZMANN, G.: Erarbeitung von Planungsgrundlagen für die
Pilotanlage Machnow - Hydraulisch-reaktive Modellierung PrognosePlanungsmodell BIOXWAND (BWB, 45203925); 2005-2006.
KASPRZAK, P.: Verbesserung der Wasserqualität in thermisch geschichteten
Hartwasserseen des NO-deutschen Tieflandes: Die Bedeutung von
äußerer Nährstoffbelastung und pelagischer Nahrungskettenstruktur für
Sedimentation und Phosphorfreisetzung aus dem Sediment (DBU
2005/801); 2006-2009.
KLOAS, W.: Untersuchung von Wasserproben auf endokrine Stoffe und
Auswertung der Analyseergebnisse im Rahmen der Risikoanalyse der
UVS (Berliner Forsten); 2004-2006.
© IGB 2007
179
KLOAS, W.: Wiederbewässerung der Rieselfelder um Hobrechtsfelde,
Untersuchungen für Sedimente, Grund-u.Oberflächenwasser
(Sedimentuntersuchung); 2004-2006
KNOPF, K: Beschreibung der Auswirkungen von Futtermittelzulagen auf den
physiologischen Zustand von Zierfischen (Tetra GmbH); 2003-2006.
KNOPF, K.: Prüfung von mindestens 5 Fischarten auf ihre Eignung als
Modell eines Zierfisches zur Wirksamkeitsuntersuchung potentiell
immunstimulierender Futterzusätze (Tetra GmbH); 2006-2007.
KÖHLER, J., MISCHKE, U.: Mitarbeit im Praxistest Bewertungsverfahren
mittels Phytoplankton für Seen zur Umsetzung der EUWasserrahmenrichtlinie (BTU Cottbus); 2005-2006.
KÖHLER, J.: Phytoplanktonanalysen von bayrischen Seen zur
Weiterentwicklung des für die EU-WRRL vorgeschlagenen
Bewertungssystems (Bayr. Seen); 2005-2006
KÖHLER, J., MISCHKE, U.: Überarbeitung der Taxaliste der
Gewässerorganismen in Deutschland (Bayrisches Landesamt für
Wasserwirtschaft); 2005-2006.
KÖHLER, J.: Umsetzung der Wasserrahmenrichtlinie – Praxistest Bayern:
Auszählung und Bewertung von Phytoplanktonproben aus bayrischen
Fließgewässern (Freistaat Bayern); 2004-2006
KOHLMANN, K.: Durchführung von Untersuchungen zurückkehrender
Laichfische des Atlantischen Lachses (Salmo salar) auf genetische Marker
(Freistaat Sachsen / Sächsische Landesanstalt für Landwirtschaft);
2003-2006.
KOHLMANN, K.: Genetische Charakterisierung rückkehrender Laichfische
des Altantischen Lachses (Salmo salar) auf der Basis von vier
Mikrosatelliten-Loci (Institut für Binnenfischerei Potsdam-Saccrow);
2004-2007.
KOSCHEL, R.: Erarbeitung der Machbarkeitsstudie für den Melzer See unter
besonderer Berücksichtigung der Nachhaltigkeit der
Restaurierungsmaßnahme Tiefwarensee (Stadt Waren/Müritz); 20062007.
KOSCHEL, R., MEHNER, T.: Ganzheitlicher Gewässerschutz: Restaurierung
Tiefwarensee (Stadt Waren/ Land Mecklenburg – Vorpommern);
2001-2006.
KOSCHEL, R.: Ganzheitlicher Gewässerschutz Tollensesee: a) Wassergüte des
Tollensesees und seiner Hauptzuflüsse, b) Limnologische
Zustandsanalyse und Machbarkeitsstudie zur Sanierung und
Restaurierung des Wanzkaer Sees (Land Mecklenburg – Vorpommern);
1995-2007.
KOSCHEL, R.: Untersuchungen zur Nachhaltigkeit der Maßnahme künstliche
Calcitfällung und Tiefenwasserbelüftung im Schmalen Luzin
(Pilotanlage) (Land Mecklenburg – Vorpommern); 1997-2007.
LUTZ, I., KLOAS, W.: Response of larval Xenopus laevis to 17-ß Estradiol (E2):
Assessment of development, time to metamorphosis, and gonodal
morphology (Syngenta TO 14017-04); 2004-2007.
180
MEHNER, T., FREYHOF, J.: Genetische Charakterisierung existierender
Populationen der Kleinen und Großen Maräne (Coregonus spp.) in Seen
Schleswig-Holsteins (Land Schleswig-Holstein, Amt für Ländliche
Räume Kiel); 2005-2006.
MEINELT, T.: Fischei-Test Zebrabärblinge (Fischerei-Test); 2003-2007
MEINELT, T.: Peressigsäure (Wofasteril) als alternatives Therapeutikum
gegen Ektoparasiten (Schreiner-Stiftung); 2005-2006.
MENZEL, R.: Untersuchung von Flusswassersedimenten (Elbe, Rhein,
Donau) auf toxische Wirkung mit einem C.elegans DNA-Microarray
(bfg DNA-Microarray); 2006.
MISCHKE, U.: Analyse und Bewertung von bayrischen Fließgewässern zur
Weiterentwicklung des für die EU-WRRL vorgeschlagenen
Bewertungssystems Phytoplankton (Bayr. LA für Umwelt); 2006-2007.
PUSCH, M.: Gutachten: Wissenschaftliche Begleitung des DBU-Projekts
"Erhaltung von Habitaten der Kleinen Flussmuschel (Unio crassus) im
Biosphärenreservat Spreewald durch Einrichtung von Borstenpässen
(Landesumweltamt Brandenburg); 2005-2006.
PUSCH, M.: Praxistest zur Bewertung von Phytoplankton, Makrophyten und
Makrozoobenthos in fünf Berliner Seen im Rahmen der Umsetzung der
EU-WRRL (VIII E22/11); 2006.
WIEDNER, C.: Cylindrospermopsis raciborskii und Cylindrospermopsin in
Gewässern der Berliner Region (Kompetenzzentrum Wasser Berlin);
2004-2007.
WIEDNER, C.: Neo-Cyanobakterien und Neo-Toxine in Berliner und
Brandenburger Gewässern (Kompetenzzentrum Wasser Berlin);
2005-2007.
WOLTER, C.: Bestandserhebung der Fischfauna, Bewertung und Erstellung
fischökologischer Referenzzönosen von ausgewählten Fließgewässern
Brandenburgs (IfB, Referenzzönosen); 2006.
WOLTER, C.: Ermittlung des fischereilich begründeten MindestWasserabflusses in großen Tieflandflüssen am Beispiel der Havel
(Fischereigenossenschaft „Havel“); 2005-2008.
WOLTER, C.: Fischerfassung in ausgewählten BundeswasserstraßenAbschnitten (SenVerw. Fischerf.); 2006.
WOLTER, C.: Untersuchung des Laichgeschehens auf dem Fischlaichplatz
"Westlicher Abzugsgraben" bei der Zitadelle Spandau sowie Abgrenzung
der Bedeutung dieses Laichplatzes mit solchen im Wehrauslaufbereich
der Schleuse Charlottenburg sowie solchen in den Tiefwerder Gräben
(Fischereiamt Berlin); 2005-2006.
© IGB 2007
181
Grants
Stipendien
ALLGAIER, M.: Zeitliche und räumliche Variabilität innerhalb der
Bakteriengemeinschaft in Seen des Rheinsberger Seengebietes;
supervisor: GROSSART, H.-P.: 2004-2006 (Stiftung des Deutschen
Volkes).
BAUER, N.: Allelopathische Wechselwirkungen zwischen Makrophyten und
Phytoplanktonarten; supervisor: HILT, S.: 2005-2008 (Freie Universität
Berlin, NaFöG).
BRAUNS, M.: Erarbeitung eines Verfahrens zur ökologischen Bewertung von
Seeufern; supervisor: WALZ, N.: 2005-2006 (FAZIT-Stiftung)
CONTARDO, V.: Einfluss veränderter Wassereintrittspfade auf aquatische
Organismen anhand ökotoxikologischer Kenngrößen; supervisor:
WIEGAND, C.: 2005-2008 (Graduiertenkolleg Stadtökologie).
FARD, M.: Wirt-Parasiten-Beziehungen in Diplomonaden Flagellaten bei
wirtschaftlich wichtigen Süßwasserfischen; supervisor: KLOAS, W.:
2004-2006 (Humboldt-Universität zu Berlin, NaFöG).
FERNANDES, M.: Identifizierung der Emission von Treibhausgasen über die
Grenzfläche Wasser-Athmosphäre geschichteter Seen in
Nordostdeutschland; supervisor: CASPER, P.: 2005-2006 (Leonardo-daVinci-Stipendium, EU).
GRIGUTYTE, R.: Oxidativer Stress in der Characee 'Nitellopsis obtusa' durch
Laubblattinhaltsstoffe - physiologische und ökologische Auswirkung;
supervisor: PFLUGMACHER, S.: 2005-2008 (Deutsche Bundesstiftung
Umwelt).
HAMANN, E.: Modellgestützte Untersuchung des Stofftransports im
Grundwasser eines urbanen Ballungsraumes unter besonderer
Berücksichtigung veränderter Wassernutzung; supervisor: NÜTZMANN,
G.: 2005-2008 (Humboldt-Universität zu Berlin, Deutsche
Forschungsgemeinschaft).
HILT, S.: Ökologische Relevanz allelopathischer Effekte submerser
Makrophyten auf Phytoplankton und Phytobenthos; supervisor: WALZ,
N.: 2003-2006 (Humboldt-Universität zu Berlin, Berliner Programm zur
Förderung der Chancengleichheit von Frauen in Forschung und Lehre).
HUTALLE, K.: Diversität und Dynamik der Bakteriengemeinschaften in
ausgewählten Seen der Mecklenburger Seenplatte; supervisor: GROSSART,
H.-P.: 2004-2007 (DAAD).
KAMARA, S.: Effects of Natural organic matter (NOM) on photosynthetic
activity, pigment pattern and antioxidant status of the aquatic
macrophytes 'Ceratophyllum demersum' and 'Lemna minor'; supervisors:
PFLUGMACHER, S.: 2005-2009 (DAAD).
LASKOV, C.: Einfluss submerser Makrophyten auf geochemische Prozesse im
Sediment eutropher wiederbesiedelter Flachseen; supervisor: HUPFER,
M.: 2004-2006 (Humboldt-Universität zu Berlin, Berliner Programm zur
Förderung der Chancengleichheit von Frauen in Forschung und Lehre).
182
NEUMANN, N.: Parasiten als Stressoren und die Auswirkungen von Stress auf
die Immunantwort bei Fischen; supervisor: KLOAS, W.: 2004-2006
(Humboldt-Universität zu Berlin, NaFöG).
OGUNJI, J.O.: Evaluation of Housefly Maggot Meal as an alternative protein
source for tilapia (Oreochromis niloticus); supervisor: KIRSCHBAUM, F. :
2005-2006 (AvHumboldtstiftg., Georg-Forster-Stip.)
OSMAN, A.: Der Einfluss von Schwermetallen auf die molekularen und
morphologischen Veränderungen im Embryo- und Larvenstadium des
afrikanischen Welses; supervisor: KIRSCHBAUM, F.: 2004-2006
(Ägyptische Regierung).
PEUTHERT, A.: Physiologische Reaktion von Alfa Alfa auf Exposition mit
cyanobakteriellen Toxinen; supervisor: PFLUGMACHER, S.: 2005-2008
(Freie Universität Berlin, NaFöG).
RYCHLA, A.: Verbesserung der Wasserqualität in thermisch geschichteten
Seen; supervisor: KOSCHEL, R.: 2006-2007 (Deutsche Bundesstiftung
Umwelt).
SERGELEN, G.: Trophic state, classification and management of Mongolian
lakes; supervisor: KOSCHEL, R.: 2006-2007 (DAAD).
© IGB 2007
183
4.7 Summary
Gesamtübersicht
Number
4.1
Peer-reviewed papers in
international journals
4.2
Non-reviewed papers, books, book
chapters and reports
4.3.1 Master Theses
122
87
17
4.3.2 PhD Theses
7
4.3.3 Pre-Professional Theses
1
4.4
Lectures at Universities
University
Humboldt-Universität zu Berlin
4.6
Number of IGB
lecturers
16
Freie Universität Berlin
1
Universität Bremen
1
Technische Universität Dresden
2
Universität Oldenburg
1
Universität Osnabrück
1
Universität Potsdam
4
University of Kalmar
1
Projects*
€ in 2006
EU-projects
136.200
DFG-projects
454.700
Federal institution projects
941.400
Other
977.600
Total
2.509.900
* incl. fremdverwaltete Mittel
184
4.8 List of published IGB reports
Liste der bisher veröffentlichten Berichte des IGB
Hrsg.: IGB, Berlin.
ISSN 1432-508X
© IGB 2007
Heft 1
Behrendt, H. & Opitz, D.
Ableitung einer Klassifikation für Gewässergüte von planktondominierten
Fließgewässern und Flussseen im Berliner Raum und güteklassenbezogene
Zielvorgaben zur Nährstoffreduzierung im Berliner Gewässersystem.
1996. 91 S.
Heft 2
Gelbrecht, J. et al.
Stoffeinträge in Oberflächengewässer und Stoffumsetzungsprozesse in
Fließgewässern im Einzugsgebiet der Unteren Spree als Grundlage für
Sanierungskonzepte.
1996. 148 S. (vergriffen)
Heft 3
Prochnow, D. et al.
Schweb- und Schadstoffe der unteren Spree 1994-1996, Modellierung und
Simulation des dynamischen Verhaltens von Schwebstoffen in eutrophen
Fließgewässern.
1997. 127 S.
Heft 4
Jahresforschungsbericht 1996.
1997. 289 S.
Heft 5
1998. 166 S.
Heft 6
Sonderheft I
Proceedings of the Workshop on Order Theoretical Tools in Environmental
th
Sciences, held on November, 16 , 1998 in Berlin.
1998. 117 S.
Heft 7
Sonderheft II
Zusammenfassungen der Beiträge des 13. Treffens deutschsprachiger
DiatomologInnen mit internationaler Beteiligung vom 25. bis 28. März 1999.
1999. 208 S.: mit CD.
Heft 8
1999. 208 S.: mit CD.
Heft 9
Ausgewählte Forschungsergebnisse aus dem IGB zum Themenkreis „Einfluss
von Eingzugsgebietscharakteristika auf die Wasserbeschaffenheit von
Oberflächengewässern in Brandenburg.
1999. 170 S.
Heft 10
Annual Report 1999.
2000. 234 S.
Heft 11
Pusch, M. et al.
Ökologisch begründetes Bewirtschaftungskonzept für die Spree unter dem
Aspekt der bergbaubedingten Durchflussreduktion.
2001. 244 S.
185
186
Heft 12
Sonderheft III
Casper, P., et al.
Stechlinsee-Bibliographie.
2001. 85 S.
Heft 13
Annual Report.
2001. 238 S.
Heft 14
Pudenz, S. et al.
Proceedings of the Workshop on Order Theoretical Tools in Environmental
Science and Decision Systems, held on November 6 th -7 th 2001 in Berlin.
2001. 224 S.
Heft 15
Annual Report 2001.
2002. Internet: www.igb-berlin.de.
[Erschienen nur als CD-ROM.]
Heft 16
Schauser, I. et al.
Seeinterne Maßnahmen zur Beeinflussung des Phosphor-Haushaltes
eutrophierter Seen. Leitfaden zur Auswahl eines geeigneten Verfahrens.
2003. 106 S.: mit CD-ROM.
Heft 17
Annual Report 2002.
2003. 127 S.
Heft 18
Arlinghaus, R.
Angelfischerei in Deutschland – eine sozialökonomische Analyse.
2004. 160 S.
Heft 19
Pusch, M. et al.
Die Elbe – Gewässerökologische Bedeutung von Flussbettstrukturen
The River Elbe – ecological importance of channel morphology
2004. 304 S.
Heft 20
Annual Report 2003.
2004. 206 S.
Heft 21
Mehner, T. et al.
Entwicklung einer leitbildorientierten Methode zur Bewertung des ökologischen
Zustands von Seen anhand der Fischfauna.
2004. 202 S.
Heft 22
Annual Report 2004.
2005. 214 S.
Heft 23
Annual Report 2005.
2006. 215 S.

Untitled

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