SRMT Mussels - Saint Regis Mohawk Tribe

Transcription

Freshwater Mussel Status Report
Habitat, Populations, Reproduction and Contaminant Assessment In
and Near the Massena/Akwesasne St. Lawrence River Area of Concern
(AOC) for Beneficial Use Impairment (BUI) Advancements
USEPA GLRI Project ID: GL-97221310
Prepared by:
Lee H. Harper
Riveredge Associates
J. Mark Erickson
St. Lawrence University
and
Jessica L. Jock
Saint Regis Mohawk Tribe Environment Division
November 2015
STATUS REPORT - FRESHWATER MUSSELS IN AND NEAR AOC
Suggested citation: Harper L.H., J.M. Erickson, and J.L. Jock. November 2015. Freshwater mussel
status report: habitat, populations, reproduction and contaminant assessment in and near the
Massena/Akwesasne St. Lawrence River Area of Concern (AOC) for Beneficial Use Impairment
(BUI) advancements. GL-97221310. 99 pp.
2
EXECUTIVE SUMMARY
Data were gathered in and near the Massena/Akwesasne Area of Concern (AOC) to assist with
the evaluation of Beneficial Use Impairments (BUI) for freshwater mussels in a project funded
by a U.S. Environmental Protection Agency (USEPA) grant (GL-97221310) to the St. Regis
Mohawk Tribe (SRMT) through the Great Lakes Restoration Initiative (GLRI). A Quality
Assurance Project Plan (QAPP) was developed and an Interim Status Report completed from
2012 qualitative surveys to identify data gaps and guide the 2013 investigations. Field work was
conducted during summer and fall 2013 to investigate freshwater mussel populations,
reproduction, and contaminants.
This study is relevant to 3 BUIs within the AOC: restriction on fish and wildlife consumption,
degradation of fish and wildlife populations, and degradation of benthos. 2013 Field surveys
were conducted in the Grasse, St. Regis, and Raquette Rivers by snorkel and scuba at 19 sites; 7
inside the AOC and 12 outside and upstream of the AOC to examine mussel populations and
reproduction. The 7 sites (segments) surveyed inside the AOC represent 5.7% of the total
number of river segments inside the AOC. Thirteen of the 19 total sites had information on
mussel presence and abundance from previous surveys conducted between 1991and 2006
Erickson 9 to 23 years earlier, although 11 of these sites were upstream and outside the AOC,
and only two were inside the AOC. There were no surveys conducted in the St. Lawrence River
in 2013. The 2013 surveys identified 13 species of mussels in and adjacent to the AOC,
including five (5) New York State Species of Greatest Conservation Need.
Mussel communities inside and outside the AOC in the Grasse, Raquette, and St. Regis Rivers
had similar species richness at the 19 survey sites across all three rivers. Compared to earlier
Erickson surveys, species richness was generally slightly higher in 2013 than in previous studies.
Two new native species are now present inside the Grasse River AOC that were not found 17
years ago, although this could be due in part to greater sampling effort. Across all rivers, the
Grasse River has the highest species richness (n=13) and perhaps the least understood mussel
fauna of rivers surveyed inside and outside the AOC. Zebra mussels continue to threaten native
unionid mussels in the lower reaches of the rivers, near the confluence of the main stem St.
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Lawrence River backwater influence, in particular American Veterans Campground (AmVets)
site on the lower Grasse River.
At most sites, mussels were found to represent a broad array of age classes from 1 year old to 20
or more years of age based on counts of external rings. Gravid individuals of several species
were found inside and outside the AOC and in each of the three tributary rivers. Combined, these
data suggest largely stable mussel populations and the occurrence of successful reproduction and
recruitment, except in areas of zebra mussel.
Thirty composite mussel samples of five individual Elliptio complanata were collected from the
tributary rivers of the AOC and analyzed for contaminants (aluminum, cadmium, lead, mercury,
organochlorine pesticides, fluoride, dioxins/furans, PCB congeners, and PAHs); 15 samples
inside the AOC and 15 samples outside (upstream) of the AOC. Not all samples could be run for
all tests due to sample mass limitations. No pesticides, PAHs, nor fluoride were detected in any
samples. With the three rivers combined, total PCBs inside the AOC were significantly higher
than total PCBs outside the AOC. Two dioxins (HpCDD and OCDD) and one furan (TCDF)
were also significantly higher inside the AOC than outside the AOC. No other contaminants
were significantly different inside versus outside the AOC when the data were pooled among
rivers.
Across all rivers inside the AOC (only), total PCBs were significantly highest in the Grasse
River. Total PCBs were not detected inside the AOC from the St. Regis River. The furan TCDF
was also significantly highest in the Grasse River inside the AOC. Across all rivers outside the
AOC, there were no significant differences in contaminant concentrations. Contaminant levels in
2013 were similar or lower to mussel tissue collected in the AOC from 1983 to 1991. Although
97% of mussels collected (n=38) on the St. Lawrence and Ottawa Rivers in 1985 had DDE, no
DDE was detected in any sample in 2013.
While consumption of mussels was not examined by EPA’s human health risk assessment for the
Grasse River, the average PCB concentrations for mussels inside the AOC on the Grasse River
exceed the EPA remedial goal of 10 ng/g for fish tissue PCB concentrations to be protective of
Mohawk health. Average PCB concentrations inside the AOC for the Raquette and St. Regis
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Rivers, and for all three rivers outside the AOC, do not exceed this level, although 3 of 12
samples from the Raquette River did.
For protection of wildlife which may consume aquatic organisms, New York State Department
of Environmental Conservation advises a limit of 110 ng/g PCBs. This threshold was exceeded
in 2013 inside the AOC for the Grasse River only.
Further field studies are necessary to identify any occurrence of rare, threatened or endangered
species, and to determine the impacts of lower Grasse River remediation on the freshwater
mussel community. Mussels appeared to be more common in shallow nearshore areas with
emergent and submergent aquatic vegetation, although this is a general qualitative impression
that needs to be supported with additional field surveys. Such surveys would also identify the
extent of zebra mussel infestation. Full restoration of the freshwater mussels and the habitats
they depend on will be a necessary part of Grasse River remediation activities, and restored
BUIs.
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TABLE OF CONTENTS
EXECUTIVE SUMMARY................................................................................................. 3
TABLE OF CONTENTS .................................................................................................... 6
LIST OF FIGURES ............................................................................................................. 8
LIST OF TABLES .............................................................................................................. 8
LIST OF PHOTOS .............................................................................................................. 9
LIST OF ABBREVIATIONS ........................................................................................... 10
ACKNOWLEDGMENTS ................................................................................................ 11
1.0
INTRODUCTION ...................................................................................................... 12
1.1
BACKGROUND AND OBJECTIVES ................................................................ 12
1.2
FRESHWATER MUSSELS OF THE AOC ........................................................ 18
1.3
PREVIOUS STUDIES OF FRESHWATER MUSSELS IN THE AOC ..................... 24
1.4
AOC REMEDIATION SUMMARIES ............................................................... 25
1.4.1
1.4.2
2.0
3.0
GENERAL REMEDIATION SUMMARY .............................................. 25
SITE SPECIFIC RIVER SEDIMENTS, BANK, AND/OR WETLAND SOIL
REMEDIATION SUMMARIES ............................................................ 26
METHODS .............................................................................................................. 31
2.1
STUDY AREA ............................................................................................. 31
2.2
STUDY GOALS AND OBJECTIVES ............................................................... 33
2.3
2012 QUALITATIVE MUSSEL SURVEYS ...................................................... 34
2.4
2013 FIELD SURVEY METHODS.................................................................. 34
2.5
2013 SAMPLING DESIGN ............................................................................ 35
2.6
CONTAMINANT SAMPLE COLLECTION METHODS....................................... 39
RESULTS AND DISCUSSION..................................................................................... 41
3.1
ACHIEVEMENT OF DATA QUALITY OBJECTIVES IN THE FIELD ................... 41
3.2
SPECIES OF MUSSELS ................................................................................. 44
3.3
MUSSEL POPULATIONS .............................................................................. 49
3.4
3.3.1 2013 MUSSELS INSIDE AND OUTSIDE THE AOC............................. 49
3.3.2 2013 DATA COMPARED TO EARLIER STUDIES ............................... 53
REPRODUCTION.......................................................................................... 62
3.5
CONTAMINANTS ......................................................................................... 69
3.5.1
3.5.2
3.5.3
QUALITY ASSURANCE AND QUALITY CONTROL ............................ 69
DATA TREATMENT ......................................................................... 70
RESULTS ........................................................................................ 70
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4.0
3.5.4 COMPARISON WITH OTHER STUDIES ............................................... 72
3.5.5 IMPLICATIONS FOR HUMAN CONSUMPTION..................................... 84
LESSONS LEARNED ................................................................................................ 86
5.0
RECOMMENDATIONS .............................................................................................. 87
6.0
REFERENCES ..................................................................................................... 91
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LIST OF FIGURES
Figure 1. Map of Massena/Akwesasne AOC ...................................................................... 32
Figure 2. Map of 2013 survey sites for populations and contaminants .............................. 43
LIST OF TABLES
Table 1. AOC Beneficial Use Impairments, Status, and Delisting Criteria ........................ 17
Table 2. Freshwater mussel species of the AOC and their status ....................................... 22
Table 3. Number of survey segments targeted for 2013 population surveys by river ........ 37
Table 4. Number of mussel samples for 2013 contaminant analysis by river .................... 40
Table 5. Number of sites surveyed in 2013 for mussels by river ....................................... 41
Table 6. Sites surveyed for 2013 populations and reproduction ......................................... 42
Table 7. Species of mussels identified in the 2012-2013 studies ....................................... 48
Table 8. Number of species, individuals, and mussels collected in 2013 per search hour . 51
Table 9. Presence of positively identified live individuals at each 2013 survey site……..52
Table 10. Number of mussels collected by Normandeau (2008) and this study (2013) ..... 57
Table 11. Number of sites historically surveyed and resurveyed by Erickson .................. 57
Table 12. Number of species, individuals, and mussels collected per search hour ............ 61
Table 13. Age of Elliptio complanata and other mussels at each 2013 sampling site ....... 66
Table 14. Presence of gravid individuals at each 2013 survey site .................................... 67
Table 15. List of contaminants detected and not detected in 2013 mussels surveys .......... 76
Table 16. Contaminants in mussels inside and outside the AOC ....................................... 77
Table 17. Contaminants in mussels from the Grasse River ................................................ 78
Table 18. Contaminants in mussels from the Raquette River ............................................. 79
Table 19. Contaminants in mussels from the St. Regis River ............................................ 80
Table 20. Contaminants in mussels from three rivers inside the AOC ............................... 81
Table 21. Contaminants in mussels from three rivers outside the AOC ............................. 82
Table 22. Historical concentrations of contaminants in mussels from the AOC ................ 83
Table 23. Rivers and areas where mussels are below the remedial goal for fish tissue ..... 85
Table 24. Potential locations for long term trend monitoring............................................. 90
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LIST OF PHOTOS
Photo 1. Mussel surveys were conducted with scuba and surface supplied air .................. 37
Photo 2. Mussels were collected, measured, and returned to the river ............................... 38
Photo 3. Mussels were collected and sorted by species and size ........................................ 47
Photo 4. The number of mussels at one site was much greater than historically ............... 58
Photo 5. Potamilus alatus in the lower Grasse River varied in size and age ...................... 59
Photo 6. Zebra mussels were found on several species in the lower Grasse River ............ 60
Photo 7. Mark Erickson examining a mussel for identification.......................................... 65
Photo 8. A gravid Potamilus alatus showing marsupial gills with larval mussels ............. 65
Photo 9. A gravid Potamilus alatus from the Grasse River ................................................ 68
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LIST OF ABBREVIATIONS
List of abbreviations used in documents related to the Massena/Akwesasne Area of Concern. Not
all of the abbreviations listed here appear in this document.
Alcoa Inc.
AOC
ASTM
BUI
COCs
COSEWIC
CPUE
DDT
GLNPO
GLWQA
GM
GRLI
HS
IJC
MCA
ND
NELAC
NOAA
NTCRA
NYNHP
NYPA
NYSDEC
NYSDOH
OMNR
PAHs
PCBs
PCDD
PCDF
POCs
QAPP
RACER Trust
RI/FS
ROD
SLRRP
SRMT
SRMTED
TDBF
USEPA (EPA)
USFWS
USGS
VOCs
Aluminum Corporation of America
Area of Concern
American Society for Testing and Materials
Beneficial Use Impairment (Indicator)
Contaminants of Concern
Committee and the Status of Endangered Wildlife in Canada
Catch Per Unit Effort
Dichlorodiphenyltrichloroethane
Great Lakes National Program Office
Great Lakes Water Quality Agreement
General Motors
Great Lakes Restoration Initiative
Hot Spots
International Joint Commission
Mohawk Council of Akwesasne
Non-detect
National Environmental Laboratory Accreditation Conference
National Oceanic and Atmospheric Administration
Non-Time Critical Removal Action
New York Natural Heritage Program
New York Power Authority
New York State Department of Environmental Conservation
New York State Department of Health
Ontario Ministry of Natural Resources and Forestry
Polycyclic aromatic hydrocarbons
Polychlorinated biphenyls
Polychlorinated dibenzodioxins
Polychlorinated dibenzofurans
Persistent organochlorine chemicals
Quality Assurance Project Plan
Revitalizing Auto Communities Environmental Response Trust
Remedial Investigation and Feasible Study
Record of Decision
St. Lawrence River Remediation Project (Alcoa East)
Saint Regis Mohawk Tribe
Saint Regis Mohawk Tribe Environment Division
Total dibenzofurans (used in SLRRP ROD)
United States Environmental Protection Agency
United States Fish and Wildlife Service
United States Geological Survey
Volatile organic compounds
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ACKNOWLEDGMENTS
This report, prepared on behalf of Saint Regis Mohawk Tribe Environment Division (SRMTED),
contains field data collection and technical writing contributions from Riveredge Associates and
Dr. J. Mark Erickson, with chemical analysis of mussel tissue by PACE Analytical Laboratories.
Technical direction, field audits, oversight of the field activities, and contributions and edits of
this report was provided by SRMTED. The work was funded by a grant from the U.S.
Environmental Protection Agency (USEPA) (GL-97221310) to the St. Regis Mohawk Tribe
(SRMT) through the Great Lakes Restoration Initiative (GLRI).
SRMTED Staff Amberdawn LaFrance provided contaminant data from the SRMT database to
Riveredge Associates for data synthesis, reporting, and comparison. Members of the Akwesasne,
Massena, and Louisville communities assisted by providing access to the rivers that were
surveyed in the field. Riveredge biologists Joel Danko, Anna Butler, and Michael Reynolds
conducted the mussel collections in the field; William Votra assisted. Christopher Baird
summarized the contaminant data and prepared text and tables for the report. Map figures were
prepared by Bill Olsen. Some mussels were sent out for verification of field identifications. Dave
Strayer, Lisa Holst, Matt Schlesinger, Erin White, Lyubov Burlakova, and Isabel Hannes all
assisted with the verification of field identifications.
A license to collect and possess freshwater mussels for the SRMT investigation into BUIs of the
AOC was obtained from the New York State Department of Environmental Conservation
(NYSDEC). This license permitted the temporary collection of mussels for population surveys
and the collection of Elliptio complanata for contaminant analysis. In addition, this license
specifically requested that mussels be collected and vouchered for the collections of NYSDEC
and the New York State Museum.
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1.0
INTRODUCTION
1.1
Background and Objectives
The international section of the St. Lawrence River was identified as one of five Bi-National
Areas of Concern (AOC) by the International Joint Commission (IJC) under the 1987 amended
Great Lakes Water Quality Agreement (GLWQA). The Bi-National geographic boundary is
delineated as, “The St. Lawrence River Area of Concern (AOC) includes the waters from the
Moses-Saunders power dam to the eastern outlet of Lake St. Francis, including the area
upstream of the Snell lock and power dam to the Massena public water supply intake, the Grasse
River from the mouth upstream to the first dam, the Raquette River from the mouth upstream to
the New York State Route 420 bridge and the St. Regis River from the mouth upstream to the
dam at Hogansburg. This includes water shared by the United States, Canada, and the
Mohawks of Akwesasne” (Environment Canada et al. 1994). The boundaries of interest under
this Great Lakes Restoration Initiative (GLRI) funded project (GL-97221310) are the upstream
and southern portion of the International St. Lawrence River Area of Concern (AOC), primarily
located in St. Lawrence County and the Mohawk Territory of Akwesasne (also called the St.
Lawrence River AOC at Massena and/or Massena/Akwesasne AOC). The Massena/Akwesasne
AOC includes the Grasse (04150304), Raquette (04150305), and St. Regis (04150306)
tributaries, Power Canal on the Grasse River, and portions of the St. Lawrence River itself.
The Massena/Akwesasne AOC was identified due to discharge of hazardous substances and
industrial byproducts to nearby tributaries, land, and the St. Lawrence River itself, thus causing
ecological impairments and impaired water quality. Contaminants of concern in the
Massena/Akwesasne AOC associated with industry facility releases include: polychlorinated
biphenyls (PCBs), polycyclic aromatic hydrocarbons (PAHs), dioxins, furans, cyanide, fluoride,
phenols, volatile organic compounds (VOCs), ammonia, styrene, phenols, sulfate, mercury and
metals (aluminum, lead, cadmium). Organochlorine pesticides of concern in the
Massena/Akwesasne AOC include chlordane, dichlorodiphenyltrichloroethane (DDT), dieldrin,
endrin, and hexachlorobenzene, and mirex. Mercury is a contaminant of concern in both the
Cornwall St. Lawrence River AOC (Cornwall AOC) and in the Massena/Akwesasne AOC due to
some contribution from Massena industry and atmospheric deposition within the watershed.
12
In addition to the presence of these contaminants, the channel of the lower Grasse River was
dredged over 100 years ago, deepening (up to 14 feet or more) and widening (100-300 ft) the
natural channel to facilitate power production and industrial operations (Alcoa 2012). More
recent navigational dredging occurred at the mouth for the construction of the St. Lawrence
Seaway in the 1950’s. These chemical and physical habitat changes inside the
Massena/Akwesasne AOC have likely had an impact on freshwater mussels, a sediment dwelling
invertebrate important for overall ecosystem health, water quality, and food sources to multiple
species, including humans historically.
Several efforts have been made to remediate contamination sources and improve water and
sediment quality in and around the AOC between 1995 and 2009. Remediation efforts have been
implemented at the three hazardous waste sites, Alcoa East (former Reynolds Metal Company
(RMC)), Alcoa West, and GM (see remediation summaries below) but the Grasse River remains
a source of a large mass of contaminated sediment in the AOC. The United States Environmental
Protection Agency (USEPA 2012b, 2013a) has selected a Grasse River remedy to mitigate risks
to the biota, fish, human and ecological receptors that includes the dredging of nearshore
contaminated sediments and capping of main channel contaminated sediments.
Marine and freshwater mussels have been used to monitor contaminants in U.S. coastal and
Great Lakes waters. Started in 1986 nationally and in the Great Lakes in 1992, the Mussel Watch
program represents the longest continuous running contaminant monitoring program in the
United States (NOAA 2014). Mussel Watch supports environmental management through
monitoring and assessment of environmental quality (NOAA 2014). Mussel tissue is analyzed
for over 100 organic and inorganic contaminants and maintained in a comprehensive database
(NOAA 2014). In the Great Lakes, the Mussel Watch program analyzes non-native dreissenid
mussels, but there are no sampling stations below the Moses-Saunders Power Dam located
within the AOC.
Monitoring contaminants in mussels is important because contaminants may affect the
reproductive health of marine or freshwater mussels and the survivorship of mussel glochidia
(Hellou et al. 2003, Gagné and Blaise 2003, Gagné et al. 2004, Yeats et al. 2008). The
freshwater mussel family Unionidae has emerged as a critical group for contaminant monitoring
13
in the field over the past 20 years (Farris and Van Hassel 2007). Hellou et al. (2003) investigated
biological indicators of mussel health during gametogenesis in marine mussels, and Gagné et al.
(2004) examined the same in freshwater mussels. Caged mussel studies have been conducted in
the St. Lawrence River using Elliptio complanata downstream of a municipal effluent plume.
These studies found a complex pattern of responses that could lead to harmful health effects
including disruption of reproduction (Gagné et al. 2004).
Wide-spread contaminant exposure from industrial waste and agricultural production is
considered one of the major threats to healthy freshwater mussel populations throughout North
America (Strayer et al. 2004). However, complex life-histories and synergistic effects of
potential stressors (e.g. habitat degradation, exotic species introductions, and water pollution)
have made it difficult to determine specific negative toxicity effects thresholds in freshwater
mussels (Keller and Ruessler 1997, Augspurger et al. 2003, Milam et al. 2005). Additionally, the
majority of studies that have evaluated specific contaminant toxicity thresholds are laboratory
based and are difficult to relate to natural populations, but Cope et al. (2008) have shown that
laboratory-based studies can represent wild mussel populations in certain cases. Another
important concern is that contaminant-specific toxicity thresholds vary substantially by species
and life-history stage (Cherry et al. 2002).
Contaminant toxicity to freshwater mussels has been the subject of emerging research in the last
decade but much work remains to be done. Some species appear to be highly sensitive while
others less so. Some studies suggest that water quality criteria might need to be revised to afford
protection of freshwater mussels (March et al. 2007). In some cases, mussels may be very
sensitive and the inclusion of freshwater mussels in regulatory standards could significantly
change criteria (USEPA 2010, Hall 2010). For some contaminants, such as pesticides and other
organic compounds, mussels may be less sensitive than species traditionally used for
toxicological reference (Keller and Augspurger 2005). For other contaminants, such as metals
and ammonia, mussels may be more sensitive (Keller and Augspurger 2005). Current water
quality standards may not be protective of sensitive life stages of freshwater mussels and new
standards will need to be developed (e.g., Cope et al. 2008, Hall 2010, USEPA 2010, Wang et al.
2011, ASTM 2013, USGS 2013). Toxicity testing has focused primarily on the early life stages
14
of freshwater mussels including glochidia and juvenile mussels in water-only exposures; future
toxicity tests may be conducted with adult freshwater mussels as well (ASTM 2013).
Because almost no data are available to directly assess the impact of local industrial pollutants on
the growth, reproduction, and survival of freshwater mussels, this study examined current mussel
populations and compared them to population assessments conducted in the same region
approximately 20 years ago.
This freshwater mussel study is one of several in the Massena/Akwesasne AOC designed to
make progress on Beneficial Use Impairments (BUIs): Restrictions on Fish and Wildlife
Consumption, Degradation of Fish and Wildlife Populations, and Degradation of Benthos (Table
1). Freshwater mussel populations may have been impacted by persistent organochlorine
chemicals (POCs) and other compounds released through discharges.
Criteria for the Restriction of Fish and Wildlife Consumption include documentation that
contaminant levels in mussels do not exceed current standards for human consumption. The
current status of this BUI is “Impaired” with no surveys conducted to date to compare mussel
contaminant burdens inside and outside the AOC.
Criteria established for Degradation of Fish and Wildlife Populations include documenting
healthy and reproducing populations and a community structure that does not significantly
diverge from unimpacted sites that would be expected from the amount of quality of suitable
physical, chemical, and biological habitat characteristics. The current status of this BUI is
“Unknown/Needs Further Assessment” with no surveys conducted to date to compare mussel
populations inside and outside the AOC. While this project was underway, the Remedial
Advisory Committee (RAC) evaluated and revised the delisting criteria for this BUI. The new
criteria was approved by the RAC on June 18, 2014 and include the following:
-
-
Concentrations of contaminants (particularly PCBs) in AOC fish and wildlife are not
significantly higher than levels found outside of the AOC; OR concentrations of
contaminants found in AOC fish and wildlife are below toxicity reference values, established
criteria to protect piscivorous wildlife, or adverse effect levels documented in scientific
literature.
Native wildlife species richness and diversity (including resident birds, amphibians, reptiles,
and freshwater mussels) in AOC wetland and riverine habitats is equal to or greater than that
15
-
found in similar habitats in the surrounding region.
Bald eagle, mink, lake sturgeon, otter, or other sentinel species are present and successfully
reproducing in the AOC.
Criteria established for the Degradation of Benthos include no significant difference between the
community structure of sites within the AOC and unimpacted sites upriver. The current status of
this BUI is “Unknown/Needs Further Assessment,” with no surveys conducted to date to
compare mussel community structure inside and outside the AOC.
In 2012, qualitative field surveys for freshwater mussels and their habitats were completed and
the findings reported in a Freshwater Mussel Interim Status Report (Harper and Jock 2014). The
2013 field studies, the subject of this report, were designed to investigate contaminant burdens in
the tissues of freshwater mussels in and near the Massena/Akwesasne AOC, and the potential
effects of these contaminants on freshwater mussel presence and distribution. Freshwater mussel
tissues were collected and tested for contaminant burdens, and field surveys of mussel species,
ages, and catch per hour (or catch per unit effort (CPUE)) were conducted to provide information
on populations and reproduction.
These surveys were conducted to gather information useful to make progress on the delisting
criteria of multiple BUIs. The results of those field surveys are reported in this Status Report.
16
Table 1. St. Lawrence River, Massena/Akwesasne AOC Beneficial Use Impairments, Status and
Delisting Criteria
Beneficial Use
Impairment
Restriction on Fish
and Wildlife
Consumption
Degradation of
Fish and Wildlife
Populations1
Status
Impaired
Delisting Criteria
Measurement
Restrictions on fish and wildlife consumption in
the AOC due to watershed or in-place
contaminants are absent. No public health
advisories are in effect for human consumption
that are due to watershed or AOC specific sources;
AND
Quantitatively measure
contaminant burden in tissue
(PCBs, organochlorine
pesticides (chlordane, DDD,
DDE, DDT, Dieldrin, Endrin,
Hexachlorbenzene, and mirex),
mercury, metals, fluoride, and
dioxin/furans)
Contaminant levels created by anthropogenic
chemicals due to watershed or in-place
contaminants do not exceed current standards,
objectives, or guidelines in resident fish and
wildlife; AND
Any remaining restrictions on fish and wildlife
consumption are due to upstream or downstream
sources that are addressed by other management
plans, such as Lakewide Management Plans
(LaMPs).
Environmental conditions support healthy, selfsustaining communities of desired fish and
wildlife at predetermined levels of abundance that
would be expected from the amount and quality of
suitable physical, chemical, and biological habitat
present; AND
Unknown/
Needs
Further
Assessment Fish populations meet applicable Index of
Biological Integrity (IBI) and wildlife populations
have healthy reproducing populations of eagle,
mink, otter, or other species.
Degradation of
Benthos
Unknown,
needs
further
assessment
Benthic macroinvertebrate community structure
does not significantly diverge from unimpacted
control sites of comparable physical and chemical
characteristics; AND
In the absence of community structure data, the
toxicity of sediment-associated contaminants is
not significantly higher than controls at
unimpacted sites.
Compare chemical analysis
data to Fish and Wildlife
Consumption Advisories.
Use data to assist update to
Mohawk Consumption
Advisory and Traditional
Pathways and Uses Restoration
Use quantitative chemical data
of tissue burden to compare to
adverse health effects threshold
levels
Collect comparable # of
samples from upstream river
locations within the same body
of water.
Use quantitative chemical data
of tissue-associated
contaminant burden to
determine impairment to
community structure, and
compare impacted and
unimpacted sites.
Review secondary data
sediment database to cross
reference sediment-associated
contaminants at impacted and
unimpacted sites.
Collect comparable # of
samples from upstream river
locations within the same body
of water.
Notes: 1Delisting Criteria listed here was used to design study (E&E 2008). Updated criteria was
approved by the RAC on June 18, 2014 during the drafting of this report.
17
1.2
Freshwater Mussels of the AOC
Freshwater mussels are found around the world in rivers, streams, lakes and ponds. There are
approximately 1,000 freshwater mussel species worldwide and North America is home to almost
300 of these species. Approximately 70 of North America’s freshwater mussels are either
endangered or threatened, and several species have already gone extinct (USFWS 2014). Threats
to their survival come from a variety of sources such as loss of habitat, water degradation, and
impoundments.
Industrial contaminants have implications for human consumption of freshwater mussels.
Freshwater mussels were traditionally harvested and consumed and have important cultural
significance for Native American tribes (Garvin 2005). The earliest wampum was believed to
have been made by the shells of freshwater mussels, drilled and polished with stone tools (Nature
Bulletin 1972). A string of wampum from freshwater mussels plays a significant role in the first
Longhouse Condolence Ceremony, and oral history of the Creation of the Haudenosaunee
Confederacy (Mohawk, Oneida, Onondaga, Cayuga, Seneca, and Tuscarora), and the Great Law
of Peace through the story of Aionwatha (Hiawatha) (NAITC 1984). In later periods, wampum
was made by the quahog shell and today by plastic beads, but there is oral evidence through the
Peacemaker story of earliest wampum made from freshwater mussels. Wampum is interwoven
throughout Mohawk and Haudenosaunee history and culture including but not limited to;
identification of those who hold chief and clan mother titles, use as jewelry, artifacts, art,
ceremonies, and wampum belts as historical records and treaties.
Freshwater mussels play an important role in the ecosystem. They provide ecological services in
water clarification, nutrient recycling, and as a food source for other organisms (USFWS 2014).
Mussels are filter-feeders, meaning they pass water over their gills filtering out particles that can
be ingested. As a result, they remove not only food particles but also inorganic and organic
compounds, some of which can be toxic to the mussel. Freshwater mussels are excellent
biomonitors for the AOC due to their well-known ability to burrow in the sediment and
accumulate contaminants from the water column and particulate matter (i.e. filter-feeding) and
thus reflect local contaminants in the environment (Richman et al. 2013).
18
Freshwater mussels in the AOC are a food source to lake sturgeon and multiple aquatic furbearer
mammals such as otter, mink, and muskrat. An intricate relationship exists between mussels and
fish, as mussels use fish as a host to assist reproduction and distribution in a watershed by
releasing glochidia (fertilized eggs) into the gills of fish for transport and survival of juveniles,
until they detach and fall to the stream bed (USFWS 2014). If a fish host is threatened,
endangered, or can no longer access spawning habitat, this impediment may affect freshwater
mussel recovery and/or reproductive success in the St. Lawrence River watershed. An example
of this intricate relationship may be demonstrated by the lack of post-1970’s records of
Hickorynut (Obovaria olivaria) in the St. Lawrence River in New York State. Strayer and Jirka
(1997) list this species as otherwise historically widely distributed in large rivers in the
Mississippi, Great Lakes, and St. Lawrence basins. Lake sturgeon (Acipenser fulvescens) a New
York State listed Threatened fish species, is assumed to be its fish host in the St. Lawrence River
basin (Bouvier et al. 2013). Evidence of Hickorynut populations have been recently identified in
the Ottawa River and in the St. Lawrence River downtstream of Montreal, Canada (Bouvier et al
2013). Recovery of this species in the St. Lawrence River basin and associated tributaries may
be dependent on habitat quality and the overlap of sufficient numbers of both species to ensure
completion of the Hickorynut’s reproductive cycle.
Very few field surveys for mussels have been conducted in or near the Massena/Akwesasne
AOC. The surveys that have been conducted suggest that the two most abundant species of
freshwater mussels in and near the AOC are Elliptio complanata and Lampsilis radiata
(Erickson and Fetterman 1996, Normandeau 2008, Harper and Jock 2014, Erickson, personal
communication). E. complanata has been considered a sentinel species for monitoring pollutant
impacts (Won et al. 2005), and has been used to monitor contaminants at several Great Lakes
AOCs for many years (Kauss and Hamdy 1985, Richman et al. 2011).
Surveys for mussel species presence and absence have previously been conducted inside and
upstream of the AOC by Erickson (2001, 2003), Erickson and Fetterman (1995, 1996, 1997),
Erickson and Garvey (1997), Fetterman and Erickson (1996), Normandeau (2008, 2009), and by
Harper and Jock (2014). In total, over 20 species of freshwater mussels could potentially occur in
the vicinity of the AOC, although some are known only from historical records and may no
longer be present (Table 2) (Natural Resource Trustees of the St. Lawrence River Environment
19
2013, Erickson and Fetterman 1996, Harper and Jock 2014). Of these species, eleven (11) are
listed in New York State as Species of Greatest Conservation Need. These species are
A.ligamentina, A. marginanta, A. varicosa, L. cariosa, L. ovata, L. ochracea, L. recta, L. nasuta,
M. margaritifera, P. alatus, and V. iris.
Surveys conducted by Erickson and Fetterman (1996) identified fifteen (15) species, with two
additional species recorded with question, from the Grasse River drainage. Prior to these studies,
only two species, L. recta and L. cariosa, had been formally recognized in the Grasse River. The
species identified in Erickson and Fetterman (1996) included: Anodonta grandis, A. cataracta,
Anodontoides ferussacianus, Strophitus undulatus, Alasmidonta undulata, A. marginata, Elliptio
complanata, Lasmigona compressa, L. subviridis (?), Lampsilis radiata, L. ovata, L. cariosa,
Leptodea ochracea (?), Ligumia recta, L. nasuta, Villosa iris and Margaritifera margaritifera.
Note, the genus Anodonta is synonymous with Pyganodon (Pyganodon grandis and Pyganodon
cataracta). Erickson later stated that Leptodea ochracea and Villosa iris are questionable, and
the Lasmignoa subviridis was probably a Lasmigona compressa (Normandeau 2009). Those
clarifications were based on examination of specimens by Strayer (personal communication from
Erickson, 2015). Erickson also clarified (Jock, personal communications 2015) the three (3)
specimen assigned as L. nasuta at the AmVets site were later changed to E. complanata
identification. A dead L. nasuta shell from Sucker Brook was identified by Dave Strayer, and is
illustrated in the Key to Unionacean Clams (Mollusca) of the Grasse River Drainage, St.
Lawrence County, New York (Erickson and Garvey 1997). The misidentification adjacent the
AmVets site does not preclude L. nasuta potential from being present in the Grasse River.
Normandeau conducted surveys in 2007, 2008, and 2009 in the Grasse River, adjacent the Power
Canal working upstream to Louisville, NY. During the 3-years of survey, nine (9) mussel
species were found; Elliptio complanata, Lampsilis ovata, L. radiata, L. cariosa, Lasmigona
costata, Ligumia recta, Pydanodon cataracta, Alasmidonta marginata, and Strophitus undulatus.
(Normandeau 2009)
Survey results from 2012 reported 10 species occur in or near the AOC: Alasmidonta marginata,
Elliptio complanata, Lampsilis cariosa, L. ratiata, L. ovata, Leptodea fragilis, Ligumia recta,
Potamilus alatus, Strophitus undulatus, and Pyganodon cataracta (Harper and Jock 2014). The
20
number of species that may have occurred historically in and near the AOC is unknown, but was
likely greater. No mussel data are available for the area prior to 1991, and nothing is known
about the historical abundance, species richness, or distribution of mussels in the region. Our
knowledge of the abundance and distribution of freshwater mussel species in the region increases
with each new survey effort.
21
Table 2. Freshwater mussel species potentially occurring in and near the AOC and their conservation status.
Scientific Name
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
Actinonaias ligamentina 1
Alasmidonta marginata
Alasmidonta undulata
Alasmidonta varicosa
Anodontoides ferussacianus
Elliptio complanata
Lampsilis cariosa
Lampsilis ovata
Lampsilis radiata
Lampsilis siliquoidea2
Lasmigona compressa
Lasmigona costata
Leptodea fragilis
Leptodea ochracea
Ligumia recta
Ligumia nasuta
Margaritifera margaritifera
Obovaria olivaria 3
Potamilus alatus
Pyganodon cataracta
Pyganodon grandis
Strophitus undulatus
Villosa iris
Common Name
Mucket
Elktoe
Triangle Floater
Brook Floater
Cylindrical papershell
Eastern elliptio
Yellow lampmussel
Pocketbook
Eastern lampmussel
Fat mucket
Creek heelsplitter
Fluted shell
Fragile papershell
Tidewater mucket
Black sandshell
Eastern pondmussel
Eastern pearlshell
Hickorynut
Pink heelsplitter
Eastern floater
Giant floater
Creeper
Rainbow
Totals
New
York
Status4
Species of
Greatest
Conservation
Need (SGCN) in
New York5


Species of New
England
Conservation
Concern
(Therres, 1999)
 (HP)

SC
SC



SC
SC
T
COSEWIC6
Ontario
Status7
Quebec
Status8
SARA
Status
9
*10

*10
 (HP)
 (HP)




E
E
E
E
E
T
3(2 E, 1
T)

 (HP)
1
11
E=Endangered, T = Threatened, SC = Special Concern, HP= high priority
COSEWIC = Committee and the Status of Endangered Wildlife in Canada
22
5
5 (3 E,2 SC)
E
*10
*10
4
*likely
E
4 (2 E,
2 SC)
Notes:
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
This species previously reported as occurring in the AOC but further research indicates it is not known to occur in the AOC.
L. siliquoidea may be present based on recent 2013 field surveys, however preliminary results have not been confirmed.
This species is considered historical (SH) in New York State.
New York Status: http://www.dec.ny.gov/animals/7494.html
SGCN Status: http://www.dec.ny.gov/docs/wildlife_pdf/sgnc2015list.pdf
COSEWIC October 2014 Status: http://www.cosewic.gc.ca/eng/sct0/rpt/csar_fall_2014_e.pdf
Ontario Status: https://www.ontario.ca/environment-and-energy/species-risk-ontario-list
Quebec Status: http://www3.mffp.gouv.qc.ca/faune/especes/menacees/liste.asp
SARA Status: http://www.registrelep-sararegistry.gc.ca/species/schedules_e.cfm?id=1
*Listed as “likely” to be designated threatened or vulnerable
23
1.3
Previous Studies of Freshwater Mussels in the AOC
PCBs and other contaminants can affect health in freshwater mussels, potentially including
reproductive impairment. Data for contaminant levels in freshwater mussel species in the
Massena/Akwesasne AOC are lacking. Most collections of freshwater mussels in or near the
AOC date from the late 1980s when the New York State Department of Environmental
Conservation (NYSDEC) targeted wildlife for study in the area surrounding Massena industrial
sites but no samples were collected in upstream reference areas outside the AOC (NYSDEC
1990; TAMS 2001; WWC 1992). Also in the mid-1980s, Metcalfe and Charlton (1990) collected
freshwater mussels in the vicinity of the AOC in small numbers. These mussels were shown to
have elevated levels of contaminants of concern (COC) compared to upstream sites.
A few individuals of Elliptio complanata and Lampsilis radiata have been tested for
contaminants in and near the Massena/Akwesasne AOC. NYSDEC (1990) reported that one
Lampsilis radiata collected in the St. Lawrence River offshore of General Motors contained up
to 680 ng/g (ppb) PCBs, while a conspecific collected upstream at Cape Vincent had no
detectable PCBs. NYSDEC’s criteria for protection of wildlife which may consume aquatic
organisms is 110 ng/g PCBs (Newell et al, 1987). Metcalfe and Charlton (1990) collected
Elliptio complanata and Lampsilis radiata from 17 sites on the St. Lawrence River between
Lake Ontario and Trois Riviéres Quebec in 1985. Mussels were tested for organochlorine
pesticides, PCBs and other compounds. One mussel (Lampsilis radiata) was collected at the
mouth of the Grasse River and another (also Lampsilis radiata) was collected downstream of the
AOC in Akwesasne. Both had elevated levels of PCBs compared to reference sites. Metcalfe and
Charlton (1990) concluded that the Grasse River was a major source of PCB contamination in
the St. Lawrence River system, and the Massena, NY industries were a source of transboundary
pollution to Lac Saint-Francois, Quebec.
Mussels from within and upstream of the AOC, collected from the St. Lawrence and Raquette
Rivers, have also been tested for PCBs, fluoride, aluminum, and cyanide (Woodward-Clyde
Consultants [WCC] 1992). In general, levels of aluminum, fluoride, cyanide, and PCBs were
higher in mussels collected from areas near Alcoa East (WCC 1992) than in Pollys Gut.
24
Aluminum and fluoride were also higher in mussels at the Raquette River station influenced by
Alcoa East releases.
1.4
AOC Remediation Summaries
1.4.1
General Remediation Summary
A principal goal of the Revised Great Lakes Water Quality Agreement of 1978, as amended by
Protocol signed November 18, 1987 (1987 GLWQA) is to restore the chemical, physical, and
biological integrity of the Great Lakes Ecosystem in the Areas of Concern (AOCs) (IJC 1987).
Primary contaminants of concern in the Bi-National St. Lawrence River AOC include:
polychlorinated biphenyls (PCBs), polyaromatic hydrocarbons (PAHs), chlorinated pesticides
(including mirex and hexachlorobenzene), dioxins, furans, and metals (Environment Canada et
al., 1994).
While many remedial successes and contaminant mass reductions (i.e. PCBs, PAHs, dioxins, and
metals) have contributed to the restoration of the Massena/Akwesasne AOC since 1995 on the
United States side, excessive levels and inventory of PCBs can still be found in sediments in the
Grasse River Superfund Site. Fish tissue concentrations are elevated, and fish and wildlife
advisories are still in effect in the Massena/Akwesasne AOC. Health risks to Mohawks have
been identified through epidemiological studies and subsistence/cultural exposure routes, and
NYSDOH had issued a Special Consumption Advisories for the Akwesasne Mohawk Nation
specific to lake sturgeon and other game consumption (Forti et al. 1995).
Between 1995-2013, a number of remedial efforts have taken place at the Massena, NY
Industrial facilities (i.e. Alcoa West, RACER formerly known as General Motors, and Alcoa
East formerly known as Reynolds Metals) to contribute to reduction of contaminant mass and/or
exposure, contaminated fish tissue concentrations and its associated human and ecological risk
reduction, and ecological restoration. The land-based remediation of eighteen contaminated sites
at Alcoa West and six contaminated sites at Alcoa East (former Reynolds Metals) was completed
in 2001, and fulfills the requirements of the two 1992 Record of Decisions (RODs) for these
sites. GM land remediation and demolition for revitalization was conducted by RACER Trust
25
(http://www.racertrust.org/files/massena-marketing-brochure.pdf ). Plant demolition began in
2011 and was completed in 2014. Remediation of site sources is proposed to be completed in
2015. Long-term groundwater remediation and monitoring of the “GM Dump” is currently
underway.
1.4.2
Site Specific River Sediments, Bank, and/or Wetland Soil
Remediation Summaries
St. Lawrence River – Alcoa East Plant (Formerly Reynolds Metal Company (RMC))
Through 1989-1992 remedial investigations and feasibility studies (RI/FS) of the St. Lawrence
River adjacent to Alcoa East were conducted with PCB-contaminated sediments identified as the
primary contaminants of concern (COCs). Other contaminants identified as present at the site
included furans, fluoride, aluminum, cyanide, and PAHs found in similar patterns of PCBs at this
site on the St. Lawrence River. USEPA issued a 1993 Record of Decision (ROD) that called for
dredging of sediments containing contaminants in excess of 1mg/kg (ppm) PCBs, 10 mg/kg
total PAHs, and 1 ug/kg (ppb) of total dibenzofurans (TDBFs). This area of contamination was
21.8 acres. In 2001 the St. Lawrence River Remediation Project (SLRRP) dredging commenced
following those prescribed clean-up goals to remove 86,000 cubic yards (cy) of contaminated
sediments (20,200 lbs of PCBs) in a dredge design divided into 268 “dredge cells” (avg. 0.08
acres each). The ROD estimated 28% of the contaminated sediment inventory on-site included
PCBs ≥ 25 mg/kg, with 9 identified Hot Spots (HS) Units delineated into 0.06 acres (2,500ft2
areas) with PCBs ≥ 500 mg/kg (USEPA 1993, USEPA 2008, USEPA 2012a).
After completion of 2001 dredging efforts, post-dredging verification sampling demonstrated a
site-wide average PCB concentration of 0.8 mg/kg PCBs, a 98.6% PCB contaminant reduction.
All but 12 of the 268 dredge cells achieved target PCB clean-up goal of 1.0 mg/kg PCBs; those
12 cells were capped in 2009 to achieve assumed 100% PCB clean-up goal achievement for risk
reduction.
26
A 90% reduction in PAHs was achieved in 2001, and additional verification sampling conducted
between 2002-2006 indicated 76 of the 268 dredge cells were above the 10 mg/kg total PAHs
clean-up goal. Fifty-three dredge cells indicated total PAHs >20 mg/kg with a maximum
concentration detection at D-118 of 741 mg/kg in fall 2002. In addition to dredge cell D-118, 5
additional dredge cells indicated > 100 mg/kg total PAHs at 285, 241, and 244, 181, and 112
mg/kg for dredge cells A-7, A-16, C-39, D-117, and D-126 respectively. All 53 dredge cells with
PAHs> 20 mg/kg were capped in 2009. Twenty-three cells indicated PAHs between 10-20
mg/kg, and these were assumed to have naturally degraded with time due to low molecular
weight PAH degradation period (~3years) (USEPA 2008).
On the 21.8 acre contaminated site, 3.5 acres were capped for achievement of risk reduction
goals associated with PCBs and total PAHs. A 100% achievement of clean-up targets for TDBFs
was achieved via 2001 dredging and 2009 capping (USEPA 2008).
St. Lawrence River –Former General Motors, Central Foundry Division (GM)
The USEPA issued a Record of Decision for the General Motors (Central Foundry Division) for
Operable Unit 01 in December 1990. The ROD outlined several major areas for soil remediation
of the North and East disposal areas and industrial landfill; sludge and liquid remediation in four
unlined industrial lagoons (350,000 gallon, 500,000 gallon, 1.5 million gallon, and 10 million
gallon lagoons); contaminated sediments, riverbanks, and associated wetlands of the St.
Lawrence River, Raquette River, and Turtle Creek; and contaminated Tribal property and
contaminated groundwater (with groundwater flow north and northeast to the St. Lawrence River
and Turtle Creek, respectively). Contaminants of concern identified during the 1988 RI/FS at the
GM Site include PCBs, PAHs, phenols, and volatile organic compounds (VOCs). PCBs were
detected at highest concentrations and frequency, and therefore drove remediation at this site.
The ROD identified over 62,000 cy of contaminated river sediments and soil with PCB
concentrations above 1 mg/kg located in and along the St. Lawrence River, Raquette River and
Turtle Creek (with majority of contaminated sediments ~56,000 cy in St. Lawrence River
adjacent to the facility) (USEPA 1990).
27
During RI/FS the highest concentration of PCBs detected was 5,700 mg/kg, and PAHs up to 8.0
mg/kg. The 1995 dredging activity on the St. Lawrence River removed 18,000 cy of
contaminated sediment. A 1.72-acre cap was placed over the areas that did not achieve the 1.0
mg/kg PCB clean-up goal (USEPA 2013b, 2015)
General Motors, Raquette River and bank soils
During RI/FS the highest PCB concentration detected in the Raquette River was 390 mg/kg. In
2002, river bank and sediment removal efforts removed 11,000 cy of soils and 1,400 cy of
sediment with respective 10 mg/kg PCB and 1.0 mg/kg PCB clean-up goals successfully
achieved.
General Motors, Turtle Cove and associated wetlands/uplands
During RI/FS, approximately 15,000 cy of soil >1 mg/kg PCBs was identified to be located on
adjacent Tribal Mohawk Property (highest concentration reported of 48 ppm). NYSDEC
detected PCBs concentrations as high as 3,101 mg/kg in Turtle Creek, with at least 4 samples
>100 mg/kg PCBs.
In 2003, 4,600 cy of highly contaminated soils between the Northeast Industrial Landfill and the
Cove were removed. By spring 2005, 18,000 cy of PCB-contaminated sediment and soils from
the cove area were excavated in the dry to achieve Mohawk clean-up standard of 0.1 mg/kg
PCBs. The sediment clean-up goal was based on the 1989 Saint Regis Mohawk Tribal Council
Resolution (No. 89-19) promulgated sediment standards for Mohawk territory protection of
human and ecological health.
An estimated 700 cy of soils still need to be remediated on Mohawk Upland Properties (soils)
with a clean-up goal of 1.0 mg/kg PCBs. Historic samples range from 1.0-10.0 mg/kg PCBs.
28
Grasse River – Alcoa West Plant
USEPA issued an Administrative Order to ALCOA, Inc. in September 1989 to investigate the
nature and extent of hazardous toxic material in the lower Grasse River, Unnamed Tributary,
Robinson Creek, and the Power Canal. The lower Grasse River underwent remedial investigation
and feasibility studies (RI/FS) from 1990-2013 when a Record of Decision (ROD) was issued in
April 2013. Remedial design and pre-monitoring are proposed for 2014, with implementation
expected in 2015-2020 (USEPA 2013a).
In 1995, EPA required Alcoa to conduct a Non-Time Critical Removal Action (NTCRA) due to
significantly elevated PCB sediment concentrations in the lower Grasse River identified adjacent
to Outfall 001. Removal of ~3,000 cubic yards (cy) of contaminated sediment, boulder, and
debris comprising of PCB concentrations ranging from 12 mg/kg-11,000 mg/kg, representative
of about 20% (8,000 pounds (lbs)) of the total PCB mass in the river was conducted. PCB
average sediment surface concentrations were reduced from 518 to 75 mg/kg (1.1-260 mg/kg
range post-dredge sampling) in 1995 (BBL 1995, USEPA 2012b, USEPA 2013a).
In 1998, 10,650 cy of PCB-containing sediments were removed from the Unnamed Tributary,
and disposed of in the on-site Secure Landfill.
In most years from the mid-1990s until currently, water column monitoring in the lower Grasse
River has been conducted spring through fall. Data trends indicate seasonal patterns with highest
concentrations in summer, and lowest in late fall and noticeable decreases over the years (i.e.
115-130 ng/L (ppt) in the mid-90s to 8-20 ng/L in 2011 with background concentrations of 0.23.0 ng/L). Power canal concentrations averaged 7.9 ng/L in 1998 and 1.9 ng/L in 2002 (USEPA
2012b).
In 2005, a Remedial Options Pilot Study (ROPS) was conducted to evaluate cost and
implementation feasibility of multiple remedial options. An 8-acre area was targeted by Transect
7 (T7) for main channel dredging of sediments ranging from non-detect (ND) to 3,668 mg/kg
PCBs (with highest concentration at 3.5 ft sediment depth, and a pre-dredge average surface
concentration of 3.8 mg/kg). A maximum volume of 75,000 cy was proposed for removal. Of
that, only 24,400 cy was removed, with 84% of PCB mass targeted successfully removed, but
29
with increased post-dredge average surface concentrations (138 mg/kg) due to difficulty from
debris and/or hard bottom preventing access to clean underlying material. This area was capped,
with post-cap average concentrations of 7.4 mg/kg, a 95% reduction in post-dredge conditions
(Alcoa 2005, 2006).
Additional river sediment investigations conducted 1995-2010 identified highest PCB
concentrations at depth, and widely distributed throughout the 7.2 river mile stretch. Current
conditions indicate approximately 1.7 million cy of sediment with PCBs ≥ 1mg/kg over a 325
acre area exist as remaining inventory in the lower Grasse River (USEPA 2012b). The 7.2 river
mile study area is broken down by 0.1 mile transect (T1-T72), and main channel and nearshore
(water depths of five feet or less during normal summer flow). Current PCB-laden sediment
concentration ranges are summarized below:
•
•
•
•
ND-3,106 mg/kg PCBs in the Main Channel (T1-T21),
ND-3,070 mg/kg PCBs in the Nearshore (T1-T21),
ND-1,063 mg/kg PCBs in Main Channel (T21-T72),
ND- 313 mg/kg PCBs in the Nearshore (T21-T72)
The 2013 Record of Decision by USEPA calls for 109,000 cy of nearshore PCB-contaminated
sediment ≥ 1 mg/kg to be removed, with clean back-fill to grade for nearshore T1-T72 (7.2
miles), a 59-acre armored cap within the upper 2-river miles, and over 225-acres of sand/natural
cap over remaining 5-river miles of main channel with PCB concentrations ≥ 1mg/kg.
Site-wide remedial action is based on PCBs only, however initial sediment investigations for
Baseline Ecological Risk Assessment also detected VOCs, PAHs, dioxin, furans, aluminum,
arsenic, fluoride, and lead in lower Grasse River sediments at variable concentrations and
locations (TRC 1993). Due to the widespread distribution of PCBs throughout the site, it is
assumed that by remediating the PCB contamination, all other contaminants bioavailable at site
will be remediated as well. EPA established several remedial action objects. These included a
0.01 mg/kg PCB fish tissue remedial goal designed to be protective of Mohawk health from fish
ingestion for the lower Grasse River (USEPA 2013a), and minimize PCB bioavailability of
PCBs in sediments to the biota (including benthos such as freshwater mussels).
30
2.0
METHODS
2.1
Study Area
The Investigation Area included the Massena/Akwesasne AOC tributaries, Grasse, Raquette and
St. Regis Rivers, and comparable river miles upstream of each river for comparison. For further
detail of comparable sampling segment, see QAPPs (Riveredge 2012, 2013a, and 2013b) and
Figures 2:8 in Freshwater Mussel Interim Status Report (Harper and Jock 2014). A map of the
AOC is depicted in Figure 1 below.
31
Figure 1. Map of Massena/Akwesasne AOC.
32
2.2
Study Goals and Objectives
The goal of the 2013 field work was to gather data that would help determine if healthy, selfsustaining populations of freshwater mussels were present inside and outside the AOC by determining
the species present, the number of individuals of each species as measured through catch per unit
effort (CPUE), and the age, sex, and presence of gravid individuals among the freshwater mussels
collected. To assess chemical characteristics of benthos and consumption restrictions in the AOC,
contaminant burden was measured to Elliptio complanata inside the AOC compared to outside the
AOC.
Data Objectives for 2013 Qualitative Mussel Surveys:
1. Select sites based on 2012 qualitative habitat work
2. Conduct semi-quantitative field surveys to describe mussel abundance and richness based on
timed searches
3. Determine the age, sex, length, height, and width of a subsample (≥20 individuals) of all
mussels
4. Examine mussels for evidence that they are gravid and reproducing
5. Report on the current status of mussels and their habitat inside and outside the AOC.
Data Objectives for 2013 Assessment of Mussel Contaminant Burden:
1. Collect freshwater mussels for contaminant testing during late summer or fall of 2013.
2. Samples from the AOC and upstream (outside AOC) reference sites will be submitted for
contaminant analysis [PCB-congeners, mercury, pesticides, dioxins/furans, metals (Pb, Cd,
Al), and fluoride]. All samples collected will be labeled, documented, and processed for
shipment to the lab for analysis within appropriate holding times.
3. Conduct chemical analysis of tissues by Pace Analytical Services utilizing USEPA Method
8082 Comprehensive for PCBs, USEPA Method 7471B for Mercury, USEPA Method 8081B
for Pesticides, USEPA Method 1613B for PCDDs and PCDFs, USEPA Method 6010B for
metals, and USEPA Method 300.0 Mod for fluoride.
33
4. Compare contaminant concentrations in freshwater mussel tissues to published literature and
to toxicity thresholds (where available).
2.3
2012 Qualitative Mussel Surveys
Qualitative 0.5 hr surveys in the nearshore shallows were conducted in 2012 (Harper and Jock 2014).
A total of 116 river segments were qualitatively surveyed for mussels in the Grasse, Raquette, St.
Regis and St Lawrence Rivers. Half the river segments were within the AOC and half were outside
the AOC. A maximum of 10 species were documented during the study across all rivers surveyed.
The most species collected live were taken from the Grasse (5); the most species live or dead from the
Raquette (7). The results of the 2012 sampling was used to design the semi-quantitative sampling
conducted in 2013.
2.4
2013 Field Survey Methods
Two Quality Assurance Project Plans (QAPP) were prepared for 2013 mussel surveys. The first was
an amendment to the QAPP prepared for fall 2012 qualitative habitat surveys conducted inside and
outside the AOC (Riveredge 2012). This QAPP was amended in August 2013 for semi-quantitative
sampling of mussel surveys using timed searches at sites inside and outside of the AOC (Riveredge
2013a). The work plan outlined in the QAPP for 2013 field work was based on the results of the 2012
qualitative habitat surveys. Note, no field survey was proposed in the St. Lawrence River for 2013 due
to lack of mussels found in 2012. In addition to the QAPP Amendment (Riveredge 2013a), a separate
QAPP was prepared for freshwater mussel Elliptio complanata collection and analysis for assessment
of contaminant burden (Riveredge 2013b).
Some of the sites selected included sites that had been previously sampled 15-20 years ago by Dr. J.
Mark Erickson of St. Lawrence University (Erickson and Fetterman 1996, Erickson unpublished
data). These sites were surveyed again in 2013 to determine if the population metrics (species, age) of
freshwater mussels have changed over time. These data will assist with the determination of whether
or not freshwater mussels are successfully reproducing inside and outside the AOC.
34
Measurements were made of all specimens, or a selected range of specimens (usually 20) if the
species was abundant (e.g. Elliptio complanata), and included valve length, height and width. These
were made using digital calipers or a measuring device provided by Erickson with an accuracy of
±0.25mm. Mussels were aged by counting external growth rings. If possible without damaging or
injuring the mussel, the valves of female mussels were gently pried open to look for evidence that the
mussel might be gravid (e.g. inflated marsupial gills). Most, but not all females were checked. All
members of the subfamily Lampsilinae are dimorphic; thus all species of Lampsilis, Ligumia,
Leptodea, and Potamilus were examined. Alasmidonta marginata, Pyganodon species, Strophitus
undulatus, and Anodontoides ferussacianus are thin-shelled and may damage upon prying open, so not
all were checked. Elliptio complanata was abundant at all sites, assumed to be reproducing
successfully, and generally not gravid in summer months, therefore not checked in the interest of time.
After measurement and examination, mussels were returned to the river alive. A few specimens were
collected as voucher specimens at the request of NYSDEC and New York Natural Heritage Program
for deposit in the State Museum collections.
Data were summarized in tabular form including species, species numbers, survey time, site number,
tables of measurements, and reproductive condition. Data were summarized and presented by
drainage and location.
2.5
2013 Sampling Design
Semi-quantitative mussel sampling was conducted at sites inside and outside of the AOC. For
population surveys, a minimum of seven sampling sites were targeted inside the AOC and seven
sampling sites outside the AOC for a total of 14 sites (Table 3). These sampling sites were selected
from a total of 246 total sampling segment sites, made up of 84 segments on the Grasse River, 130
segments on the Raquette River, and 32 segments on the St. Regis River (Figure 2). In total, the field
sampling surveys for populations were conducted on 5.7% of the river segments inside and outside the
AOC (Table 3; Figure 2). Priority sites were those for which Erickson could provide data from his
previous work. For contaminant surveys, 30 samples were targeted to be spatially representative of the
AOC and upstream areas (Table 4).
35
A wide range of survey methodologies exist for sampling freshwater mussels, including qualitative,
semi-quantitative and quantitative techniques (Cvancara 1972, Hornbach and Deneka 1996, Miller
and Payne 1993, Obermeyer 1997, Strayer, Claypool and Sprague 1997). Strayer et al. (1997) showed
that random quadrat sampling can miss species whose population densities are less than 0.1/m2 unless
more than 10 person-hours of search is conducted. When faunal surveys are desired, Erickson (pers.
comm) believes that the most effective method is a timed survey reporting species numbers per
person-hours of survey time. This method was employed throughout Erickson’s earlier studies and
was therefore repeated in the present work.
In-stream collection involved both visual and tactile examination of bottom sediments by a team of
waders, snorkelers and divers using both scuba and surface supplied air (Air Line hookah rig) and the
recovery of all mussels discovered (Photo 1). Total search time at each site ranged from 1.0 to 1.5
person-hours. Surveys included areas of nearshore, slope, and main channel habitats. Specimens
were returned to shore in mesh bags for identification and measurement (Photo 2). All species
identifications were verified in the field by J. Mark Erickson, while some mussels were sent out for
verification of field identification assisted by Dave Strayer, Lisa Holst, Matt Schlesinger, Erin White,
Lyubov Burlakova, and Isabel Hannes. A few specimens were vouchered at the request of the
NYSDEC and sent to NYSDEC and the New York State Museum for verification of identifications.
36
Table 3. Number of survey segments targeted for 2013 population surveys by river.
River
Segments
Outside
AOC
Total
Segments
Segments
Inside
Surveyed
AOC
by River
Total River
Segments
Percent of
Total River
Segments
Surveyed
Grasse River
3
3
6
84
7.1%
Raquette River
2
2
4
130
3.1%
St. Regis River
2
2
4
32
12.5%
Total Sites or
Segments
7
7
14
246
5.7%
Photo 1. Mussel surveys were conducted by scuba and surface supplied air.
37
Photo 2. Mussels were collected, measured, and returned to the river.
38
2.6
Contaminant Sample Collection Methods
To assess contaminant burdens in freshwater mussels, samples of Elliptio complanata, the dominant
species, were collected from sites inside and outside the AOC for each tributary river (St. Regis,
Raquette, and Grasse) during the late summer and early fall of 2013. Because qualitative field surveys
of mussels populations and habitat in the fall of 2012 (Harper and Jock2014) failed to locate native
mussels in the St. Lawrence River in sufficient numbers to support sampling, no animals were
collected from the main stem St. Lawrence River.
Mussels (Elliptio complanata) were visually located and collected for contaminant analysis in each of
the targeted locations. Mussels were collected using latex gloves, rinsed in the river, measured in the
field (mm), and placed in whirlpak or resealable plastic bags. These bags were placed in a cooler with
ice for transport. A Sample ID was assigned to each sample collected. The Sample ID included a two
character code for the river (e.g. GR for Grasse River, RR for Raquette River, SR for St. Regis River),
a 1 letter code for inside or outside the AOC (D for downstream or in the AOC and U for upstream or
outside the AOC), a 2 number code for the river segment, a 3-letter Month, and six digit day and year
of collection, and the identification of the species collected for analysis EC – Elliptio complanata. A
complete sample code would appear as GRD12SEP192013EC. Since all mussels collected were
Elliptio complanata, the last two letters for species were dropped to save space.
Each contaminant sample was a composite of five individuals. To the extent possible, these five
animals were of approximately equal size, and all individuals were at least five years old. Age was
determined by counting the annual growth rings on the outside of the shell. Samples were frozen until
shipped overnight to Pace Analytical.
Fifteen composite samples were collected inside the AOC and 15 composite samples were collected
outside the AOC (Table 4). Of the 15 total samples collected inside or outside the AOC, six samples
were collected from the Grasse River, six from the Raquette River, and three from the St. Regis River
(Table 4). Sites were selected on each of the tributary rivers based on the results of the investigation of
populations and habitat conducted in the fall of 2012 (Harper and Jock 2014). Specific segment
numbers were targeted where mussels were known to be the most abundant, while trying to maintain
39
some separation of sample sites as well as distribute them among each river reach approximately
equidistantly for adequate spatial representation.
The location of all samples was recorded in the field with a Garmin GPS 76 handheld global
positioning receiver.
All samples were to be tested for PCB congeners, mercury, pesticides, PCDDs, PCDFs, PAHs, metals
(Al, Pb, Cd) and fluoride.
Table 4. Number of mussel samples1 for 2013 contaminant analysis by river.
Samples
Inside
AOC
Samples
Outside
AOC
Total
Samples
Mussels
per
Sample
Total Mussels
(inside and outside
AOC)
Grasse
6
6
12
5
60
Raquette
6
6
12
5
60
St Regis
3
3
6
5
30
St. Lawrence2
0
0
0
0
0
Total
15
15
30
River
150
1
Each sample is a composite of five individual mussels of approximately equal size
2
No mussels collected for contaminant analysis based on limited availability in 2012.
40
3.0
RESULTS AND DISCUSSION
3.1
Achievement of Data Quality Objectives in the Field
The data quality objectives required that 30 mussel contaminant samples be collected, 15 inside the
AOC and 15 outside the AOC, distributed spatially among the three rivers of the AOC (Table 4;
Figure 2). These 30 samples were collected and sent to the laboratory for analysis.
The data quality objectives required that 14 sites be surveyed for populations and reproduction with
equal numbers inside and outside the AOC (Riveredge 2013). At the completion of field work, 19
sites had been surveyed, exceeding the data quality objectives of the QAPP (Table 5). The locations of
these survey sites are indicated in Table 6.
Table 5. Number of sites surveyed in 2013 for mussels by river.
Proposed
Completed
River
Sites
Outside
AOC
Sites
Inside
AOC
Total Sites
Sites
Outside
AOC
Sites
Inside
AOC
Total Sites
Grasse River
3
3
6
6
3
9
Raquette River
2
2
4
2
2
4
St. Regis River
2
2
4
4
2
6
7
7
14
12
7
19
Total Sites
41
Table 6. Sites surveyed for 2013 populations and reproduction.
Drainage
and Date
Erickson
River Segment
Historical
(this study)
Site No
GRASSE RIVER
9/18/2013
A495
9/18/2013
A481
9/16/2013
A572
9/16/2013
A502
8/15/2013
A581
8/15/2013
A1026
9/19/2013
NA
9/19/2013
NA
8/14/2013
A1025
RAQUETTE RIVER
9/16/2013
A2403
8/13/2013
A2265
8/16/2013
A2266
NA
8/16/2013
ST. REGIS RIVER
Site Location
Latitude
Longitude
GRU99
GRU98
GRU43
GRU22
GRU11
GRU02
GRD12
GRD18
GRD39
Madrid boat launch
Chase Mills bridge
Louisville bridge
Massena Rod and Gun Club
Rt. 37 bridge
Massena Memorial Park, Fire Station
GR near Dennison Rd.
Rt. 131 Bridge.
American Veterans campground
N 44.74808
N 44.84841
N 44.89906
N 44.91280
N 44.92200
N 44.93288
N 44.95050
N 44.95463
N 44.97940
W 75.12901
W 75.07670
W 75.01590
W 74.95770
W 74.92738
W 74.89466
W 74.85694
W 74.83800
W 74.77987
RRU38
RRU01
RRD18
RRD42
Raymondville Rt. 56 bridge
Massena Springs
RR near O'Neil RoadRR east of Haverstock Rd.
N 44.84629
N 44.91608
N 44.93106
N 44.96828
W 74.97709
W 74.89054
W 74.83094
W 74.75890
N 44.92396
N 44.92288
N 44.94660
N 44.97081
N 44.99574
N 44.99783
W 74.72302
W 74.72691
W 74.69820
W 74.66959
W 74.64954
W 74.64234
SRU99
9/20/2013
A1705
Rt. 53 north of Brasher Center
SRU98
9/11/2013
A1702
Nevin Road below old bridge
SRU16
9/11/2013
A1704
North Road where close to west bank
SRU02
9/11/2013
NA
Mohawk School
SRD12
9/17/2013
NA
Tom White Rd Hogansburg
SRD14
9/17/2013
NA
SR near mouth
NA = not applicable as not surveyed historically.
- = Site upstream and outside of the river segments delineated for this study
42
Figure 2. Map of 2013 survey sites for mussel populations and contaminants.
43
3.2
Species of Mussels
Field surveys conducted in 2012 and 2013 identified 13 species of mussels inside and outside the AOC
(Table 7, Photo 3). The Grasse River had the richest freshwater mussel fauna with 13 species, followed
by the St. Regis River with 10 species and the Raquette River with 8 species (Table 7). Only one
species was found in the St. Lawrence River in 2012, and this was represented by only a single
individual Lampsilis radiata found on the shore of an island opposite the mouth of the Raquette River,
raising the possibility that it could have been transported downstream from the Raquette during a high
flow event. No other native mussels were found in the St. Lawrence River at the nearshore sites
surveyed in 2012, and 2013 survey was limited to the tributaries of the AOC.
No state-listed threatened or endangered species were found but five species are considered Species of
Greatest Conservation Need in New York (Table 7) (NYSDEC 2015).
Overall, Elliptio complanata remains the dominant cosmopolitan unionoid in main stem North Country
rivers. Lampsilis radiata and Lampsilis cariosa remain co-dominants in second and third place
numerically.
Two species, Potamilus alatus and Leptodea fragilis, were not previously known from the Grasse or
St. Regis rivers prior to surveys conducted in 2012 and 2013. Results found Potamilus alatus: 2 sites
in St. Regis age 4-6, n=2; 3 sites in lower Grasse, age 3-17, n=40; Leptodea fragilis: 3 sites lower
Grasse age 3-11, n=12; 1 site St. Regis age 6-7, n=2. These two species are most common in the lower
gradient, softer substrate sections of the Grasse River and St. Regis River inside the AOC. They are not
known to occur in the gravelly or rocky reaches upstream and outside the AOC, and probably do not
occur there. It is also possible that these species have long been present but were only located through
more survey effort. Erickson felt that he would have found them at the American Veteran's
campground site on the Grasse River if they were there during his early surveys between 1991 and
1996. This change in community structure could have occurred in the last two decades.
Anodontoides ferussacianus was found in low numbers in the Grasse, Raquette and St. Regis rivers
during this study. This species was not previously known from the lower reaches of these rivers,
although had been recorded in the upper reaches by Erickson and Fetterman (1996).
44
One individual of Lasmigona costata was found in the Raquette and one in the Grasse during this
study, and had not been found in the lower reaches of these rivers before. This species is relatively rare
wherever it occurs, although it was known from the upper reaches of these rivers previously (Erickson,
personal communication). Single specimens were also collected in a couple of locations upstream of
the AOC between the Main Street Bridge and the Massena Rod and Gun Club (Normandeau 2008).
The two species of Pyganodon (formerly Anodonta), cataracta and grandis, are typical of slow moving
waters where they were found in the lower Grasse River in areas that had not been searched in
previous years. P. cataracta was previously documented from the stretch of the Grasse River between
the Main Street bridge and the Rod and Gun Club (Normandeau 2008).
All mussels collected were identified in the field and verified by Erickson. Some species were sent out
for further verification of these field identifications. Mussels were hand carried to the New York
Natural Heritage Program (NYNHP) and NYSDEC for examination and later will be placed in the
collections of the New York State Museum. One mussel that was thought might possibly be
Actinonaias ligamentina was sent to NYNHP for verification and identified as L. radiata.
Actinonaias ligmentina is known to occur in Ontario.
Mussels that appeared phenotypically to be Lampsilis siliquoidea were found in the Grasse, Raquette,
and St. Regis Rivers, although Strayer and Jirka (1997) report no L. siliquoidea from northern New
York. The distinction between L. siliquoidea and L. radiata is the focus of research in progress by
doctoral student Isabel P. Hannes at the State University of New York at Buffalo working with Dr.
Lyubov Burlakova at Buffalo State College. Hannes is analyzing DNA samples from several sites in
North America to investigate the phylogenetic relationship of these species. Preliminary results suggest
that two mussels collected from the Grasse River may have L. siliquoidea haplotypes (i.e.,
particular DNA sequence; Hannes 2014) although additional tests and statistical analyses need to be
performed to determine the significance of this finding. Following the established practice of Strayer
and Jirka (1997), all these mussels have been considered to be Lampsilis radiata in this report.
However, Lampsilis siliquoidea was also included in our list of species (Table 7), with qualification,
because some individual mussels appeared phenotypically as this species. Future work by Hannes will
shed further light on the taxonomy of this group and the distinction between these species.
45
Overall, the river reaches inside the AOC and outside the AOC had similar species richness, although
the species in the mussel community may be different in areas where the waters of the AOC are lowgradient, low-flow, and dominated by softer substrates than in the higher gradient higher flow areas
upstream and outside the AOC. In particular, Potamilus alatus and Leptodea fragilis occur in the lower
reaches of the Grasse River and St. Regis River but not in the upper reaches where substrates have
more sand, gravel, and cobble. In addition, the two species of Pyganodon are much more common in
low flow rivers, and more common inside the AOC than outside and upstream.
46
Photo 3. Mussels were collected and sorted by species and size. After examination, mussels were
returned to the river at the same site.
47
Table 7. Species of mussels identified in the 2012-2013 studies.
Scientific Name
Common Name
St.
Lawrence
River
Raquette
River
St. Regis
River
1
Alasmidonta marginata2
Elktoe
X
X
X
2
Anodontoides ferussacianus
Cylindrical papershell
X
X
X
3
Elliptio complanata
Eastern elliptio
X
X
X
4
Lampsilis cariosa2
Yellow lampmussel
X
X
X
5
Lampsilis ovata2
Pocketbook
X
X
X
6
Lampsilis radiata
Eastern lampmussel
X
X
X
Lampsilis siliquoidea1
Fat mucket
7
Lasmigona costata
Fluted shell
X
X
8
Leptodea fragilis
Fragile papershell
X
9
Ligumia recta2
Black sandshell
X
10
Potamilus alatus2
Pink heelsplitter
X
11
Pyganodon cataracta
Eastern floater
X
12
Pyganodon grandis
Giant floater
X
13
Strophitus undulatus
Creeper
X
X
Totals by River
1
Grasse
River
1
13
X
X
X
X
X
8
10
Recent DNA evidence on at least one individual animal (2013) suggests this genetic haplotype is present in the AOC (Hannes 2014). However, preliminary
results have not been confirmed. The current status report treats L. siliquoidea as L. radiata following Strayer and Jirka (1997).
2
NYSDEC Species of Greatest Conservation Need (SGCN)
48
3.3
Mussel Populations
Mussel populations were assessed by the number of species, number of individuals, and the number
collected per search hour (catch per unit effort or CPUE) found during timed searches. Across all
segments of all three rivers (Grasse, Raquette, St. Regis), timed searches identified three to seven
species of mussels at each site and 40 to 620 individual mussels collected per search hour (Table 8). At
least one survey site on each river had seven species, with one site on the Raquette having only three
species. This site was the Massena Springs site upstream the 420 Bridge, just upstream the upper limit
of the AOC where the fewest species were recorded (Table 8). The total number of positively
identified live individuals by species found at each survey site were recorded (Table 9).
3.3.1
2013 Mussels Inside and Outside the AOC
The total number of species found inside the AOC at each site ranged from 4 to 7, similar to the range
of 3 to 7 species found at survey sites outside and upstream of the AOC (Table 8). The average number
of species found at each site inside the AOC was 4.0 for the St. Regis River, 6.0 for the Raquette, and
5.7 for the Grasse River (Table 8). Outside (and upstream) of the AOC, the average number of species
found at each site was 7.0 for the St. Regis River, 4.0 for the Raquette River, 5.5 for the Grasse River.
(Table 8). On average, the Grasse River sites had 5.5 species of mussels outside and upstream of the
AOC, and 5.7 species inside the AOC (Table 8). The Raquette River had an average of 4.0 species
outside the AOC, and 6.0 species inside the AOC. The St. Regis River had the greatest difference
between sites inside and outside the AOC with an average of 4.0 species inside the AOC and 7.0
species outside and upstream of the AOC. On the St. Regis River, every site outside and upstream of
the AOC had more mussel species than sites inside the AOC (Table 8). Inside the AOC, the St. Regis
River is dominated by soft sediments and low flow, whereas upstream of the AOC the habitat is much
more complex, including areas of sand, gravel, cobble, and boulders with rapids and pools. Variability
in habitat complexity and in the density of the most common species Elliptio complanata resulted in
differences in the number of mussels collected per search hour (Table 8).
Overall, the number of mussel species inside and outside the AOC was similar, although the species
might be different, and the number of mussels collected per search hour inside and outside the AOC
49
varied with habitat. Because mussel habitats tended to be more varied upstream and outside the AOC
than inside the AOC in general, more mussels (CPUE) were typically encountered upstream and
outside the AOC than inside the AOC.
50
Table 8. Number of species, individuals, and mussels collected in 2013 per search hour (CPUE). All sites listed upstream to
downstream. River segments with a U indicate upstream and outside of the AOC; segments with a D are inside the AOC.
River and Site (listed from
upstream to downstream)
Inside or
Outside
the AOC
Site
Segment/
Identifier
GRASS RIVER
Madrid boat launch
Outside
GRU99
Chase Mills bridge
Outside
GRU98
Louisville bridge
Outside
GRU43
Outside
GRU22
Rt. 37 bridge
Outside
GRU11
Massena Memorial Park, Fire
Outside
GRU02
Grasse River Outside AOC Average
Inside
GRD12*
Rt. 131 bridge.
Inside
GRD18*
Inside
GRD39*
Grasse River Inside AOC Average
RAQUETTE RIVER
Raymondville Rt 56 bridge
Outside
RRU38
Massena Springs
Outside
RRU01
Raquette River Outside AOC Average
RR near O'Neil Road
Inside
RRD18**
RR east of Haverstock Rd.
Inside
RRD42**
Raquette River Inside AOC Average
ST. REGIS RIVER
Rte. 53 N. of Brasher Ctr
Outside
SRU99
Outside
SRU98
North Road where close to west
Outside
SRU16
Mohawk School
Outside
SRU02
St. Regis River Outside AOC Average
Inside
SRD12
SR near mouth
Inside
SRD14
St. Regis Inside AOC Average
Number of
Mussel
Species
Number of
Mussels
Collected
Number of Mussels
Collected per Search
Hour (CPUE)
6
4
7
5
6
5
5.5
6
7
4
5.7
620
127
91
159
451
210
276.3
116
132
51
99.7
620
127
61
159
301
210
241.3
116
132
51
99.7
5
3
4.0
7
5
6.0
315
43
179
127
87
107.0
315
29
172
127
58
92.5
7
7
7
7
7.0
4
4
4.0
275
153
74
149
162.8
40
91
65.5
211
153
74
149
146.8
40
91
65.5
* Downstream of Alcoa West facility, within Grasse River Superfund Study Area and 2013 ROD (EPA 2013a).
** Upstream of the GM outfall to Raquette River and bank/in-river remediation.
51
Total Mussel
Count/Segment
Anodontoides
ferussacianus
4
121
2
Louisville bridge
GRU43
7
77
3
GRU22
5
127
Rt. 37 bridge
GRU11
6
409
16
GRU02
5
200
6
GRD12
6
41
19
1
6
47
2
Rt. 131 bridge.
GRD18
7
71
42
2
2
7
4
GRD39
4
24
11
4
12
RRU38
5
295
3
Massena Springs
RRU01
3
40
2
RR near O'Neil Road-
RRD18
7
111
2
5
6
1
RRD42
5
80
1
2
3
1
SRU99
7
231
3
20
6
3
2
10
275
SRU98
7
98
1
6
10
4
2
32
153
SRU16
7
61
1
1
4
3
3
1
74
Mohawk School
SRU02
7
137
2
3
4
1
1
Lasmigona
costata
GRU98
Ligumia
recta1
Chase Mills bridge
Pyganodon
cataracta
24
Pyganodon
grandis
579
Strophitus
undulatus
6
Potamilus
alatus1
GRU99
Leptodea
fragilis
Lampsilis
radiata
Madrid boat launch
Lampsilis
cariosa1
Number of
Mussel
Species
River and Site (listed from upstream
to downstream)
Lampsilis
ovata1
Segment
Elliptio
complanata
Alasmidonta
marginata1
Table 9. Presence of positively identified live individuals at each 2013 survey site.
GRASS RIVER
4
11
1
1
2
3
3
3
12
14
1
7
15
1
620
2
127
1
91
1
451
5
159
3
2
1
1
210
116
4
132
51
RAQUETTE RIVER
5
7
5
315
1
43
1
1
127
87
ST. REGIS RIVER
SRD12
4
33
5
SR near mouth
SRD14
4
45
43
1
2
1. New York State Species of Greatest Conservation Need (SGCN) Status
52
1
149
1
40
1
91
3.3.2
2013 Data Compared to Earlier Studies
The results of the timed searches conducted during this study were compared to earlier timed search
data from surveys conducted by Normandeau (2008) in 2007 and 2008 and by Erickson from 1991 to
2005 (unpublished data). Surveys were conducted in the same general area of previous surveys, but not
at the exact same site. Search times and search areas were similar between Erickson and this study
(1.0-1.5 person-hours), but some Normandeau (2008) searches were longer (3.0 hours) and covered a
much wider area.
Normandeau (2008) surveyed the Grasse River during 2007 and 2008 in a study related to the
proposed Massena hydroelectric facility. The portions of the Grasse River surveyed by Normandeau
corresponded roughly to the upstream segments of the Grasse surveyed in this study. Four survey sites
were surveyed by both Normandeau (2008) and the 2013 study with similar methods. At each of the
four individual survey sites, Normandeau (2008) reported 2 to 5 species (Table 10). At the same sites,
the 2013 study reported 5 to 7 species (Table 10). Overall, the number of mussels encountered per
search hour was variable, but somewhat similar between the two surveys. Normandeau (2008) covered
a greater proportion of the river segment in their surveys than we did, and this likely resulted in a
greater probability of encountering dense mussel beds in areas such as at the Massena Rod and Gun
Club which had the greatest number of mussels encountered per search hour (Table 10). This greater
spatial coverage may also have increased the probability of encountering areas of low density as well,
such as areas of bedrock near the Louisville Bridge. Our 2013 surveys were designed to replicate the
methods of Erickson as outlined in QAPP (Riveredge 2013a) rather than the methods of Normandeau
(2008) since our goal was to generate a data set comparable to Erickson's to compare species and
numbers over a longer temporal time frame.
Erickson provided data for mussel species and abundance at 13 sites on these rivers from surveys he
conducted between 1991 and 2006 (Table 11). Only two of these sites were inside the AOC, one for
the Grasse River (American Veterans campground) and one for the Raquette River (near O’Neil Rd).
The number of mussels collected per search hour was only available for the Grasse River site at the
American Veterans campground. Across all sites inside and outside the AOC, the comparison of these
53
timed search data suggested changes in the distribution and abundance of some mussel species from
the 1990s and 2000s to the present.
In the Grasse River, the number of species encountered during the 2013 surveys was greater at 4 of 7
sites than it was from 1991 to 1996, approximately 20 years earlier (Table 12). There was no change at
two site, and the number of species decreased at one site by one species. Across all nine Grasse River
sites the average number of species at each survey site was 4.3 from 1991-1996 and 5.6 in 2013 (Table
12). For the 7 sites for which both current (2013) and earlier (1991-1996) data are available (6
upstream and 1 inside the AOC), the average number of species increased from 4.3 to 5.3.
The number of individual mussels encountered per search hour on the Grasse River increased at 3
sites, but decreased at 4 sites. (Table 12). For the 7 sites where both current (2013) and earlier data
were available, the overall average number of individuals collected per search hour at each survey site
was fairly similar at 255.7 individual mussels in 1991-1996 and 218.4 mussels in 2013 (Table 12). At
some sites, like the Madrid boat launch, the number of mussels encountered per search hour was very
similar between the 2013 and earlier surveys conducted from 1991 to 1996 (Table 12). At other sites,
notably the Massena Memorial Park (adjacent to the Massena Fire Station), the number of mussels
collected per search hour was much greater in 2013 than it was approximately 20 years earlier (210
mussels per hour vs. 27 mussels per hour) (Photo 4). This site was historically a lake-like
impoundment created by the Massena Weir, but is now a free-flowing river with riffles and pools. The
removal of an impediment to fish passage had the potential to increase fish hosts accessing the
Massena Memorial Park area and to allow for upstream transport of glochidia from mussel beds
downstream of the former weir. This increase in habitat diversity over time could have resulted in an
increase in species richness at this site. At the American Veteran’s (AmVets) campground site on the
Grasse River inside the AOC, the number of species increased by one, but the number of mussels
encountered per search hour dropped from 75 to 51 (Table 12). Although results are listed as
increasing and/or decreasing, it is recognized mussel distribution is patchy, and sampling on the same
exact plot is challenging. At the AmVet’s site the same water access points were utilized. To the
greatest extent possible, efforts were made to cover the same search area.
In the Raquette River, the number of species increased at 2 of the 3 sites which had historical data. The
average increase across all three sites was from 3.7 species to 5.0 species (Table 12). Erickson reported
54
that the number of mussels collected per search hour also increased, although limited data were
available from earlier site surveys (Table 12). Erickson felt that the Raymondville bridge site was
poorly searched in 2005 due to deep water and the lack of scuba gear at this site at the time.
The number of species encountered on the St Regis River increased at 2 of 3 sites (Table 12), and was
similar at the third site. Across all three sites for which 2013 and earlier data were available the
average number of species increased from 4.3 to 6.0 (Table 12). The number of mussels collected per
search hour also increased at these three sites from 82.3 mussels to 119.7 mussels per search hour
(Table 12).
Overall, these data indicate that current mussel populations are very similar to the earlier data, and the
species richness appears to have increased at several sites. Where declines in richness have occurred,
they have been minor (by only a single species). Two notable additions are Potamilus alatus and
Leptodea fragilis. Where Potamilus alatus occurred at the American Veteran's campground site, the
local population was characterized by a wide range of sizes of individual mussels (Photo 5).
Some of these changes are likely due to the greater survey effort in the lower reaches of these rivers as
compared to previous work, as most differences are in relatively rare species that are represented by
very few individuals. These rare species are difficult to find. Lasmigona costata for example, is often
hidden in small crevices among rocks, making it difficult to encounter unless all microhabitats are
searched carefully, and often for extended periods.
One change in mussel species distribution that is notable is the loss of large reproductive Lampsilis
radiata from the lower Grasse River. Erickson (Erickson and Fetterman 1996, Erickson unpublished
data) reported this species as common at the American Veterans campground site in the lower Grasse
River in 1996, with large and gravid individuals commonly encountered. However, many of these
mussels were covered in zebra mussels. In contrast, 2013 surveys recorded few of these individuals,
and none were large nor in reproductive condition. The dense concentrations found by Erickson in
1996 were gone. Of the species that were present in 2013, many mussels of varying species had zebra
mussels attached (Photo 6).
Erickson's 1996 surveys indicate that Potamilus alatus was not present in the lower Grasse River at the
American Veterans campground site in 1996. Age data for this species at this site in 2013 suggest it
55
appeared approximately 13 years ago. It is possible that the appearance of zebra mussels in the lower
Grasse River had two effects: 1) the zebra mussels smothered out the Lampsilis radiata, and 2)
freshwater drum were attracted to the lower Grasse River using zebra mussels as a food source.
Freshwater drum are the host fish species for Potamilus alatus glochidia, and could have brought them
to this area. This may also be true of the St. Regis River and the mouths of other St. Lawrence River
tributaries.
56
Table 10. Number of mussel species and number of mussels per hour collected by Normandeau (2008)
and this study (2013).
River
Segment
Site Location
2013 Surveys (this
study)
Species
Normandeau 2007 and
2008 Surveys
Mussels
per Hour
Species
Mussels
per Hour
Louisville bridge
GRU43
7
61
2
12
GRU22
5
159
4
353
Rt. 37 bridge
GRU11
6
301
5
191
Station
GRU02
5
210
4
69
Table 11. Number of sites historically surveyed and resurveyed by Erickson in this study.
River
Sites Outside AOC
Sites Inside AOC
Total Sites
Grasse
6
1
7
Raquette
2
1
3
St. Regis
3
0
3
11
2
13
Total Sites
57
Photo 4. The number of mussels encountered at one site on the Grasse River was much greater than
historically.
58
Photo 5. Potamilus alatus in the lower Grasse River was represented by individuals of varying sizes
and ages.
59
Photo 6. Zebra mussels were found on several species in the lower Grasse River during 2013 surveys.
60
Table 12. Number of species, individuals, and mussels collected per search hour (CPUE). All sites listed upstream to downstream.
River segments with a U indicate upstream and outside of the AOC; segments with a D are inside the AOC.
Inside Outside
the
AOC?
Site
Segment/
Identifier
Number of
Species
GRASS RIVER
1991-1996
Outside
Madrid boat launch
GRU99
4
Outside
Chase Mills bridge
GRU98
4
Outside
Louisville bridge
GRU43
3
Outside
4
GRU22
Outside
Rt. 37 bridge
GRU11
6
Massena Memorial Park, Fire Station Outside
6
GRU02
Inside
GRD12
Inside
Rt. 131 bridge.
GRD18
Inside
GRD39
3
Past and Current Average for Grasse River
4.3
RAQUETTE RIVER
2003-2005
Outside
2
RRU38
Outside
Massena Springs
RRU01
3
Inside
RR near O'Neil RoadRRD18
6
Inside
RRD42
Past and Current Average for Raquette River
3.7
ST. REGIS RIVER
2005-2006
Outside
SRU99
7
Outside
SRU98
4
North Road where close to west bank Outside
SRU16
2
Outside
Mohawk School
SRU02
Inside
SRD12
Inside
SR near mouth
SRD14
Past and Current Average for St. Regis River
4.3
61
2013
6
4
7
5
6
5
6
7
4
5.6
2013
5
3
7
5
5.0
2013
7
7
7
7
4
4
6.0
Number of Mussels
Collected
Number of Mussels
Collected per
Search Hour
(CPUE)
1991-1996
755
131
111
362
798
40
1991-1996
668
87
55
398
480
27
112
2003-2005
7
2005-2006
69
471
404
-
2013
620
127
91
159
451
210
116
132
51
2013
315
43
127
87
2013
275
153
74
149
40
91
-
75
255.7
2003-2005
7
2005-2006
28
111
108
82.3
2013
620
127
61
159
301
210
116
132
51
197.4
2013
315
29
127
58
132.3
2013
211
153
74
149
40
91
119.7
3.4
Reproduction
The age of individual mussels present at a site along with the presence of gravid female mussels is a
good indication of whether or not successful reproduction is occurring. For mussels to successfully
reproduce, their host fish species must be present as well. Although no fisheries studies were
conducted as part of this work, the host fish species in the rivers known to be present include
smallmouth bass, freshwater drum, lake sturgeon, yellow perch, and many others. Species of mussels
that have host fish that are colder water fish species, such as trout, are known to occur in the upper
reaches of these rivers (e.g. Margaritifera margaritifera) but not in the warmer, lower reaches of the
AOC and nearby upstream areas (Erickson and Fetterman 1996). Erickson thought we might find this
upstream of Helena, less than 10 miles from AOC, but did not during 2013 surveys.
Successful reproduction of freshwater mussels can be inferred by age distributions of mussels and by
the presence of gravid individuals. Age can be estimated by counting growth rings on the exterior of
the shell. Counting rings on the exterior of the shell is most accurate for individuals under 15-20 years
old, after which age estimates are unreliable and underestimate the actual age of the animal. Shell
length is not always a good indicator of age (Schneider and Strayer 2006). Nonetheless, aging mussels
by counting exterior growth rings gives an approximation of the range of ages, especially for mussels
aged 20 years or less. If a broad range of ages is present at any given site, it suggests that reproduction
is successful and recruitment is occurring.
On the Grasse River, Elliptio complanata was found to range in age from 1 year to 15 years old, with
no apparent difference in the maximum and minimum ages between mussels from inside or outside the
AOC (Table 13). Similarly, other mussels were found to be of ages between 2 and 17 years old.
On the Raquette River, Elliptio complanata ranged in age from 3 to 20 years of age, with mussels
inside the AOC slightly younger than outside the AOC (Table 13). Other species ranged in age from 7
years old to 18 years old.
On the St. Regis River, Elliptio complanata ranged in age from 1 to 20 years of age, with upstream and
outside AOC individuals showing a slightly broader range of ages (Table 13). Other mussels were aged
at between 2 and 24 years old.
62
The mussels collected by Metcalfe and Charlton (1990) on the St. Lawrence River were of similar
ages, ranging from 6 to 16 years old for Elliptio complanata and 3 to 10 years old for Lampsilis
radiata. These mussels were aged by preparing thin sections of shells and counting internal growth
rings while the present study ages were determined by counting external annuli.
Mussels of all three tributaries, inside and outside the AOC, are represented by individuals of a broad
range of ages, suggesting that successful reproduction is taking place and recruitment is occurring.
Most mussels were examined to see if they were gravid by gently prying open the shell slightly and
looking inside for inflated marsupial gills (Table 14; Photos 7, 8, and 9). The posterior portion of the
outer gills serve as the glochidial marsupium (Photo 8). Elliptio complanata was not examined since it
is a hermaphroditic short-term breeder that mostly reproduces in late spring and early summer (Clarke
1981 in Metcalfe and Charlton 1990), and abundant at all sites. Leptodea fragilis also was generally
not examined because of its very thin shell and the likelihood that the shell valves could not be
separated even slightly to look inside without damaging the animal.
Lampsilis radiata was found gravid in the Grasse, Raquette and St. Regis Rivers, including in the
downstream reaches of the AOC of the Raquette and Grasse. As noted earlier, few individuals of this
species were found in the lower Grasse River, and none were large or gravid. Other species were found
gravid inside and outside the AOC in the Grasse and Raquette Rivers, but not in the lower St. Regis
River (Table 14). Overall, gravid individual mussels were found widespread in each river, both inside
and outside the AOC. In the Grasse River, three species were gravid outside the AOC, and four species
inside the AOC. In the Raquette River, two species were found gravid outside the AOC, and four
species inside the AOC. On the St. Regis River, four species were gravid outside the AOC, and one
species was found gravid inside the AOC (Table 14).
These results, based on the range of ages of mussels and the presence of gravid mussels for some
species in the three rivers inside and outside the AOC, suggest that reproduction and recruitment are
occurring at the sites we surveyed. No endangered or unreproductive populations were observed in the
2013 survey, although faunal compositions have changed at some sites, which may have resulted from
unreproductive populations having occurred in the intervening years. Erickson, with over 30 years of
experience surveying mussels in Northern New York, felt that these data suggest recruitment appears
to be continuing at levels equal to or better than those demonstrated in his earlier surveys, and that
63
mussel populations at these sites appear to be healthier now than when they were surveyed a decade or
more ago. If these statements are correct, it is encouraging the mussels of these rivers are doing
relatively well, when mussels in many parts of New England and southern Canada are declining. The
continued health and protection of mussel populations in these tributary rivers is important to the
overall diversity and health of the mussel populations in the greater St. Lawrence River watershed.
Mussels in the tributaries to the St. Lawrence have the potential to serve as refugia for St. Lawrence
River populations impacted by non-native zebra and quagga mussels (Ricciardi et al 1996).
64
Photo 7. Mark Erickson examining a mussel for identification.
Photo 8. A gravid Potamilus alatus showing marsupial gills with larval mussels.
65
Table 13. Age, by external ring count, of Elliptio complanata and other mussels at each 2013 sampling site.
Elliptio complanata
Segment
Other Species
Min
Max
Ave
S.D.
N
Min
Max
GRU99
GRU98
GRU43
GRU22
GRU11
GRU02
GRD12
GRD18
GRD39
3
4
2
2
1
5
4
3
7
12
15
12
14
12
17
11
13
12
6.8
8.7
8.3
6.8
6.8
8.8
7.5
8.7
9.8
2.73
3.03
2.38
3.01
3.41
3.71
2.16
3.33
1.85
20
19
15
20
29
10
20
20
12
7
4
8
3
3
6
4
3
2
16
11
13
13
12
11
17
14
13
RRU38
RRU01
RRD18
RRD42
7
5
3
3
20
18
16
16
12.9
10.1
9.4
9.7
3.66
3.14
3.88
3.74
23
39
20
21
9
8
7
8
18
12
14
18
GRU99
GRU98
SRU16
SRU02
SRD12
SRD14
4
1
2
3
6
4
13
13
12
20
15
12
7.9
8.4
8.3
8.3
10.6
8.0
2.48
3.18
2.38
3.53
3.12
2.54
20
18
15
23
20
18
4
2
6
6
4
5
16
14
13
19
12
24
GRASS RIVER
Madrid boat launch
Chase Mills bridge
Louisville bridge
Rt. 37 bridge
Rt. 131 bridge.
American Veterans
RAQUETTE RIVER
Massena Springs
ST. REGIS RIVER
North Road where close to west
Mohawk School
SR near mouth
66
Pyganodon
cataracta
Ligumia
recta
A1705
A1702
A1704
-
Pyganodon
grandis
SRU99
SRU98
SRU16
SRU02
SRD12
SRD14
Strophitus
undulatus
A2403
A2265
A2266
-
Potamilus
alatus
RRU38
RRU01
RRD18
RRD42
Leptodea
fragilis1
A495
A481
A572
A502
A581
A1026
A1025
Lampsilis
cariosa
GRU99
GRU98
GRU43
GRU22
GRU11
GRU02
GRD12
GRD18
GRD39
Lampsilis
ovata
Segment
Erickson
Site
Number
Lampsilis
radiata
Elliptio
complanata1
Table 14. Presence of gravid individuals at each 2013 survey site.
GRASS RIVER
Madrid boat launch
Chase Mills bridge
Louisville bridge
Rt. 37 bridge
Rt. 131 bridge
RAQUETTE RIVER
Massena Springs
ST. REGIS RIVER
Mohawk School
SR near mouth
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Note: 1Species not examined.
67
X
X
Photo 9. A gravid Potamilus alatus collected for the State Museum from the American Veterans
campground site on the Grasse River.
68
3.5
Contaminants
Thirty samples were collected across the study area (inside and outside the AOC, combined) in the
tributaries only for contaminant analysis. Each sample was a composite of five individual mussels. All
samples were run for PCBs and pesticides. Analysis for PAHs, mercury, and metals could not be run
on all samples due to mass limitations. Twenty four samples were run for mercury, 23 for metals, and
16 for PAHs.
Of the 16 samples that were analyzed for PAHs, 12 (75%) were from inside the AOC (expected to
have potential PAH exposure routes). Of the 14 samples that could not be run for PAHs, 11 were from
upstream and outside of the AOC (not expected to have PAH exposure routes) and three samples were
inside the AOC, two from the Raquette and one from the Grasse. Of the 16 samples run for PAHs, no
PAHs were detected in any sample.
3.5.1
Quality Assurance and Quality Control
Contaminant analysis was performed by Pace Analytical (Schenectady, NY) and met all National
Environmental Laboratory Accreditation Conference (NELAC) standards. Fluoride analysis was
completed by EMSL Analytical, Inc. (Cinniminson, NJ). All samples were kept frozen in storage until
delivered to the laboratory via overnight courier. At the lab, they were received intact and within
approved holding times and were kept in frozen storage until analysis.
Analysis of percent lipids was performed by Pace method SOP NE158.05 and all quality assurance
parameters were met for the analysis. Congener PCB analysis was performed by comprehensive
Quantitative Congener Specific (SOP NE133_02) method and samples were extracted by Soxhlet
Extraction Method (EPA method 3540C) and all quality assurance parameters were met for the
analysis. Pesticide analysis was performed using method SW-846 8081A and samples were extracted
using EPA method 3540C. Endosulfan sulfate was recovered above acceptable limits in the CCV, but
samples were not-detected (ND) for that analyte and no bias was indicated. Mercury was performed by
method SW-846 7471A and all quality assurance parameters were met for the analysis. Other heavy
metal (lead, cadmium, aluminum) analysis was performed using method SW-846 6010B with one
laboratory note: the relative percent difference between the sample and the duplicate sample was
69
outside quality acceptance limits for one sample. Fluoride analysis was done using Metrohm 881
Compact IC Pro- Ion Chromatography (IC) and the limit of quantitation for fluoride was between 4.3
and 5.3 mg/kg. Dioxins and Furans were analyzed using USEPA method 1613B and labeled standard
recoveries were within target ranges specified by method 1613B with the exception of one sample.
Laboratory method blanks revealed no contamination and laboratory spike samples indicated a high
degree of precision and accuracy for sample determinations.
3.5.2 Data Treatment
Contaminant results in freshwater mussels were not evenly distributed so we selected a non-parametric
approach to evaluate differences in contaminant exposure among rivers and inside and outside the
Massena/Akwesasne St. Lawrence River AOC. To evaluate overall differences in contaminant burdens
and lipids from inside and outside the AOC, data were pooled from all river stems (i.e. Grasse, St.
Regis, Raquette) and classified as inside or outside the AOC. We also compared contaminant burdens
from inside and outside the AOC for each river stem (i.e. Grasse Inside AOC vs. Grasse Outside AOC)
when sample sizes were sufficient. Lastly, we compared contaminant burdens among rivers and inside
and outside the AOC.
When we obtained values less than the detection limit, they were set at 10% below the detection limit
to complete the statistical comparisons (Provencher et al. 2014). In cases where less than 60% of
samples had values above the detection limit, only the minimum and maximum values are reported and
they were not included in the analysis. In all cases, statistics in tables do not include values set by the
investigators during analysis. Wilcoxon tests and Wilcoxon Each Pair were performed with a
significance level (alpha) set to 0.05 to compare contaminants from within and outside the AOC. All
results are reported in ng/g (ppb) wet weight (w.w.) ± standard error (SE). All analyses were performed
using the statistical package JMP (version 11.0).
3.5.3
Results
PCBs, metals, mercury and dioxins/furans were detected in the samples. No pesticides, no PAHs, and
no fluoride were detected in any samples (Table 15).
For freshwater mussels with the three rivers combined, several contaminants were significantly higher
inside the AOC than outside the AOC (Table 16). Total PCBs inside the AOC (90 ± 30.0 ng/g; n=12)
was significantly higher (p = 0.02) than total PCBs outside the AOC (4.0 ± 1.0 ng/g; n=10). Two
70
dioxins (HpCDD and OCDD) and one furan (TCDF) were also all significantly higher inside than
outside the AOC. The dioxin HpCDD inside the AOC (0.0015 ± 0.0003 ng/g; n=12) was significantly
higher (p = 0.04) than outside the AOC (0.0008 ± 0.0002 ng/g; n=10) and OCDD inside the AOC
(0.0058 ± 0.0013 ng/g/ n=9) was also significantly higher (p = 0.03) than outside the AOC (0.0026 ±
0.0004 ng/g; n = 8). Total TCDF inside the AOC (0.0076 ± 0.0035 ng/g; n=12) was higher than outside
the AOC (0.0009 ± 0.0002 ng/g; n=14) but the difference was not significant (p = 0.09) because of the
high range of observed values inside the AOC. No other contaminants were significantly different
inside vs. outside the AOC when the data were pooled among rivers (Table 16).
In the Grasse River, total TCDF inside the AOC (0.014 ± 0.0062 ng/g) was significantly higher (p =
0.004) than outside the AOC (0.0007 ± 0.0001ng/g; Table 17). Percent lipids in mussels collected from
the Grasse River inside the AOC (1.08 ± 0.19 %) was also significantly higher (p = 0.007) than those
collected outside the AOC (0.68 ± 0.07 %). No other contaminants in the Grasse River were
significantly different inside or outside the AOC. Importantly, the mussel sample with the highest
Total PCB concentration outside the AOC (1.0 ng/g) is lower than the lowest Total PCB concentration
reported for inside the AOC (97.0 ng/g), but they were not statistically comparable because PCBs were
detected in n = 2 samples outside the AOC. However, PCBs were detected in all inside AOC Grasse
River samples (97.0-283.0 ng/g; n=6; Table 17). Conversely, the sample with the highest mercury
concentration inside the AOC (Grasse River; 60 ng/g) is lower than the lowest concentration reported
for mussels collected outside the AOC from the Grasse River (68.0 ng/g; Table 17), but was also not
statistically comparable because of a limited sample size inside the AOC (n=2).
In the Raquette River, no contaminants or lipids were significantly different between those collected
from inside vs. outside the AOC (Table 18). Importantly, in the Raquette River outside the AOC, the
sample with the highest OCDD concentration was lower than the lowest OCDD concentration reported
for samples collected from inside the AOC (Table 18).
In the St. Regis River, lipids outside the AOC (0.74 ± 0.10%) were significantly higher (p = 0.0495)
than mussels from the St. Regis inside the AOC (0.54 ± 0.05%; Table 19). Interestingly, total PCBs
were not detected inside the AOC from the St. Regis River.
Across all rivers inside the AOC, Total PCBs were significantly highest in the Grasse River (p = 0.03;
Table 20). Total TCDF and lipids (%) were also significantly highest in the Grasse River AOC
71
(p=0.005; p = 0.03, respectively; Table 20). Across all rivers outside the AOC, there were no
significant differences (Table 21).
Overall, contaminants that were significantly higher in mussels collected inside the AOC included:
Total PCBs, Dioxins HpCDD and OCDD, and the furan TCDF. Inside the Grasse River AOC, the
range of PCBs is much higher than for samples collected outside the AOC on the Grasse River, but
because it was not detected in several samples outside the AOC, the sample size was insufficient for
analysis. Interestingly, mussel lipid content was also significantly higher inside the AOC for the Grasse
and outside the AOC for the St. Regis River.
In the St. Regis and Raquette Rivers, no contaminants were significantly higher in samples collected
inside the AOC, but this was largely because most samples were below the detectable limit so they
could not be compared.
3.5.4
Comparison with other studies
Mussels inside the AOC were sampled from 1983 to 1997 by NYSDEC (1990), Woodward-Clyde
Consultants (WWC) (1992), and TAMS Consultants for Reynolds Metals Corporation (RMC) (2001)
(Table 22). Most samples were collected on the St. Lawrence River east of the mouth of the Grasse
River in the vicinity of General Motors and RMC and were analyzed for aluminum, fluoride, PCBs and
PAHs. Samples were collected in 1983 and 1986 (NYSDEC 1994), 1991 (Woodward-Clyde 1992),
and in 1996 and 1997 (RMC 2001). In addition, Alcoa conducted caged mussel studies with two 30day deployments in the Grasse River in June/July and September/October 1998 using Margaritifera
margaritefera. These mussels were submitted to NEA Laboratories for PCB Aroclor analysis, pre- and
post-caged studies. Pre-deployment samples were non-detect (ND) for PCBs, using a detection limit of
120 ng/g (Alcoa Inc. 2001). The Alcoa results and the Woodward-Clyde results were reported in dry
weight (d.w.) whereas the NYSDEC (1994) and TAMS (2001) results were reported in wet weight
(w.w.). Metcalfe (unpub. data in Metcalfe and Charlton 1990) suggests a conversion factor of 10 times
between wet weight and dry weight contaminant values in mussels.
NYSDEC (1990) collected mussels in the AOC from the St. Lawrence, Grasse and Raquette Rivers
and Environs. Four mussels collected from 1983 to 1986 near General Motors and the MassenaCornwall Bridge were found to have 170 to 680 ng/g (ppb)(w.w.) total PCBs (Table 22) (NYSDEC
1990).
72
Woodward-Clyde collected a St. Lawrence River mussel sample in 1991 that contained 368 ng/g
(d.w.) of aluminum, 63.2 ng/g (d.w.) of fluoride, and 360 ng/g (d.w.) of PCBs (WWC 1992). Samples
collected in 2013 for this study in the tributary rivers of the AOC contained no PAHs nor fluoride.
Aluminum, however, was much greater in the 2013 tributary samples, with a mean value of 142,420
ng/g (ppb) (w.w.) inside the AOC. Note, however, that no 2013 samples were collected from the St.
Lawrence River.
Metcalfe and Charlton (1990) examined contaminant concentrations in freshwater mussel species
Elliptio complanata and Lampsilis radiata at 17 stations on the St. Lawrence River from Lake Ontario
to Trois Riviéres Quebec in October 1985. They collected a total of 38 mussels from 20 sampling
stations, including a single gravid Lampsilis radiata aged nine years old at the mouth of the Grasse
River (station 30) from a depth of 10.5 meters using a ponar dredge (Metcalfe and Charlton 1990).
This individual was found to have the highest total PCB concentration (63 congeners) reported of all
mussels sampled by Metcalfe and Charlton (1990), with 492 ng/g of total PCBs (w.w.) (Table 22).
This value is 100 times higher than they reported for the Ottawa River (same study) and similar to the
highest concentration reported in the current study inside the AOC and Grasse River (280.0 ng/g).
These two studies, NYSDEC (1990) and Metcalfe and Charlton (1990), sampled freshwater mussels
from inside the AOC between 1983 and 1986 and found total PCB concentrations ranging from 170 to
680 ng/g (w.w.). The mussel collected by WWC (1992) in 1991 could have been even higher if the
conversion rate suggested by Metcalfe (unpub. data in Metcalfe and Charlton 1990) of 10 times
between wet weight and dry weight contaminant values in mussels is considered. The 1998 caged
mussel samples analyzed by Alcoa Inc. (2001), three years after the Non-Time Critical Removal
Action adjacent Outfall 001 on the Grasse, found PCBs (ng/g d.w.) ranging from non-detect (ND) to
738 ng/g (ppb) depending on location and position in the water column, and season of collection. All
these levels are higher than those found in this study (280 ng/g w.w. total PCBs in the most
contaminated sample) 15-30 years later, using Elliptio complanata, albeit, inside the AOC where field
collected mussels have been exposed over their life span.
Mean total PCBs in samples collected outside the AOC (4.0 ng/g) are similar to freshwater mussel
reference locations such as mean PCBs in Fossaria sp. and Gyraulus sp. from Kusawa and Laberge
Lakes, Yukon, Canada, which were 0.85 and 2.03 ng/g (w.w.), respectively (Schindler and Kidd, 1993)
73
Interestingly, Metcalfe and Charlton (1990) found that 97% of the 38 mussels they collected from 20
sampling stations on the St. Lawrence River and Ottawa River sampling sites contained detectable
levels of p, p'-DDE, which was the dominant organochlorine pesticide in mussels. The second highest
concentration was from the mussel collected at the mouth of the Grasse River (Station 30). No
pesticides were found in any of the samples analyzed in our 2013 study.
For heavy metals, Kwan et al. (2003) evaluated heavy metals in zebra mussels (Dreissena
polymorpha) from the St. Lawrence River between Cornwall, Ontario and Quebec City, Quebec, and
reported a mean Hg concentration 123 ng/g (d.w.) near Cornwall; which is similar to the wet weight
(w.w.) ranges reported in the current study for Hg inside (42.0 – 155.0 ng/g) and outside (68.4 – 168.0
ng/g) the AOC. Further, Kwan et al. (2003) reported mean lead and cadmium concentrations (d.w.)
near Cornwall of 1,500 and 3,080 ng/g, respectively.
Also on the St. Lawrence River, Johns (2001, 2012) used zebra mussels and quagga mussels as
biomonitors for cadmium, copper, and zinc at 5-12 sites including one site in the AOC from 1994 to
2007. In quagga mussels, levels of copper were greatest in the AOC, but in general, concentrations of
the three metals were not high compared to reports in the published literature. However, few published
studies used quagga mussels instead of zebra mussels. In zebra mussels, Johns (2012) found levels of
cadmium highest at the head of the St. Lawrence River (Cape Vincent) but second highest in the AOC,
but all levels declined over time. Cadmium levels in the Massena/Akwesasne AOC ranged from 2,930
to 3,640 ng/g d.w. (Johns 2012).
The values for lead and cadmium reported by Kwan et al. (2003) and Johns (2012) are higher than
reported in the current study inside the AOC (468.0 and 952.0 ng/g w.w.), but with a conversion rate of
10 between wet weight and dry weights, the values of the current study may be higher.
In the current study, mussel dioxin concentrations inside the AOC range from 0.0001 ng/g to 0.013
ng/g. Few field studies have measured the concentrations of dioxins and furans in freshwater mussels
of the Great Lakes (although see Marvin et al. 2002). The mean concentration of total TCDD inside
the AOC was 0.0014 ng/g, higher than reported for marine mussels from northern Norway 0.0004 ng/g
(Schlabach and Skotvold 1996). The dioxin HxCDD inside the AOC (current study) ranged from
0.0001 – 0.0007 ng/g, similar to the concentration reported in Schlabach and Skotvold (1996) for
northern Norway (0.00023 ng/g). Further, Schlabach and Skotvold (1996) report HpCDD and OCDD
74
concentrations of 0.00019 and 0.00041 ng/g, respectively, whereas we report higher mean
concentrations (inside the AOC) of 0.0015 and 0.0058 ng/g, respectively.
Furan concentrations reported in Schlabach and Skotvold (1996) are: TCDF – 0.0032 ng/g, HxCDF –
0.0008 ng/g, HpCDF – 0.0004 ng/g, and OCDF – 0.0012 ng/g. In the current study, inside the AOC,
mean TCDF was higher (0.0076 ng/g), HxCDF similar (0.0002 – 0.0011 ng/g), HpCDF similar
(0.0002 – 0.0022 ng/g), and OCDF similar (0.0004 – 0.0036 ng/g).
75
Table 15. List of contaminants detected and not detected in 2013 mussels surveys.
Detected
PCBs
Mercury
Aluminum
Cadmium
Lead
TCDD
PeCDD
HxCDD
HpCDD
OCDD
TCDF
PeCDF
HxCDF
HpCDF
OCDF
2,3,7,8 TCDF
Not detected
Fluoride
Aldrin
beta-BHC
gamma-BHC
delta-BHC
Heptachlor
alpha-BHC
Heptachlor epoxide
Endosulfan I
p,p'-DDE
Dieldrin
Endrin
p,p'-DDD
Endosulfan II
2-Methylnaphthalene
Acenaphthene
Acenaphthylene
Anthracene
Benzo(a)anthracene
Benzo(a)pyrene
Benzo(b)fluoranthene
Benzo(g,h,i)perylene
Benzo(k)fluoranthene
Chrysene
Dibenz(a,h)anthracene
Fluoranthene
Fluorene
Indeno(1,2,3-cd)pyrene
p,p'-DDT
Naphthalene
Endrin aldehyde
Phenanthrene
Pyrene
2,3,7,8 TCDD
Endosulfan sulfate
Chlordane
Toxaphene
alpha Chlordane
gamma Chlordane
Hexachlorobenzene
Methoxychlor
Endrin ketone
76
Table 16. Average concentrations of contaminants (ng/g w.w.; ppb) and total lipids (%) in freshwater mussels collected inside (n = 15)
and outside (n = 15) the Massena/Akwesasne AOC in 2013. In cases where not all samples detected a given contaminant, the sample
number is given in parentheses. Note: ND = Non-detect; NA= Not applicable due to small number of samples with levels above
detection limit; NS = Not significant.
Inside AOC
Outside AOC
Range (n)
Mean ± SE
0.3 – 11.0 (10)
4.0 ± 1.0
ND
Contaminant
Range (n)
Mean ± SE
3.1 - 280.0 (12)
90.0 ± 30.0
Total PCBs
ND
Fluoride
Metals
Mercury
42.0 – 155.0 (7)
NA
68.4 – 168.0 (13)
117.0 ± 9.0
Aluminum
29,700 – 549,000 (10)
142,420 ± 47,320
29,000 – 351,000 (13) 124,000 ± 29,900
Cadmium
468.0 (1)
NA
511.0 – 697.0 (3)
NA
Lead
952.0 (1)
NA
551.0 – 924.0(4)
NA
Dioxins
TCDD
0.0003 - 0.0033 (11)
0.0014 ± 0.0004
0.0003 – 0.001 (5)
NA
PeCDD
.00013 – 0.0010 (2)
NA
0.0001 (1)
NA
HxCDD
0.0001 - 0.0007 (3)
NA
0.00008 - 0.0003 (4)
NA
HpCDD
0.0003 – 0.0045 (12)
0.0015 ± 0.0003
0.0003 – 0.0018 (10)
0.0008 ± 0.0002
OCDD
0.0012 – 0.0130 (9)
0.0058 ± 0.0013
0.0011 – 0.0046 (8)
0.0026 ± 0.0004
Furans
TCDF
0.0006 – 0.039 (12)
0.0076 ± 0.0035
0.0002 – 0.0032 (14)
0.0009 ± 0.0002
PeCDF
0.00002 – 0.0013 (3)
NA
0.0002 - 0.0005 (6)
NA
HxCDF
0.0002 – 0.0011 (6)
NA
0.0002 - 0.0009 (7)
NA
HpCDF
0.0002 – 0.0022 (6)
NA
0.0002 - 0.0004 (3)
NA
OCDF
0.0004 – 0.0036 (6)
NA
0.0002 - 0.001 (2)
NA
0.44 - 1.28 (15)
0.84 ± 0.07
0.41 - 1.24 (15)
0.76 ± 0.06
Lipids
Note: PAHs (n=16), Fluoride (n=30), and Organochlorine pesticides (n=30) all non-detect (ND)
77
Significance
p = 0.02
NA
NS
NA
NA
NA
NA
NA
p = 0.04
p = 0.03
NS (p = 0.09)
NA
NA
NA
NA
NS
Table 17. Concentrations of contaminants (ng/g w.w.; ppb) and total lipids (%) in freshwater mussels collected from the Grasse River
inside (n = 6) and outside (n = 6) the Massena/Akwesasne AOC in 2013. In cases where not all samples detected a given contaminant,
the sample number is given in parentheses. Note: ND = Non-detect; NA= Not applicable due to small number of samples with levels
above detection limit; NS = Not significant.
Grasse River
Inside AOC
Contaminant
Total PCBs
Fluoride
Metals
Mercury
Aluminum
Cadmium
Lead
Dioxins
TCDD
PeCDD
HxCDD
HpCDD
OCDD
Furans
TCDF
PeCDF
HxCDF
HpCDF
OCDF
Lipids
Outside AOC
Range (n)
Mean ± SE
0.4 – 1.0 (2)
NA
ND
Range (n)
97.0- 283.0 (6)
ND
Mean ± SE
180.0 ± 30.0
42.0 – 60.0 (2)
71,400 – 156,000 (5)
ND
ND
NA
117,540 ± 16,330
NA
NA
68.0 – 150.0 (6)
29,100 – 328,000 (6)
ND
ND
110.0 ± 10.0
108,650 ± 45,300
NA
NA
NA
NS
NA
NA
0.0012 – 0.0033 (5)
ND
ND
0.0013 – 0.0045 (5)
0.0041 – 0.013 (3)
0.0025 ± 0.0005
NA
NA
0.0024 ± 0.0006
NA
ND
ND
ND
0.0003 - 0.0006 (4)
0.0017 – 0.0034 (4)
NA
NA
NA
0.0004 ± 0.00007
0.0025 ± 0.0004
NA
NA
NA
NS
NA
0.0027 – 0.039 (6)
0.0001-0.0013 (2)
0.0007 – 0.0011 (2)
0.0004 – 0.0022 (2)
0.0013 – 0.0036 (3)
0.86 - 1.28 (6)
0.014 ± 0.0062
NA
NA
NA
NA
1.08 ± 0.08
0.0004 – 0.0011 (6)
0.0002 (1)
0.0003 - 0.0006 (3)
0.0002 (1)
ND
0.42 – 0.88 (6)
0.0007 ± 0.0001
NA
NA
NA
NA
0.68 ± 0.07
p =0.004
NA
NA
NA
NA
p = 0.007
78
Significance
NA
Table 18. Concentrations of contaminants (ng/g w.w.; ppb) and total lipids (%) in freshwater mussels collected from the Raquette
River inside (n =6) and outside (n = 6) the Massena/Akwesasne AOC in 2013. In cases where not all samples detected a given
contaminant, the sample number is given in parentheses. Note: ND = Non-detect; NA= Not applicable due to small number of samples
with levels above detection limit; NS = Not significant.
Raquette River
Inside AOC
Contaminant
Total PCBs
Fluoride
Metals
Mercury
Aluminum
Cadmium
Lead
Dioxins
TCDD
PeCDD
HxCDD
HpCDD
OCDD
Furans
TCDF
PeCDF
HxCDF
HpCDF
OCDF
Lipids
Outside AOC
Range (n)
Mean ± SE
2.0 – 11.0 (6)
7.2 ± 2.0
ND
Range (n)
3.0 – 13.0 (6)
ND
Mean ± SE
6.5 ± 1.0
63.0 – 117.0 (3)
29,700 – 549,000 (4)
468.0 (1)
952.0 (1)
NA
197,180 ± 119,800
NA
NA
80.0 – 170.0 (5)
58,300 – 351,000 (5)
510.0 – 700.0 (3)
550.0 – 920.0 (4)
120.0 ± 17.0
158,200 ± 57,400
NA
750.0 ± 80.0
NA
NS
NA
NA
0.0003 - 0.0009
ND
0.0007 (1)
0.0004 – 0.0019 (5)
0.0031 – 0.0062 (4)
NA
NA
NA
0.001 ± 0.0003
0.0052 ± 0.0007
0.0003 - 0.001 (4)
ND
0.0002 - 0.0009 (3)
0.0006 – 0.0018 (4)
0.0022 – 0.0027 (2)
0.0006 ± 0.0002
NA
NA
0.0012 ± 0.0003
NA
NA
NA
NA
NS
NA
0.0006 – 0.0019 (5)
0.0002 - 0.0005 (2)
0.0003 - 0.0006 (3)
0.0003 - 0.0007 (3)
0.001 – 0.0012 (2)
0.51 - 1.03 (6)
0.0013 ± 0.0003
NA
NA
NA
NA
0.74 ± 0.08
0.0002 – 0.0032 (5)
0.0004 - 0.0005 (4)
0.0002 - 0.0009 (3)
0.0003 - 0.0004 (2)
0.001 (1)
0.41 - 1.24 (6)
0.0013 ± 0.0005
0.0004 ± 0.00002
NA
NA
NA
0.84 ± 0.14
NS
NA
NA
NA
NA
NS
79
Significance
NS
Table 19. Concentrations of contaminants (ng/g w.w.; ppb) and total lipids (%) in freshwater mussels collected from the St. Regis
River inside (n = 3) and outside (n = 3) the Massena/Akwesasne AOC in 2013. Note: ND = Non-detect; NA= Not applicable due to
small number of samples with levels above detection limit; NS = Not significant.
St. Regis
Inside AOC
Contaminant
Total PCBs
Fluoride
Metals
Mercury
Aluminum
Cadmium
Lead
Dioxins
TCDD
PeCDD
HxCDD
HpCDD
OCDD
Furans
TCDF
PeCDF
HxCDF
HpCDF
OCDF
Lipids
Outside AOC
Range (n)
Mean ± SE
0.3 - 0.8 (2)
NA
ND
Range (n)
ND
ND
Mean ± SE
NA
60.0 – 160.0 (2)
47,800 (1)
ND
ND
NA
NA
NA
NA
110.0 – 160.0 (2)
54,600 – 119,000 (2)
ND
ND
NA
NA
NA
NA
NA
NA
NA
NA
0.0003 - 0.0006 (3)
0.0001 (1)
0.0001 - 0.0003 (2)
0.0003 - 0.0006 (2)
0.0012 – 0.0019 (2)
0.45 ± .08
NA
NA
NA
NA
0.0006 (1)
0.0001 (1)
0.00008 (1)
0.0003 – 0.0012 (2)
0.0011 – 0.0046 (2)
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
0.0009 (1)
ND
0.0002 (1)
0.0002 (1)
0.0004 (1)
0.44 - 0.60 (3)
NA
NA
NA
NA
NA
0.54 ± 0.05
0.00041 – 0.0010 (3)
0.0003 (1)
0.0003 (1)
ND
0.0002 (1)
0.64 - 0.95 (3)
0.0008 ± 0.0002
NA
NA
NA
NA
0.74 ± 0.10
NA
NA
NA
NA
NA
p = 0.0495
80
Significance
NA
Table 20. Concentrations of contaminants (ng/g w.w.; ppb) and total lipids (%) in freshwater mussels collected inside the
Massena/Akwesasne AOC in 2013 from the Grasse (n = 6), Raquette (n = 6), and St. Regis (n = 3) Rivers. Notes: ND = Non-detect;
NA= Not applicable due to small number of samples with levels above detection limit; NS = Not significant; significant differences
among groups use different symbols (*,+).
Grasse River
Range (n)
Mean ± SE
Contaminant
97.0–283.0 (6)
Total PCBs
ND
Fluoride
Metals
42.0–60.0 (2)
Mercury
71,400–156,000 (5)
Aluminum
ND
Cadmium
ND
Lead
Dioxins
*
Inside AOC
Raquette River
Range (n)
Mean ± SE
+
St. Regis River
Range (n)
Mean ± SE
Sig.
180.0±30.0
3.0–13.0 (6)
ND
6.5±1.0
ND
ND
NA
p=0.03
NA
117,540±16,300
NA
NA
63.0-117.0 (3)
29,700–549,000 (4)
468.0 (1)
952.0 (1)
NA
197,180±119,800
NA
NA
60.0–160.0 (2)
47,800 (1)
ND
ND
NA
NA
NA
NA
NA
NS
NA
NA
0.0001 (1)
0.0001-0.0003 (2)
0.0003-0.0006 (2)
0.0012–0.0019 (2)
0.0005±
0.0001
NA
NA
NA
NA
NA
NA
NS
NS
0.00129±0.00030+
NA
NA
NA
0.0009 (1)
ND
0.0002 (1)
0.0002 (1)
NA
NA
NA
NA
p=0.005
NA
NA
NA
NA
0.74±0.08+
0.0004 (1)
0.44-0.60 (3)
NA
0.54±0.05+
NA
p=0.03
TCDD
0.0012–0.0033 (5)
0.0025±0.0005
0.0003-0.0009 (3)
NA
0.0003-0.0006 (3)
PeCDD
HxCDD
HpCDD
OCDD
Furans
TCDF
PeCDF
HxCDF
HpCDF
OCDF
Lipids
ND
ND
0.0013–0.0045 (5)
0.0041–0.013 (3)
NA
NA
0.0024±0.0006
NA
ND
0.0007 (1)
0.0004–0.0019 (5)
0.0031–0.0062 (4)
NA
NA
0.0010±0.0003
0.0052±0.0007
0.0027–0.039 (6)
0.0001-0.0013 (2)
0.0007–0.0011 (2)
0.0004–0.0022 (2)
0.0140 ± 0.0062*
NA
NA
NA
0.0006–0.0019 (5)
0.0002-0.0005 (2)
0.0002-0.0006 (3)
0.0003-0.0008 (3)
0.0013–0.0036 (3)
0.86-1.28 (6)
NA
1.08 ± 0.08*
0.0010–0.0012 (2)
0.51-1.03 (6)
81
NS
Table 21. Concentrations of contaminants (ng/g w.w.; ppb) and total lipids (%) in freshwater mussels collected outside the
Massena/Akwesasne AOC in 2013 from the Grasse (n = 6), Raquette (n = 6), and St. Regis (n = 3) Rivers. Notes: ND = Non-detect;
NA= Not applicable due to small number of samples with levels above detection limit; NS = Not significant; significant differences
among groups use different symbols (*,+).
Grasse River
Range (n)
Mean ± SE
Contaminant
0.4 – 1.0 (2)
Total PCBs
ND
Fluoride
Metals
68.0 – 150.0 (6)
Mercury
29,100–328,000 (6)
Aluminum
ND
Cadmium
ND
Lead
Dioxins
ND
TCDD
ND
PeCDD
ND
HxCDD
0.0003-0.0006 (4)
HpCDD
0.0017–0.0034 (4)
OCDD
Furans
TCDF
PeCDF
HxCDF
HpCDF
OCDF
Lipids
Outside AOC
Raquette River
Range (n)
Mean ± SE
St. Regis River
Range (n)
Mean ± SE
Sig.
NA
2.0 – 11.0 (6)
ND
0.0072 ± 0.002
0.3 - 0.8 (2)
ND
NA
NS
110.0 ± 10.0
108,650 ± 45,300
NA
NA
80.0 - 170.0 (5)
58,300–351,000 (5)
510.0 - 700.0 (3)
550.0 - 920.0 (4)
120.0 ± 20.0
158,240±57,400
NA
750.0 ± 80.0
110.0 - 160.0 (2)
54,600–119,000 (2)
ND
ND
NA
NA
NA
NA
NS
NS
NA
NA
NA
NA
NA
0.0004 ± 0.00007
0.0025 ± 0.0004
0.0003 – 0.0010 (4)
ND
0.0002 - 0.0009 (3)
0.0006 – 0.002 (4)
0.0022 – 0.0027 (2)
0.0006 ± 0.0002
NA
NA
0.0012 ± 0.0003
NA
0.0006 (1)
0.0001 (1)
0.00008 (1)
0.0003–0.0012 (2)
0.0011–0.0046 (2)
NA
NA
NA
NA
NA
NA
NA
NA
NS
NS
0.0004 – 0.0011 (6)
0.0007 ± 0.0001
0.0002 – 0.0032 (5)
0.0013 ± 0.0005
0.0004 – 0.0010 (3)
NS
0.0002 (1)
0.0004-0.0006 (3)
0.0002 (1)
ND
0.42 - 0.88 (6)
NA
NA
NA
NA
0.68 ± 0.07
0.0004 - 0.0005 (4)
0.0002 - 0.0009 (3)
0.0003 - 0.0004 (2)
0.001 (1)
0.41 - 1.24 (6)
0.0004 ± 0.00002
NA
NA
NA
0.84 ± 0.14
0.0003 (1)
0.0003 (1)
ND
0.0002 (1)
0.64 - 0.95 (3)
0.0008 ±
0.0002
NA
NA
NA
NA
0.74 ± 0.10
82
NA
NA
NS
NA
NS
Table 22. Historical concentrations of contaminants (ng/g [ppb] w.w. unless noted) and total lipids (%) in freshwater mussels collected
inside the Massena/Akwesasne AOC. Where N>1 values are means and SE. No samples were analyzed for pesticides, mercury, other
metals, dioxins, furans, or other contaminants. Blank cells mean the analysis was not done.
Site
Year
Collected
N
Total PCBs Aluminum
1983
1983
1986
1986
1985
1991
1991
1996
1997
1996
1996
1996
1
1
1
1
1
1
1
5
3
3
3
3
680
400
100
50
492
50
360
81.6 ± 13
516 ± 33
519 ± 40
146 ± 25
42.7 ± 2.9
Fluoride
Total Lipids
(%)
Author
Inside AOC
STLW-GM2
STLW-GM3
STLW-CB1
STLW-CB2
Station 30
SL1 1
SL2 1
TAMS-SL3
TAMS-SL4
TAMS-SL5
TAMS-SL6
TAMS-SL8
1
368
63.2
60.2
0.78 ± 0.05
0.93 ± 0.09
1.1 ± 0.15
0.93 ± 0.19
1.1 ± 0.09
Samples from WWC 1992 were reported as dry weight, not wet weight.
83
NYSDEC 1990
NYSDEC 1990
NYSDEC 1990
NYSDEC 1990
Metcalfe and Charlton 1990
WWC 1992
WWC 1992
TAMS 2001
TAMS 2001
TAMS 2001
TAMS 2001
TAMS 2001
3.5.5
Implications for human consumption
Contaminant data have implications for human consumption of freshwater mussels. Freshwater
mussels are known to have important cultural significance for Native American tribes (Garvin
2005). Mussels were traditionally used for food, utensils, and ornaments. The distribution of
mussels along streams and rivers in the southeastern U.S. may have been more important in
determining the location of Native America villages than the presence of big game animals for
food (Garvin 2005). Elder interviews on file with SRMTED indicate freshwater mussels were
consumed as recently as within the last 30 years. Current consumption is unknown. However,
Mohawk Akwesasne Cultural Restoration (ACR) Program efforts target restored uses of all
traditional and customary consumption pathways and practices.
While many remedial successes and contaminant mass reductions have contributed to the
restoration of the AOC since 1995 on the United States side, excessive levels and inventory of
PCBs can still be found in sediments in the Grasse River Superfund Site (USEPA 2012b, 2013a).
Fish tissue concentrations are elevated. Fish and wildlife advisories are still in effect in the
Massena/Akwesasne AOC (SRMT 2014a, 2014b).
Data from this study indicate that PCB levels in freshwater mussels inside the AOC exceed the
EPA remedial goal of 10 ng/g for fish tissue to be protective of Mohawk health. On average,
across all three rivers, the levels of total PCBs inside the AOC was 90 ± 30.0 ng/g. Mussels
collected upstream of the AOC had significantly lower levels of average total PCBs (4.0 ± 1.0
ng/g) than inside the AOC. However, the results varied across each of the three rivers (Table 20,
Table 21). On the Raquette River, one sample inside the AOC and two samples outside the AOC
contained PCB levels above 10 ng/g, although the remaining five samples inside and four
samples outside were below the threshold. On the St. Regis River, all mussel samples were
below 10 ng/g (Table 23).
84
Table 23. Rivers and areas where average mussel contaminant levels are below the EPA Grasse
River remedial goal for fish tissue. Numbers in parentheses are the number of samples above 10
ng/g/total samples.
Mussels below the fish
tissue remedial goal
inside the AOC?
Mussels below the fish
tissue remedial goal outside
(Upstream) the AOC?
No (6/6)
Yes (0/6)
Raquette
Yes (1/6) 1
Yes (2/6) 2
St Regis
Yes (0/3)
Yes (0/3)
NA3
NA3
River
Grasse
St. Lawrence
1
2
3
The average of six samples is below the goal but one of six samples inside the AOC exceeded
the fish tissue remedial goal
The average of six samples is below the goal but two of six samples upstream of the AOC
exceeded the fish tissue remedial goal.
NA Not sampled in 2013
85
4.0
LESSONS LEARNED
Overall, field sampling of freshwater mussels went very smoothly and most identifications in the
field were accurate. Considerable phenotypic plasticity exists in the mussels among the three
rivers and some identifications can be difficult. The DNA analysis of Lampsilis radiata and
Lampsilis siliquoidea will ultimately shed light on which species is present or if both are present.
Several species that could occur in the AOC and environs but were not found in this survey are
species of big, deep rivers such as the St. Lawrence (e.g. Obovaria olivaria). At present, it
appears that these species have been eliminated from the Great Lakes and connecting channels
due to the presence of zebra mussels (Bouvier et al. 2013).
Determining the age of older mussels can be difficult or impossible. Selected mussels could be
sacrificed and the shells thin-sectioned and microscopically examined to determine mussel age.
However, at present it seems that counting external growth rings and finding gravid individuals
suggests that successful reproduction and recruitment are occurring. Future surveys should
consider aging mussels through internal ring counts to confirm age distributions of mussel
populations.
Field surveys did not start early enough in the year to find gravid Elliptio complanata, although
the large numbers of individuals found and the wide range of ages of these individuals suggests
that this species is successfully reproducing in each river and active recruitment is occurring.
In future work that involves collecting mussels for broad contaminant analysis, the number of
mussels collected for each sample should be increased to ensure sufficient sample mass (e.g.
minimum of 150g, approximately 10 large bivalves minimum age of 5 years). If only PCBs are
being investigated, then a composite sample of five individuals would be sufficient even with
smaller individuals.
These surveys were not designed to locate rare species. Rare species surveys would require
greater search time and concerted efforts in targeted microhabitats. These surveys were also not
designed to map mussel beds, or to estimate the total number of mussels inside or outside the
AOC, by river or in total, or to compare findings between nearshore and deeper water (channel)
habitat.
86
5.0
RECOMMENDATIONS
Overall, healthy, self-sustaining mussel populations appear to be present inside and outside the
AOC in all three tributary rivers (Grasse, Raquette, St. Regis) based on our surveys of 7 sites
inside the AOC and 12 sites outside the AOC (19 sites total). Only a single mussel was found in
the St. Lawrence River shallow nearshore during 2012 surveys, where most all mussels appear to
have been eliminated by zebra mussels.The mussels of the St. Regis River inside and outside the
AOC are the most uncontaminated of the AOC. The mussels of the lower Grasse River are the
most contaminated.
Surveys of mussels for population and reproduction assessment included only 3 of 42 (7.1%)
river segments in the lower Grasse River (this study). Additional survey data are needed to
determine the overall distribution pattern of species and individuals in the river, locations of
mussel beds, and distribution and abundance in nearshore, side slope and channel areas. Mussels
appeared to be more common in shallow nearshore areas with emergent and submergent aquatic
vegetation, although this is a general impression that needs to be supported with additional field
surveys. Additional surveys also would provide more information on the presence or absence of
rare species, and possibly estimates of density depending on the survey methods employed. Two
species considered Endangered in Canada could occur in the lower Grasse River. Ligumia
nasuta, was reported by Erickson in 2008, although he later decided the mussels he found were
not this species, it could be present (Jock, personal communications 2015). Strayer suggested
Obovaria olivaria could be present in the lower Grasse River as well (Dittman, personal
communications 2014). Future surveys should look for these species, and could be designed to
search the nearshore, slope, and main channel habitats of the river to gather data on the number
of individuals of each species present in these habitats. These data would be useful in guiding
dredging, capping, and proposed 2016-2020 remediation activities, as well as post-remediation
mussel community restoration in the lower Grasse River.
Mussel community restoration following Grasse River remediation will need to restore the
habitats used by mussels in the lower Grasse River. Although current knowledge of mussel
distribution is limited, shallow nearshore areas, wetlands with emergent and submergent aquatic
vegetation, and slope areas are important mussel habitats in the lower Grasse River. In particular,
soft, silty substrates with high organic matter appear to be important habitats for species such as
87
Potamilus alatus and Leptodea fragilis. Restoring these habitats may require additional
engineering design beyond the simple sand and topsoil mix proposed for capping. Nearshore
dredging of the Grasse River will remove mussels and main channel capping will bury mussels.
The ability of mussels to recolonize the remediated areas will depend upon, amongst numerous
factors, the suitability of the reconstructed habitat; and the number, species composition, and
proximity of mussels remaining in the lower Grasse River following remediation. Restoration of
lower Grasse River mussels following remediation may not be possible without mitigating for
their loss through transplant and seeding efforts.
Recent efforts on the Hogansburg Hydroelectric Project will result in its decommissioning and
removal by 2016 (SRMT 2015). This project is proposed to restore fish passage for fish species
like walleye, muskellunge, Atlantic salmon, lake sturgeon, and American eel. Pre- and postmonitoring of freshwater mussel species richness and diversity distribution in the impoundment
should be conducted to verify no project impacts to overall populations. A pre-assessment would
help identify any mitigation efforts needed, if any. However, it is recognized this impoundment
is outside (upstream) the AOC boundaries, and already indicative of contaminant free, healthy
reproducing mussel populations.
Additional surveys and/or long term trend monitoring surveys should be designed to track
changes, if any, to freshwater mussel species richness and diversity in the main stem St.
Lawrence River. The freshwater mussel surveys efforts were limited to 2012 presence/absence
sampling efforts only in the St. Lawrence River sites (n=16), and were conducted primarily in
the nearshore (<5 feet of water) (Harper and Jock 2014). Additional surveys in nearshore, side
slopes, and deep water main channel areas should be considered. Such surveys would also
identify the extent of current zebra mussel infestation in the St. Lawrence River.
On the St. Lawrence River and the lower Grasse River, freshwater mussels may be useful
indicators of Grasse River contamination during remediation activities, as has been done at
contaminated sites on the Niagara River. On the Niagara River and several other locations in the
Great Lakes, caged Elliptio complanata have been used to monitor the concentrations of
contaminants at hazardous waste sites and to document the effectiveness of remedial actions
(Richman et al. 2011). Mussels are collected from a clean source area and transferred to
88
contaminated sites where they are held in cages anchored to the nearshore areas for 21 days
during July and August (Richman et al. 2011). Mussels have also been used to monitor the
uptake of PCBs by mussels before, during, and after PCB dredging activities in Michigan (Rice
et al. 1987). The authors concluded that there was a significant increase in the available PCBs
during dredging, although PCBs were not mobilized far downstream and that available PCBs in
the water column declined sharply once dredging activities ceased.
Programs of these kinds have proven useful as monitoring tools during remediation activities.
Such programs should be examined to see if they form a useful framework for the
Massena/Akwesasne AOC. In particular, caged mussel studies may provide information on the
remediation of the St. Lawrence River where no live mussels are currently known to be present
and available for sampling. Such studies may also be useful before, during and following the
lower Grasse River remediation.
Long-term trend monitoring could also be conducted by establishing sample plots in the AOC for
periodic sampling of mussels and their contaminant burdens. Such an effort could be hampered
by remedial impacts to freshwater mussels in the lower Grasse River. Long-term monitoring sites
could be incorporated into NOAA's Mussel Watch program, which at the moment has no St.
Lawrence River monitoring stations below the Moses-Saunders Power Dam at Massena.
Potential sampling points in the rivers of the AOC were selected based on known locations of
contamination, mussels, and access points (Table 24), although other suitable sites likely exist as
well. These sites include the St. Regis River, although mussels from this river were largely
uncontaminated. They also include sites on the St. Lawrence River, where zebra mussels may be
used instead of freshwater mussels.
89
Table 24. Potential locations for long term trend monitoring.
River
Segment
Latitude
Longitude
Grasse
GRD11
N 44.947812
W 74.860488
Below ALCOA detention pond
Grasse
GRD22
N 44.958518
W 74.826141
Upstream of Border Patrol station
Grasse
GRD27
N 44.962173
W 74.809376
Shallow bay adjacent to pasture
Raquette
RRD40
N 44.962429
W 74.765347
Rt. 37 turnoff at North Raquette Rd.
Raquette
RRD47
N 44.974468
W 74.743796
Across Rt. 37 from Reynolds
Raquette
RRD51
N 44.978692
W 74.731950
Across Rt. 37 from GM
St. Regis
SRD03
N 44.975298
W 74.660526
Pool area below dam and rapids
St. Regis
SRD09
N 44.988005
W 74.650828
Second to last bay on St. Regis River
St. Regis
SRD15
N 44.998611
W 74.639932
Just upstream of island near mouth
St. Lawrence
SL
N 44.989493
W 74.739755
Downstream of GM, south shore
St. Lawrence
SL
N 44.993712
W 74.723857
Downstream of Alcoa East, south shore
St. Lawrence
SL
N 44.994328
W 74.694413
Raquette Point
River
Site Description
90
6.0
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SRMT Mussels - Saint Regis Mohawk Tribe

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