A Screening Level Probabilistic
Ecological Risk Assessment of
Copper and Cadmium in the
Chesapeake Bay Watershed
Chesapeake Bay Program
410 Severn Avenue, Suite 109
Annapolis, Maryland 21403
l-800-YOUR-BAY
http://www.chesapeakebay.net/bayprogram
September 1997
Lenwood Hall
Printed by the U.S. Environmental Protection Agency for the Chesapeake Bay Program
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September 1997
Final Report
A Screening Level Probabilistic Ecological Risk Assessment of Copper and Cadmium in the
Chesapeake Bay Watershed
Lenwood W. Hall, Jr.
Mark C. Scott
William D. Killen
University of Maryland
Agricultural Experiment Station
Wye Research and Education Center
P.O. Box 169
Queenstown, MD 21658
U. S. Environmental Protection Agency
Environmental Science Center
701 Mapes Road
Ft. Meade, MD 20755-5350
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ABSTRACT
The goal of this study was to conduct a screening level probabilistic ecological risk
assessment for copper and cadmium in the Chesapeake Bay watershed by using the following
distinct phases: problem formulation, analysis and risk characterization. This probabilistic
ecological risk assessment characterized risk by comparing the probability distributions of
environmental exposure concentrations with the probability distributions of species response data
determined from laboratory studies. The overlap of these distributions was a measure of risk to
aquatic life. Comparative risk from copper and cadmium exposure was determined for various basins
in the Chesapeake Bay watershed.
Dissolved copper and cadmium exposure data were available from six primary data sources
covering 102 stations in 18 basins in the Chesapeake Bay watershed from 1985 through 1996.
Highest environmental concentrations of copper (based on 90th percentiles) were reported in the C
and D Canal, Choptank River, Middle River and Potomac River. Sources of copper responsible for
these exposures can not be identified with certainty but human activities such as watercraft
antifouling paint, non-point source runoff (fertilizer) and industrial/municipal effluents are likely
candidates. As expected, the lowest concentrations of copper were reported in areas with the least
amount of direct human activity such as the lower and middle mainstem Chesapeake Bay and the
Nanticoke River. Based on the calculation of 90th percentiles, cadmium concentrations were highest
in the C and D Canal, Potomac River, Upper Chesapeake Bay and West Chesapeake. The high
exposures were likely related to human activities such as industrial/municipal effluents, non-point
source runoff and atmospheric deposition although a direct link can not be established with the
available data. Lowest environmental concentrations of cadmium were reported in areas with the
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least amount of direct human activity such as the lower and middle mainstem Chesapeake Bay and
Susquehanna River.
The ecological effects data used for this risk assessment were derived from copper and
cadmium acute and chronic laboratory toxicity tests conducted in both fresh and salt water.
Fortunately, the effects data were extensive for both metals. Freshwater toxicity data for both metals
were standardized to a hardness of 50 mg/L to allow for accurate rankings of species sensitivity. The
10th percentile (concentration protecting 90% of the species) for all species derived from the
freshwater acute copper toxicity data base was 8.3 ug/L. Within the acute freshwater copper data
base, a lower 10th percentile of 6.9 ug/L was reported for the most sensitive trophic group (benthos).
For acute saltwater copper data, the acute 10th percentile for all species was 6.3 ug/L copper. The
lowest 10th percentile for the most sensitive trophic group within the saltwater acute copper data
base was 4.1 ug/L copper for benthos. The acute 10th percentile for all species in the freshwater
cadmium data base was 5.1 ug/L cadmium. Within the acute freshwater cadmium data base, the
lowest 10th percentile (0.9 ug/L) was reported for fish. The acute 10th percentile for all saltwater
species was 31.7 ug/L. Benthos were the most sensitive trophic group (with adequate data) within
the saltwater data base with a 10th percentile of 23.3 ug/L. The acute toxicity benchmarks described
above ,with at least 8 data points by trophic group, were used to characterize ecological risks for
copper and cadmium in the 18 basins where exposure data were available.
Highest potential ecological risk from copper exposures was reported in the C and D Canal
area of the northern Chesapeake Bay watershed. Relatively high potential ecological risk from
copper exposures was also reported in the Middle River. Moderate potential ecological risk from
copper exposures was reported in the Choptank and Potomac Rivers. Potential ecological risk from
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copper exposures was either low or data were lacking to assess ecological risk in the other fourteen
basins.
Potential ecological risk from cadmium exposures was much lower than for copper. Highest
potential ecological risk from cadmium exposures was reported in the C and D Canal. Low to
moderate potential ecological risk for the most sensitive trophic group (fish) was reported in the
Potomac River, upper mainstem Bay, West Chesapeake, Choptank River and Chester River. In the
other twelve basins, ecological risk was either judged to be low or insufficient data were available
for determining risk.
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ACKNOWLEDGEMENTS
We would like to acknowledge the U.S. Environmental Protection Agency's Chesapeake Bay
Program Office for funding this study through grant number CB993438010. The "Toxics of
Concern Workgroup" of EPA's Toxics Subcommittee is also acknowledged for their support. The
following individuals are acknowledged for providing data: G. F. Reidel and J. R. Scudlark.
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TABLE OF CONTENTS
Page
ABSTRACT i
ACKNOWLEDGMENTS iv
TABLE OF CONTENTS v
LIST OF TABLES vii
LIST OF FIGURES x
1. INTRODUCTION 1
1.1 Problem Formulation 3
1.1.1 Stressor Characteristics 3
1.1.2 Ecosystems at Risk 4
1.1.3 Ecological Effects 4
1.1.4 Endpoints 5
1.1.5 Stressors Potentially Impacting Aquatic Communities 6
1.1.6 Temporal Concurrence of Copper/Cadmium and
Critical Ecological Periods 6
1.1.7 Conceptual Model 7
2. EXPOSURE CHARACTERIZATION 8
2.1 Introduction 8
2.2 Copper and Cadmium Loadings in the Chesapeake Bay Watershed 8
2.3 Chemical Properties of Copper and Cadmium 9
2.4 Measured Concentrations of Copper and Cadmium in the Chesapeake
Bay Watershed 10
2.4.1 Data Sources and Sampling Regimes 10
2.4.2 Methods of Metals Analysis 12
2.4.3 Methods of Data Analysis 13
2.5 Measured Concentrations by Basin 14
2.6 Temporal Trends 16
2.6.1 Patuxent River 16
2.6.2 James and Susquehanna Rivers 16
2.7 Exposure Duration 17
2.7.1 C and D Canal 17
2.7.2 Potomac River 18
2.8 Summary of Exposure Data 20
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Table of Contents (continued) Page
3. ECOLOGICAL EFFECTS 22
3.1 Modes of Toxicity 22
3.1.1 Copper 22
3.1.2 Cadmium 22
3.2 Methods of Toxicity Data Analysis 23
3.3 Effects of Copper and Cadmium from Laboratory Toxicity Tests 25
3.3.1 Acute Toxicity of Copper 25
3.3.2 Chronic Toxicity of Copper 26
3.3.3 Acute Toxicity of Cadmium 27
3.3.4 Chronic Toxicity of Cadmium 27
3.4 Microcosm Studies 28
3.5 Summary of Effects Data 29
4. RISK CHARACTERIZATION 31
4.1 Characterizating Risks 31
4.2 Risk Characterization of Copper in the Chesapeake Bay Watershed 32
4.3 Risk Characterization of Cadmium in the Chesapeake Bay Watershed 33
4.4 Uncertainty in Ecological Risk Assessment 34
4.4.1 Uncertainty Associated with Exposure Characterization 34
4.4.2 Uncertainty Associated with Ecological Effects Data 36
4.4.3 Uncertainty Associated with Risk Characterization 38
5. CONCLUSIONS AND RESEARCH NEEDS 39
6. REFERENCES 42
TABLES 80
FIGURES 143
APPENDICES
Appendix A - Copper risk characterization by basin
Appendix B - Cadmium risk characterization by basin
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LIST OF TABLES
Page
Table 1. Summary of six copper and cadmium data sources used for this risk
assessment 81
Table 2. Summary of copper and cadmium data for all basins and stations.
Maximum concentrations and 90th percentile values (minimum
of four detected concentrations) are presented by station and basin 82
Table 3. Freshwater acute copper toxicity data presented in order from most
to least sensitive species 86
Table 4. The 10th percentile intercepts for freshwater and saltwater copper
toxicity data by test duration and trophic group. These values represent
protection of 90% of the test species 99
Table 5. Saltwater acute copper toxicity data presented in order from most to least
sensitive species 100
Table 6. Freshwater chronic copper toxicity data presented in order from most to
least sensitive species 106
Table 7. Saltwater chronic copper toxicity data presented in order from most to
least sensitive species 110
Table 8. Freshwater acute cadmium toxicity data presented in order from most
to least sensitive species 112
Table 9. The 10th percentile intercepts for freshwater and saltwater cadmium
toxicity data by test duration and trophic group. These values represent
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protection of 90% of the test species 126
Table 10. Saltwater acute cadmium toxicity data presented in order from
most to least sensitive species 127
Table 11. Freshwater chronic cadmium toxicity data presented in order from
most to least sensitive species 136
Table 12. Saltwater chronic cadmium toxicity data presented in order from
most to least sensitive species 139
Table 13.The percent probability of exceeding the acute copper
freshwater or saltwater 10th percentile for all species and the percent
probability of exceeding the acute 10th percentile for the most
sensitive trophic group with n>8 141
Table 14.The percent probability of exceeding the cadmium acute freshwater
or saltwater 10th percentile for all species and the percent probability of
exceeding the acute 10th percentile for the most sensitive trophic group
with n > 8 142
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LIST OF FIGURES
Page
Figure 1. Ecological risk assessment approach 144
Figure 2. Location of the 102 stations where copper and cadmium were
measured from 1985 to 1996. See key to map where stations are
described 145
Figure 3. Quarterly copper measurements from the Patuxent River
(May 1995 to February 1996) 149
Figure 4. Quarterly cadmium measurements from the Patuxent River
(May 1995 to February 1996) 150
Figure 5. Copper measurements from the James River (1990 to 1993) 151
Figure 6. Copper measurements from the Susquehanna River (1990 to 1993) 152
Figure 7. Cadmium concentrations measured every 24 h at three stations
during two 96 h experiments in 1985 153
Figure 8. Copper concentrations measured every 24 h at three stations during
two 96 h experiments in the C and D Canal in April of 1985 154
Figure 9. Cadmium concentrations measured daily for 9 days at Chesapeake
City in the C and D Canal during April and May of 1987 155
Figure 10. Copper concentrations measured daily for 9 days at Chesapeake
City in the C and D Canal during April and May of 1987 156
Figure 11. Cadmium concentrations from successive 24 h samples during
three 96 h experiments at three stations in the Potomac River in
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April of 1986 157
Figure 12. Copper concentrations from successive 24 h samples during three
96 h experiments at three stations in the Potomac River in April of 1986 158
Figure 13. Cadmium concentrations from a 27 day period at three stations in the
Potomac River in April and May of 1988 159
Figure 14. Copper concentrations from a 27 day period at three stations in the
Potomac River in April and May of 1988 160
Figure 15. Cadmium concentrations from a 29 day period at three stations in the
Potomac River in April and May of 1989 161
Figure 16. Copper concentrations from a 29 day period at three stations in the
Potomac River in April and May of 1989 162
Figure 17. Cadmium concentrations during a 22 day period at three stations in
the Potomac River in April and May of 1990 163
Figure 18. Copper concentrations during a 22 day period at three stations in the
Potomac River in April and May of 1990 164
Figure 19. Acute geometric means for copper toxicity data by trophic group
for freshwater and saltwater species 165
Figure 20. Acute copper toxicity data for families of freshwater fish 166
Figure 21. Acute copper toxicity data for various groups of freshwater
benthic species 167
Figure 22. Acute copper toxicity data for various families of saltwater
fish species 168
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Figure 23. Acute geometric means for cadmium toxicity data by trophic
group for freshwater and saltwater species . . . . 169
Figure 24. Freshwater acute cadmium toxicity data for various groups of
benthic species 170
Figure 25. Saltwater acute cadmium toxicity data for various families of
fish species 171
Figure 26. Saltwater acute cadmium toxicity data for various zooplankton
species 172
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SECTION 1
INTRODUCTION
The 1987 Chesapeake Bay Agreement identified the improvement and maintenance of water
quality as the most critical elements in the restoration and protection of the Chesapeake Bay
(Chesapeake Executive Council, 1988). This Agreement also called for the development and
adoption of a Chesapeake Bay Basinwide Toxics Reduction Strategy in order to achieve a reduction
of toxic substances consistent with the Water Quality Act of 1987. The Chesapeake Bay Basinwide
Toxics Reduction Strategy contained various commitments in areas such as research, monitoring and
toxic substance management that were directed to overall chemical reduction in the Chesapeake Bay
watershed (Chesapeake Bay Executive Council, 1988). One commitment specified for the creation
of a Toxics of Concern List (TOC) for the Chesapeake Bay. This TOC list was designed to: (1)
prioritize over 1000 chemicals that may be impacting aquatic life or human health in Chesapeake
Bay by using a risk based ranking system and (2) direct future research efforts and management.
The first TOC list was completed in 1990 and was recently revised in 1996 (U. S. EPA,
1991; U. S. EPA, 1996). The proposed revised list is currently under review. The proposed revised
TOC list was developed using a chemical ranking system that incorporates sources, fate, exposure
and effects of chemicals on Chesapeake Bay living resources and human health (Battelle, 1989).
The TOC list contains both a list of primary toxics of concern as well as a secondary list (chemicals
of potential concern). For both the 1990 and 1996 TOC lists, copper and cadmium were identified
as either primary or secondary toxics of concern. Both of these metals are found naturally in the
environment at low concentrations. Copper is widely discharged in the Chesapeake Bay from both
point sources (metal plating, industrial and domestic waste facilities, boat paints and mineral
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leaching) and non-point sources. Cadmium enters the Chesapeake Bay primarily through industrial
and municipal effluents, landfill leaching, non-point source runoff and atmospheric deposition (U.S.
EPA, 1990).
Although both of these metals have been identified as toxics of concern in the Chesapeake
Bay watershed, a quantitative probabilistic ecological risk assessment has not been conducted for
either metal. The objective of this study was to apply EPA's new Ecological Risk Assessment
paradigm for assessing ecological risk of copper and cadmium in the Chesapeake Bay watershed.
Procedures described in the following documents were used for this assessment: Report of the
Aquatic Risk Assessment and Mitigation Dialogue Group (SETAC, 1994), the EPA Framework for
Ecological Risk Assessment (U. S. EPA, 1992) and a recent paper entitled "An ecological risk
assessment of atrazine in North American surface waters" (Solomon et al., 1996). This probabilistic
risk assessment characterizes risk by comparing probability distributions of environmental exposure
concentrations with the probability distributions of species response data (determined from
laboratory studies). The overlap of these distributions is a measure of potential risk to aquatic life
in Chesapeake Bay. This approach has a number of advantages over a quotient method (comparing
the most sensitive species with the highest environmental concentrations) because it allows, if not
exact quantification, a least a strong sense for the magnitude and likelihood of potential ecosystem
effects of copper and cadmium in Chesapeake Bay. An implied assumption of this approach is that
protecting a large percentage of species will also preserve ecosystem structure and function. The
final result of the risk characterization is expressed as the probability that exposure concentrations
of copper and cadmium (within a defined spatial and temporal range) will exceed concentrations
deemed protective of aquatic life in the Chesapeake Bay watershed.
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1.1 Problem Formulation
This ecological risk assessment has the following distinct phases: Problem Formulation,
Analysis and Risk Characterization (Figure 1). The problem formulation phase involves the
identification of major issues to be considered in the risk assessment. The analysis phase reviews
existing data on exposure (environmental monitoring) and ecological effects (laboratory toxicity
studies). The risk characterization phase involves estimation of the probability of adverse effects on
aquatic populations and communities in potentially impacted areas of the Chesapeake Bay
watershed.
The problem formulation phase of this risk assessment identified the following major issues
to be addressed: stressor characteristics, ecosystems at risk, ecological effects, endpoints, stressors
impacting aquatic communities, temporal concurrence of copper and cadmium, critical ecological
periods and a conceptual model for risk assessment.
1.1.1 Stressor Characteristics
The chemical and physical properties of copper and cadmium are described in detail in the
Exposure section of this report. In the problem formulation phase of this risk assessment, the
solubility, persistence in water and sediment and bioconcentration potential of copper and cadmium
were considered important.
Copper and its salts (e.g. chloride, sulfate) are soluble in water, persistent and may bind to
particulates. Aquatic biota bioconcentrate copper in their tissue. Bioconcentration factors (BCFs)
as high as 2000 for freshwater algae and 28,200 for saltwater bivalves have been reported (U. S.
EPA, 1985a).
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Cadmium is slightly soluble in water although its chloride and sulphate salts are freely
soluble. Cadmium does not easily degrade in aquatic systems and tends to bind to sediments. This
metal is also readily bioaccumulated by aquatic organisms. BCFs as high as 12,400 have been
reported in freshwater fish and 3,160 for a saltwater polychaete ( U. S. EPA, 1985b). In both fresh
and salt waters, particulate matter and dissolved organic matter may bind a substantial portion of
cadmium.
1.1.2 Ecosystems at Risk
The aquatic ecosystem addressed in this risk assessment was the Chesapeake Bay watershed.
Most of the exposure data for copper and cadmium were reported for the mainstem and tributaries
(102 stations in 18 basins/areas) primarily in Maryland waters of Chesapeake Bay (Figure 2).
1.1.3 Ecological Effects
A comprehensive review and synthesis of the copper and cadmium aquatic toxicity literature
was conducted by using literature searches (AQUIRE etc.) and various review documents such as
the U. S. EPA water quality criteria reports (U. S. EPA, 1985a,b). Acute copper toxicity data were
available for 121 species in freshwater and 57 species in saltwater. Chronic toxicity data for copper
were available for 35 freshwater species and 12 saltwater species. For cadmium, acute toxicity data
were reviewed for 139 freshwater species and 88 saltwater species. Chronic cadmium toxicity data
were available for 24 freshwater species and 16 saltwater species.
The following ranking of sensitivities from most to least sensitive, using acute geometric
means by trophic group, was reported for freshwater trophic groups for acute copper toxicity tests:
zooplankton, amphibians, fish and benthos. For saltwater acute copper toxicity data the ranking of
trophic groups from most to least sensitive was phytoplankton, zooplankton, fish, benthos and
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macrophytes. The following ranking (from most to least sensitive) of trophic groups from acute
freshwater cadmium toxicity studies was phytoplankton, zooplankton, fish, benthos and amphibians.
For saltwater acute cadmium toxicity data, the ranking of trophic groups from most to least sensitive
was phytoplankton, zooplankton, benthos, macrophytes and fish.
A review of the acute toxicity data showed that effects of copper on aquatic species have
been reported at concentrations as low as 1.3 ug/L for Daphnia tested in freshwater and 1.2 ug/L for
a bivalve tested in saltwater. For cadmium, acute effects in freshwater have been reported at
concentrations as low as 0.5 ug/L for rainbow trout and in saltwater acute effects have been reported
for concentrations as low as 1.1 ug/L for a shrimp species.
1.1.4 Endpoints
Two types of endpoints defined in the Framework for Ecological Risk Assessment are
assessment endpoints and measurement endpoints (U. S. EPA, 1992). Assessment endpoints are the
actual environmental values that are to be protected. Measurement endpoints are the measured
responses to a stressor that can be correlated with or used to protect assessment endpoints (Suter,
1990). With each higher level of testing, measurement endpoints differ while assessment endpoints
remain the same.
The assessment endpoints for this risk assessment are the long term viability of aquatic
communities in the Chesapeake Bay (fish, invertebrates etc.). Specifically, the protection of at least
90% of the species 90% of the time (10th percentile from species susceptibility distributions) from
acute copper and cadmium exposures is the defined assessment endpoint. Measurement endpoints
include all acute copper and cadmium toxicity data (survival, growth and reproduction) generated
from freshwater and saltwater laboratory toxicity studies.
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1.1.5 Stressors Potentially Impacting Aquatic Communities
When assessing the potential impact of copper and cadmium on aquatic communities in the
Chesapeake Bay watershed it is important to remember that both biotic (food quality and quantity)
and abiotic factors (water quality, other contaminants, physical habitat alteration) influence the
status of biological communities. Individuals within the various biological communities are more
sensitive to contaminant stress than the community as a whole. Therefore, individual losses due to
stressors such as copper and cadmium may or may not impact the viability (persistence, abundance,
distribution) of the population depending on all the factors influencing the population.
1.1.6 Temporal Concurrence of Copper/Cadmium and Critical Ecological Periods
The overlap of contaminant exposures and critical ecological periods is a key issue in the risk
assessment process. The presence of copper and cadmium in the Chesapeake Bay watershed was
determined from exposure data that were primarily collected during the spring and summer at the
various locations (Figure 2). Although these data are somewhat biased due to their temporal
limitations, the data collected during the spring and early summer are likely to represent "worst
case conditions" from non-point source loading. The spring time period in the Chesapeake Bay
watershed is the period of high freshwater input in various tributaries due to snow melt and spring
rains (Schubel and Pritchard, 1987). Therefore, potential loading of copper and cadmium from non
point sources exists. The spring time period is also a critical ecological period for various important
aquatic resources of concern in this risk assessment. Various fish species such as striped bass, white
perch, alewife and blueback herring spawn in the spring in freshwater areas of various bay tributaries
such as the Potomac River, Choptank River, Nanticoke River and the Upper Chesapeake Bay (Hall
et al., 1993). Therefore, early life stages of these fish species may be susceptible to direct impacts
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from metals such as copper and cadmium or indirectly affected if their food organisms (eg.
zooplankton) are impaired. The spring is also a critical period for zooplankton, the trophic
intermediaries between the very productive phytoplankton and the higher trophic groups such as fish.
In oligohaline areas of the Bay, total microzooplankton numbers were reported to peak in May
(Brownlee and Jacobs, 1987). Spring is also a critical period for the lowest trophic group
(phytoplankton) as peak primary production occurs during March through May followed by a
secondary maximum peak during the July and August (Sellner, 1987).
1.1.7 Conceptual Model
Problem formulation is completed with the development of a conceptual model where a
preliminary analysis of the ecosystem at risk, stressor characteristics and ecological effects are used
to define the possible exposure and effects scenarios. The goal is to develop working hypotheses
to determine how the stressor might affect exposed ecosystems. The conceptual model is based on
information about the ecosystem at risk and the relationship between the measurement and
assessment endpoints. Professional judgement is used in the selection of risk hypotheses. The
conceptual model describes the approach that will be used for the analysis phase and the types of
data and analytical tools that will be needed. Specific data gaps and areas of uncertainty will be
described later in this report.
The hypothesis considered in this risk assessment was:
Copper and cadmium may cause permanent reductions at the species and community level
for fish, benthos, zooplankton or phytoplankton in the Chesapeake Bay watershed and these
reductions may adversely impact community structure and function.
The ecological risk of each metal will be evaluated separately.
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SECTION 2
EXPOSURE CHARACTERIZATION
2.1 Introduction
The potential for exposure of aquatic organisms to copper and cadmium is an important
component of a probabilistic ecological risk assessment. Exposure data are used in conjunction with
effects data (see next section) to conduct a risk characterization. The exposure analysis for these
metals considers use rates, sources, loadings, chemical properties and spatial/temporal scale of
measured concentrations (data sources, sampling regimes, analytical methods and data analysis).
2.2 Copper and Cadmium Loading in the Chesapeake Bay Watershed
Anthropogenic activities that contribute to copper loading in Chesapeake Bay are municipal
and industrial effluents (particularly from smelting, refining or metal plating industries), non-point
sources runoff (eg. poultry manure based fertilizer and pesticides), atmospheric depositions,
commercial and recreational boating and water treatment for algae control (U. S. EPA, 1991). In
1985, the estimated annual urban loading of copper in Chesapeake Bay was 230,000 pounds (U. S
EPA, 1994). Total annual atmospheric deposition loads of copper to tidal waters of Chesapeake Bay
were estimated at 24,000 pounds (U. S. EPA, 1994). Maximum annual loading estimates for copper
at Fall Line Monitoring stations in the Susquehanna and James River in 1990 and 1991 were 479,000
and 150,000 pounds, respectively (U. S. EPA, 1993).
Loading of cadmium in the Chesapeake Bay watershed occurs mainly through industrial and
municipal effluents, landfill leaching, non point source runoff and atmospheric deposition ( U. S.
EPA, 1991). In 1985, the estimated annual urban loading of cadmium in Chesapeake Bay was
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14,000 pounds (U. S. EPA, 1994). Total annual atmospheric deposition loads of cadmium to tidal
waters of Chesapeake Bay were estimated at 2,700 pounds (U. S. EPA, 1994). Maximum loading
estimates for cadmium at the Fall Line monitoring stations in the Susquehanna and James Rivers in
1990 and 1991 were 95,000 and 16,490 pounds, respectively (U. S. EPA, 1993).
23 Chemical Properties of Copper and Cadmium
Copper has two main oxidation states: V and 2. The Cu (II) is most environmentally
relevant to aquatic systems and is generally considered the most toxic form to aquatic life. Copper
is present in both soluble and particulate forms in the environment. Copper may remain in soluble
forms and be diluted in the environment or it may bind to particulates. Copper oxide is very
insoluble whereas copper hydroxide is reasonably soluble and potentially bioavailable. Copper
bioavailability is controlled by the presence of iron and manganese oxides in aerobic environments
as well as dissolved organic matter. In anaerobic environments sulfide chemistry dominates.
Processes that control copper reactions with particles are sorption, chelation, coprecipitation and
biological concentration. In freshwater environments, an increase in hardness has been shown to
reduce toxicity. Particulate forms of copper may be deposited in bedloads near the source or
distributed into adjacent environments. Particle size, currents and density determine the final
deposition of copper in the ecosystem. Aquatic biota have a moderate to high potential to
bioconcentrate copper as bioconcentration factors (BCFs) as high as 28,200 have been reported for
saltwater bivalves (U. S. EPA, 1985a). As exposure concentrations of copper decline, BCFs have
been reported to increase.
The oxidation state for cadmium is the 2* ion. Chloride and sulphate cadmium salts are
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highly soluble in water although cadmium is rather insoluble. Soluble forms of cadmium are
removed from the water column by interaction or adsorption onto sediments and by biota. Removal
of cadmium from the water column is controlled by various factors such as complexing ligands,
other metals, oxidation potential, and pH. Cadmium is not rapidly degraded in aquatic systems and
tends to bind to sediment. The inorganic speciation of cadmium is predicted to be dominated by
association with chloride ions in saltwater. In freshwater, total cadmium is dominated by free
hydrated ion (Cd+2) at pH 6 and partitioned between the free ion and carbonate complexes at higher
pH (Byrne et al., 1988). Increasing hardness (calcium carbonate) reduces the toxicity of cadmium
in freshwater. BCFs as high as 12,400 have been reported in freshwater fish (U. S. EPA, 1985).
Although the potential for sediment-bound copper and cadmium to cause risk to sediment
dwelling aquatic biota exists, the focus of this risk assessment was an evaluation of risk to aquatic
biota from exposures to surface water concentrations of these metals. Probabilistic risk assessment
techniques for assessing risk of aquatic species to sediment exposures is still developmental and
contains a higher degree of uncertainty than water column exposures. By using surface water
concentrations in this risk assessment, the results can be more closely related to regulatory issues
such as the U. S. Environmental Protection Agency's water quality criteria for each respective
metal.
2.4 Measured Concentrations of Copper and Cadmium in the Chesapeake Bay Watershed
2.4.1 Data Sources and Sampling Regimes
Dissolved copper and cadmium exposure data from six data sources were available from
1985 to 1996 at 102 stations (18 basins) in freshwater and saltwater tributaries and mainstem areas
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of the Chesapeake Bay watershed ( Figure 2, Tables 1 and 2). For nearly all samples used in this
risk assessment, both copper and cadmium were measured from the same sample. The exception
was the Fall Line data base where there were more measurements for copper. There was no planned
rain event sampling conducted to measure these metals as all samples were collected from a pre-
determined sampling regime. The data sources are described below.
Ambient Toxicity Testing Program CHall et aL 1991. 1992. 1994a and 19961
These data were collected over a period of four years (1990 - 1994) on a limited temporal
scale (August through October and April 1993) at the following locations: Elizabeth River, Potomac
River, Wye River and Patapsco River in 1990; Patapsco River, Potomac River, Wye River in 1991;
Middle River, Nanticoke River and Wye River in 1992-3 and Patapsco River (Baltimore Harbor),
Magothy River, Sassafras River and Severn River in 1994.
Fall Line Monitoring Data CMDE. 1993. 19951
These data were collected at one station each in the Susquehanna and James Rivers monthly
from 1990 to 1993.
NQAA Data fRiedel. 19961
These data were collected quarterly (May, August, November and February) at 15 stations
during 1995 and 1996 in the Patuxent River.
Striped Bass Data (Hall et al.. 1985.1986.1987.1989. 1991 and 19921
Copper and cadmium were measured from 1985 through 1990 in following tributaries or
mainstem areas during April and May as part of an in-situ striped bass contaminant study:
Chesapeake and Delaware (C and D) Canal in 1985; Potomac River in 1986; Choptank River and
C and D Canal in 1987; Potomac River in 1988; Potomac River and Upper Chesapeake Bay in 1989
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and Potomac River and Upper Chesapeake Bay in 1990.
University of Delaware Data f Culberson and Church. 19881
Data were collected at 20 stations in mainstem Chesapeake Bay from the mouth of the Bay
in Virginia to the northern section in Maryland during August of 1985.
Maryland Coastal Plain StTeam Data (Hall et al.. 1994b. 1995a1
Data were collected at 24 Maryland coastal plains stream stations at five different sampling
periods over a two year period (1992-93). Streams from the following basins were sampled for these
metals: Nanticoke, Choptank, Chester, West Chesapeake, Patuxent and Potomac.
2.4.2 Methods of Metals Analysis
Copper and cadmium data reported during the Ambient Toxicity Testing Program were
collected from subsurface depth integrated grab samples (a composite of bottom, mid-depth and
surface samples). All samples were filtered using a 0.40 um polycarbonate membrane and preserved
in ultrex grade nitric acid. Both metals were analyzed using an atomic absorption-furnace (AA-F)
method as outlined in U. S. EPA (1979). The limit of detection for copper was 1 to 2 ug/L; the
cadmium detection limit ranged from 0.5 to 2 ug/L.
Both metals from the Fall Line Monitoring Program were measured from grab samples
at the James River and Susquehanna River stations using ultra clean sampling procedures. Dissolved
concentrations of copper and cadmium were measured using an Inductively coupled plasma mass
spectrometer (ICP-MS) method as described in Fishman and Friedman (1985). The detection limit
was 0.02 ug/L for copper and 0.1 ug/L for cadmium.
In the NOAA study, both copper and cadmium were measured from surface water grab
samples using an ultra-clean technique. All samples were filtered using 0.45 um polypropylene
12
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capsule filters and preserved using 0.2% ultrex grade hydrochloric acid. Metals analysis was
conducted by using an AA-F method as described in Bruland et al. (1979). Detection limits for
copper and cadmium were <0.01 and <0.001 ug/L, respectively, for each metal.
The copper and cadmium data from the Striped Bass Study were collected from both
subsurface grab samples and composite samples (usually 24 h in duration). All samples were filtered
using 0.40 um polycarbonate membranes and preserved using ultrex grade nitric acid. Both metals
were analysed using an atomic absorption furnace (AA-F) method as outlined in U. S. EPA (1979).
Detection limits for copper ranged from 1 to 5 ug/L (< 2 ug/L most of the time). Limits of detection
for cadmium were 0.5 ug/L for all years except 1988 (< 3.5 ug/L).
Copper and cadmium measurements from the University of Delaware Data Base were taken
from discrete water column depths in the mainstem Chesapeake Bay. All samples were filtered with
0.4 um acid cleaned nuclepore membranes, acidified to pH<2 and frozen until analysis. Both metals
were analysed using an AA-F method as described in Danielsson et al.(1978). Limits of detection
for copper and cadmium were <0.4 and <0.006 ug/L, respectively for each metal.
For the Maryland Coastal Plain Stream Data Base, copper and cadmium were measured
from grab samples taken seasonally. All samples were filtered using 0.40 um polycarbonate
membranes and preserved in ultrex grade nitric acid. Both metals were analysed using an AA-F
method (U. S. EPA, 1979). Limits of detections for copper and cadmium were < 0.5 to 2.0 and 0.10
to 0.50 ug/L, respectively.
2.4.3 Methods of Data Analysis
Approaches for handling values below the detection limits include assigning these values as
zero, one-half the detection limit or the detection limit (MacBean and Rovers, 1984; Johnson et al.,
13
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1992). For this risk assessment, copper and cadmium values below the detection limit were assumed
to be log-normally distributed. The distribution of exposure data was calculated based on the
measured values and the concentrations of the non-detects were assumed to be distributed along a
lower extension of this distribution. For example, if 80 out of 100 were reported as non-detects, the
20 measured values were assigned ranks from 81 to 100 and the frequency distribution was
calculated from these 20 values. In some cases in these data sets, actual concentrations were reported
even though they were below the detection limits. When this occurred, the concentrations were used
in the analysis. For cases where more than one value was available at the same time and station,
the highest value was used in the frequency distribution.
For data sets arranged by basin or station with four or more values above the detection limit,
log-normal distributions of exposure concentration were determined as follows. The observations
in each data set were ranked by concentration and for each observation the percentile ranking was
calculated as n/(N+l) where n is the rank sum of the observation and N is the total number of
observations including the non-detects. Percentile rankings were converted to probabilities and a
linear regression was performed using the logarithm of concentration as the independent variable and
normalized rank percentile as the dependent variable. Although non-detects observations were not
included in the regression analysis, they were included in the calculation of the observation ranks.
The 90th percentile concentrations (exceedence of a given value only 10% of the time) were
calculated for sampling stations (or basins) based on the calculated log-normal concentration
distributions.
2.5 Measured Concentrations by Basin
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The 90th percentile values for copper in 18 basins presented in Table 2 showed that values
ranged from a high of 70 ug/L in the C and D Canal to a low of 1.08 ug/L in the Middle mainstem
Chesapeake Bay. The high 90th percentile value in the C and D Canal was likely related to boating
activity (copper based antifouling paint) because two of the stations were located near marina areas
and all stations were affected by the heavy commercial boating traffic that uses this canal. The
second highest 90th percentile value of 22 ug/L copper in the Choptank Basin was likely related to
agricultural activity in the area (poultry manure fertilizer or limited pesticide use). The third highest
90th percentile value for copper (12.9 ug/L) in Middle River was likely related to boating activities
in adjacent marinas or urban runoff. Lower concentrations of copper were generally reported in the
mainstem Chesapeake Bay when compared with the various freshwater and saline tributaries.
Copper 90th percentile values were not calculated for the Severn and Magothy basins due to lack
of data (only two data points for each basin). These values were not calculated for the Chester,
Sassafras, West Chesapeake or Wye basins because fewer than four detected concentrations were
reported.
The 90th percentile values for cadmium in Table 2 ranged from 4.6 ug/L in the C and D
Canal to 0.05 ug/L in the middle mainstem Chesapeake Bay. The high cadmium values in the C
and D Canal mirror the high values reported for copper and are likely related to human activity near
marina areas. The second highest 90th percentile value for cadmium in the Potomac River (2.43
ug/L) is likely related to the proximity of sampling stations near point source discharges from
facilities such as Quantico Marine Base, the Possum Point Power Plant or the Indian Head Military
Facility. In general, the 90th percentile values for cadmium were lower in mainstem areas of the
Chesapeake Bay when compared to the various tributaries. The 90th percentile values for cadmium
15
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were not calculated for the Severn and Magothy basins due to the few number (two) of data points
and these values were not calculated for Baltimore Harbor, James, Middle, Sassafras and Wye
basins because fewer than four detected concentrations were reported.
2.6 Temporal Trends
The NOAA data from the Patuxent River (quarterly sampling in 1995 and 1996) and the Fall
Line Monitoring Data from the James and Susquehanna River (monthly sampling in 1990 to 1993)
were used to examine temporal trends in copper and cadmium over single or multiple years (G. F.
Riedel, personal communication). These were the only data sets that were appropriate for temporal
analysis.
2.6.1 Patuxent River
The quarterly copper data (May, August, November and February) from the 15 locations was
fairly consistent over time at each station with a range of 0.3 to 1.5 ug/L for the entire data set
(Figure 3). The highest values were at station PXT0603 near Bowie, Maryland (South of Route 50)
and station PXT0494 near Route 4 at Wayson's Corner (Figure 2). Cadmium values shown in
Figures 4 were less than 0.12 ug/L at all locations except WBPTXT0045 at Western Branch near
Upper Marlboro, Maryland (maximum value = 0.43 ug/L).
2.6.2 James and Susquehanna Rivers
Monthly measurements of copper in the James River over 4 years (1990 to 1993) ranged
from 0.5 to 9 ug/L (Figure 5). Most values were less than 5 ug/L with the exception of two data
points (8 and 9 ug/L) in April and July of 1991. All cadmium values measured during the same
period were less than 0.5 ug/L.
16
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Monthly measurements of copper in the Susquehanna River during 1990 through 1993 were
generally less than 4 ug/L except for spikes of 7 and 8 ug/L during June and July 1990, respectively.
(Figure 6). Cadmium was only detected from 5 of 55 samples during the 4 year measurement period
in this basin; therefore an assessment of temporal trends was inappropriate.
2.7 Exposure Duration
Exposure data from the C and D Canal (1985 and 1987) and the Potomac River (1986,1988,
1989 and 1990) were used to examine the duration of exposure of both copper and cadmium because
measurements from sequential daily sampling during limited time periods (weeks) were conducted
during multiple years at these highest risk (highest 90th percentiles) locations (Figures 7-18). An
examination of exposure duration will provide insight on the variability of environmental exposures
and frequency of high concentrations.
2.7.1 C and D Canal
Cadmium concentrations measured in the C and D Canal in 1985 at three locations ranged
from 0.8 to 6.1 ug/L during two 96 h measurement periods in the spring ( Hall et al., 1985).
Concentrations were variable during both experiments with occasional spikes occurring (Figure 7).
Copper concentrations in the C and D Canal in 1985 at the same three locations mentioned above
ranged from 9 to 68 ug/L during two 96 h measurement periods with somewhat more variability
occurring during the first experiment than the second (Figure 8).
In 1987 both cadmium and copper measurements were made at one of the same locations
used in 1985 (Chesapeake City) during a 9 day period in late April and early May (Hall et al., 1987).
There was no clear temporal trend in cadmium values which ranged from 0.6 to 2.9 ug/L (Figure 9).
Measurements were generally similar to those reported at this station in 1985 except two higher
17
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values of 4 of 6 ug/L were reported in 1985. Copper concentration in 1987 at Chesapeake City
remained fairly constant during the 9 day measurement period in late April and early May (Figure
10). Copper concentrations at Chesapeake City were much lower in 1987 (5 to 9 ug/L) than reported
in 1985 (22 to 68 ug/L).
The exposure duration data for both cadmium and copper in the C and D Canal showed that
within a given year values were fairly constant for a given station with occasional spikes occurring,
particularly in 1985. Due to the limited data it is not possible to provide any further insight on the
implication of these spikes although it is unlikely than the few measurements that were made would
have detected the highest concentrations present in this area.
2.7.2 Potomac River
Cadmium and copper concentrations were measured daily for 17 days ( three 96 h
experiments) from three stations in the Potomac River in April of 1986 ( Hall et al., 1986).
Cadmium concentrations were more variable, particularly during experiment 2, at the Quantico
Station (middle river station) and the Widewater (downstream station) than Cherry Hill (upstream
station) (Figure 11). During experiment 3, cadmium values were consistently low at all three sites.
Copper concentrations were higher and more variable during the second experiment than either the
first or third experiment (Figure 12). As reported above for cadmium, copper concentrations were
higher at Quantico (middle river station) and Widewater (downstream station) than Cherry Hill
(upstream station).
Cadmium and copper concentrations were measured during a 27 day period at three stations
in the Potomac River in April and May of 1988 (Hall et al., 1988). Cadmium values ranged from 1.4
to 13 ug/L at the three stations; the highest value was reported at the station located on the Maryland
18
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side of the River (Figure 13). Cadmium concentrations at the other two stations were fairly
consistent. Copper concentrations were variable over time at all three sites (ranging from 3 to 10
ug/L) during the measurement period (Figure 14). Peak concentrations for both metals occurred at
same date (April 10) and station (Maryland side of the River).
Cadmium and copper concentrations were measured during a 29 day period at three stations
(same ones used in 1988) in the Potomac River in April and May of 1989. As shown in Figure 15,
all cadmium values were less than or equal to the detection limit of 1 ug/L (Hall et al., 1991).
Copper concentrations were also consistently low (< 3 ug/L) during this period with exception of
one value of 4.2 ug/L at the station on the Virginia side of the river (Figure 16). Both the cadmium
and copper data showed similar temporal trends during the 1989 measurement period.
Cadmium and copper concentrations were measured during a 22 day period ( at the same
three stations used in 1988 and 1989) in April and May in the Potomac River in 1990 (Hall et al.,
1992). Cadmium values were all consistently low (<1 ug/L) at all stations and dates except for one
spike concentration of 4.7 ug/L on April 14 on the Virginia side of the river (Figure 17). Copper
concentrations were consistently less than 5 ug/L during the measurement period with two
exceptions: a 37 ug/L spike at the Virginia station on April 14 and a 12 ug/L spike on the same Hqte
at the station in the Middle of the river (Figure 18). Spikes for both cadmium and copper occurred
at the same date and the same station.
Cadmium and copper exposure duration data from the Potomac River showed that occasional
spikes occur for these metals during a four year period (1986 - 1990). Although the frequency of
these spikes is limited, the likelihood that maximum values occurring in this river were measured
is remote. A comparison of spike values for both metals also suggests that at least in a few cases
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where maximum values were reported at the same location and date a common source may be
involved.
2.8 Summary of Exposure Data
Highest environmental concentrations of copper (based on 90th percentiles) in the
Chesapeake Bay watershed were reported in C and D Canal, Choptank River, Middle River and
Potomac River. Sources of copper responsible for these exposures can not be identified with
certainty but human activities such as watercraft antifouling paint, non point source runoff
(fertilizer) and industrial/municipal effluents are likely candidates. As expected the lowest
concentrations of copper were reported in areas with the least amount of direct human activity such
as the lower and middle mainstem Chesapeake Bay and the Nanticoke River. Exposure duration
analysis of multiple year data sets from the C and D Canal and the Potomac River demonstrated
that copper concentrations can remain fairly constant for several days but spikes occasionally
occurred in both of these systems (maximum values of - 70 ug/L). Quarterly and monthly
measurements of copper in the Patuxent, James and Susquehanna Rivers also showed occasional
spikes of copper (9 ug/L) but at much lower concentrations than reported above.
Based on the calculation of 90th percentiles, cadmium concentrations were highest in the C
and D Canal, Potomac River, Upper Chesapeake Bay and West Chesapeake. The high exposures
were likely related to human activities such as industrial/municipal effluents, non point source runoff
and atmospheric deposition although a direct link can not be established with the available data. As
reported above for copper, the lowest environmental concentrations were reported in areas with the
least amount of direct human impact such as the lower and middle mainstem Chesapeake Bay and
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Susquehanna River. Analysis of exposure duration data for cadmium in the C and D Canal and
Potomac River showed that concentrations were fairly consistent during some time intervals (days)
although spikes of 6.1 ug/L in the C and D Canal and 14 ug/L in the Potomac River were reported.
Spikes of cadmium from quarterly or monthly measurements in the Patuxent, James and
Susquehanna Rivers were rare and even the maximum values were less than 0.5 ug/L.
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SECTION 3
ECOLOGICAL EFFECTS
3.1 Modes of Toxicity
Both copper and cadmium are broad spectrum enzyme inhibitors that impact various trophic
groups of aquatic species. Modes of toxicity for each metal are addressed below.
3.1.1 Copper
Copper is a minor nutrient for both plants and animals at low concentrations and is toxic to
aquatic life at concentrations approximately 10 to 50 times higher. The toxic effects of copper are
avoided in living organisms by (1) developing an active process for eliminating any excess copper
ingested in the diet; (2) by reducing the thermodynamic activity of copper ions virtually to zero by
utilizing the metal only as a prosthetic element tightly bound to specific copper proteins and (3) by
an interaction between zinc and copper (Scheinberg and Stemlieb, 1984). Although little is known
about the primary mode of copper toxicity in plants, the inhibition of photosynthesis and disruption
of plant growth are suspected to be the major insults resulting from copper exposure. Morel et al.
(1978) suggested that one of the targets of copper in diatoms is silica metabolism which leads to a
disruption of cell division.
Copper adversely impacts fish by causing histological alterations in the gill, kidney,
hematopoietic tissue, mechanoreceptors, chemoreceptors and other tissues (Sorenson, 1991).
Reproductive effects from copper exposure such as reduced egg production per female,
abnormalities in newly hatched fry and reduced survival of young have also been reported
(Sorenson, 1991).
3.1.2 Cadmium
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Cadmium is a non essential element that can be both carcinogenic and toxic to aquatic biota
(Wright and Welbourne, 1994). In algae, cadmium has been reported to increase cell volume, lipid
relative volume and vacuole relative volume (Visviki and Rachlin, 1994). Cadmium has been shown
to adversely affect invertebrates by inhibiting calcium influx (Wright, 1980). In fish, cadmium has
been shown to adversely impact several enzyme systems such as those systems involved with
neurotransmission, transepithelial transport, intermediary metabolism and mixed function
oxidase/antioxidant activity (Wright and Welbourne, 1994). Skeletal deformities in fish from low
level exposures to cadmium have also been reported (Muranoto, 1981). In general, a common result
of cadmium exposure in vertebrates is hypocalcemia which is likely related to the inhibition of
calcium influx (Larsson et al., 1981).
3.2 Methods of Toxicity Data Analysis
For freshwater toxicity studies with both copper and cadmium, hardness (concentrations of
calcium and magnesium) is one water quality variable that significantly influences toxicity. As
hardness increases, the toxicity of the trace metal to biota generally decreases due to reduced
bioavailability of the metal or alteration of the osmoregulatory capacity of the organism. The U. S.
Environmental Protection Agency addresses the influence of hardness on both copper and cadmium
toxicity in their development of fresh water quality criteria (U-. S. EPA, 1985a,b). For the copper and
cadmium toxicity data used in this risk assessment, hardness was also considered in the ranking of
sensitivities of various freshwater species. In order to realistically compare freshwater toxicity data
among species all data were standardized to a hardness of 50 mg/L CaC03. Fifty mg/L was selected
because it is the mean hardness value of 24 coastal plains streams sampled five times over a two
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year period in 1992-93 (Hall et al., 1994b; 1995a). The following equation was used to hardness
adjust the freshwater acute and chronic toxicity data:
In LC50 standardized ^ LCjo observed " O't 1 ] 1 n hardneSSg^^^j - In hirdnessstandirdized)
hardneustandardized ^ ^ mg/L aS C3CO3
Slope = b[l] = 0.942 for copper acute data
= 0.855 for copper chronic data
= 1.128 for cadmium acute data
= 0.785 for cadmium chronic data
The primary toxicity benchmark used for this risk assessment was the 10th percentile of
species sensitivity (protection of 90% of the species) from acute exposures. The implied assumption
when using this benchmark is that protecting a large percentage of the species assemblage will
preserve ecosystem structure and function. This level of species protection is not universally
accepted, especially if the unprotected 10% are keystone species and have commercial or
recreational significance. However, protection of 90% of the species 90% of the time (10th
percentile) has been recommended by the Society of Environmental Toxicology and Chemistry
(SETAC, 1994) and others (Solomon et al., 1996). Recent mesocosm studies have reported that this
level of protection is conservative (Solomon et al.,1996; Giddings, 1992).
Copper and cadmium toxicity data were analyzed as a distribution on the assumption that the
data represented the universe of species. An approximation was made since it is not possible to test
all species in the universe. This approximation assumes that the number of species tested (N) is one
less than the number in the universe. To obtain graphical distributions for smaller data sets that are
symmetrical (normal distributions) percentages were calculated from the formula (100 x n/(N + 1))
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where n is the rank number of the datum point and N is the total number of data points in the set
(Parkhurst et al., 1994). This formula compensates for the size of the data sets as small (uncertain)
data sets will give a flatter distribution with more chance of overlap than larger (more certain) data
sets. In cases where there were multiple data points for a given species, the lowest value was used
in the regression analysis of the distribution. Data were plotted using Sigma Plot (Jandel
Corporation, 1992).
33 Effects of Copper and Cadmium from Laboratory Toxicity Tests
Acute and chronic copper and cadmium toxicity data used in this risk assessment were
obtained from the AQUIRE database through 1995, U. S. EPA water quality criteria documents (U.
S. EPA, 1985a, b) and manual searches of grey literature from academia, industry and government
sources. Copper and cadmium acute and chronic toxicity data by water type (freshwater and
saltwater) are discussed below.
3.3.1 Acute Toxicity of Copper
Acute freshwater copper toxicity data were available for 121 species, primarily benthos and
fish, as shown in Table 3. The range of acute toxicity values was 1.3 ug/L for Daphnia to 13,000
ug/L for an aquatic sowbug. Acute geometric means by trophic group for freshwater species showed
that zooplankton (n=4) were most sensitive followed by fish and benthos (Figure 19). Within the fish
trophic group, the Cyprinidae and Salmonidae families contained species that were more sensitive
to acute copper exposures than the other eight families of freshwater fish (Figure 20). The most
sensitive benthic species to acute copper exposures were gastropods followed by amphipods (Figure
21). Despite the variability in sensitivities of the various species and trophic groups, the acute
25
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freshwater 10th percentile value for all species together (8.3 ug/L) and by trophic group (6.9 to 10.8
ug/L) were somewhat similar as shown in Table 4.
Acute copper saltwater toxicity data were available for 57 species as shown in Table 5. As
reported for the acute copper freshwater toxicity studies, most of the data were available for benthos
and fish. Acute copper toxicity ranged from 1.2 ug/L for a bivalve to 346,700 ug/L for a crab species
(Table 5). Acute saltwater geometric means by trophic group (from most sensitive to least sensitive)
were as follows: phytoplankton, zooplankton, fish, benthos and macrophytes (Figure 19). The fish
families with the most sensitive species to saltwater copper exposures were Pleuronectidae,
Antherinidae and Moronidae (Figure 22). The acute saltwater 10th percentiles for all species,
phytoplankton, zooplankton, benthos and fish were 6.3,2.1,9.3,4.1, and 16.1 ug/L, respectively.
(Table 4).
3.3.2 Chronic Toxicity of Copper
Chronic copper toxicity data were available for 35 freshwater species (Table 6). Chronic
values ranged from 3,9 ug/L for the brook trout to 60.4 ug/L for the Northern pike. The lowest
freshwater 10th percentile value (0.8 ug/L) was for zooplankton (Table 4). The 10th percentile for
all species, benthos and fish were similar (=3.8 ug/L). The 10th percentile for all species from
chronic tests (3.8 ug/L) was approximately half the 10th percentile value (8.3 ug/L) reported from
the all freshwater species from acute tests. These data are supportive of the very low acute to chronic
ratios (ACR) generally reported for trace metals (Lussier et al.( 1985).
Saltwater chronic toxicity data were limited to 12 species and actual chronic values were
only reported for the mysid (54 ug/L) and a copepod (64 ug/L) (Table 7). The 10th percentile for
the saltwater chronic toxicity data was 6.4 ug/L (Table 4).
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3.3.3 Acute Toxicity of Cadmium
Acute freshwater cadmium toxicity data were available for 139 species with benthos and fish
the most predominant trophic groups represented (Table 8). Acute cadmium toxicity values ranged
from 0.5 ug/L for rainbow trout to 18,000,000 ug/L for an alterfly. Acute freshwater geometric
means by trophic group showed that phytoplankton were most sensitive followed by zooplankton,
fish, benthos and amphibians (Figure 23). Within the benthic trophic group, various species of
amphipods were somewhat more sensitive than the other benthic species ( Figure 24). The 10th
percentile for all species, zooplankton, benthos and fish were 5.1, 4.0, 12.3 and 0.9 ug/L,
respectively (Table 9).
Acute cadmium saltwater toxicity data were available for 88 species (Table 10). Toxicity
values ranged from 1.1 ug/L for the grass shrimp to 135,000 ug/L for an oligochaete worm. Acute
saltwater geometric means by trophic group (from most sensitive to least sensitive) were
phytoplankton, zooplankton, benthos, macrophytes and fish (Figure 23). Moronidae was the most
sensitive family of fish to acute saltwater cadmium exposures (Figure 25 ). Copepods appeared to
be the most sensitive zooplankton (Figure 26). The saltwater 10th percentile values for all species,
phytoplankton, zooplankton, benthos and fish were 31.7,17.0,15.0,23.3, and 163 ug/L, respectively
(Table 9).
3.3.4 Chronic Toxicity of Cadmium
Freshwater cadmium toxicity data from chronic exposures were reported for 24 species;
twenty chronic values and/or no observed effect concentrations (NOEC) were available (Table 11).
Chronic values ranged from 0.15 ug/L for a cladoceran to 60 ug/L for a rotifer. The 10th percentiles
reported for chronic exposures were 0.4 ug/L for all species, 0.03 ug/L for zooplankton and 1.8 ug/L
27
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for fish (Table 9).
Chronic saltwater cadmium toxicity data were available for 16 species; however, only four
of these data points were either chronic values, NOEC or Lowest Observed Effects Concentrations
(LOEC) (Table 12). The range of values was rather wide as a 28 day NOEC of 4 ug/L was reported
for the mysid and a 120 h LOEC of 1000 ug/L was reported for a nematode. The 10th percentile for
all species (four benthic species) was 0.25 ug/L (Table 9).
3.4 Microcosm Studies
Copper and cadmium microcosm studies with reported MATC, LOEC or NOEC values
were very limited. Pratt et al. (1987) reported NOEC, MATC and LOEC values of 6.6,9.2 and 12.7
ug/L copper for freshwater protozoan communities exposed to copper for 21 days. The MATC of
9.2 ug/L is similar to the 10th percentile reported for all freshwater species subjected to acute copper
exposures (8.3 ug/L) (see Freshwater acute copper section). In another copper microcosm study,
Balczon and Pratt (1994) reported a LOEC of 20.2 to 42.8 ug/L in artificial communities measuring
community structure and a LOEC of 24 to 98.5 ug/L in littoral microcosms. LOECs for measures
of community processes ranged from 42.8 to 310.3 ug/L. The various copper benchmarks used by
Balczon and Pratt (1994) were generally higher than the various 10th percentiles listed by trophic
group in Table 4.
Only one microcosm result was reported for cadmium. Niederlehner et al. (1985) reported
a NOEC of 5.6 ug/L cadmium for colonization rates for protozoan communities. This value is very
similar to the 10th percentile for all species (acute freshwater data) of 5.1 ug/L reported in Table 9.
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3.5 Summary of Effects Data
The 1 Oth percentile for all species derived from the freshwater acute copper toxicity data base
was 8.3 ug/L. Effects were reported at concentrations slightly above 1 ug/L from acute freshwater
exposures although effects at this low range were rare. A comparison of the sensitivity of the
various trophic groups to acute copper freshwater exposures using acute geometric means by trophic
group showed that zooplankton were somewhat more sensitive than fish or benthos. The 1 Oth
percentile for all species in the freshwater chronic data base was 3.8 ug/L copper. This value is
approximately half the 10th percentile for the acute freshwater data. These data suggest a very low
acute to chronic ratio for copper. The 10th percentile for all species exposed to acute saltwater
copper exposures was 6.3 ug/L. This concentration is similar to the acute copper freshwater 10th
percentile (8.3 ug/L) reported above. A comparison of geometric means by trophic group showed
that zooplankton were more sensitive than either fish or benthos. Saltwater chronic data with copper
were limited to four species; a 10th percentile of 6.4 ug/L was determined from these data.
The 10th percentile for all species derived from the freshwater acute cadmium toxicity data
base was 5.1 ug/L. Acute toxicity values as low as 0.5 ug/L cadmium were reported for rainbow
trout. A comparison of the sensitivity of the various trophic groups to acute freshwater cadmium
exposures showed that zooplankton were more sensitive than benthos or fish. The 10th percentile
for all species in the freshwater chronic toxicity data base was 0.4 ug/L. A comparison of the acute
and chronic 10th percentiles shows an acute to chronic ratio of approximately 13. The 10th
percentile for all species in saltwater acute cadmium toxicity data set was 31.7 ug/L. This value is
six times higher than the freshwater acute cadmium 10th percentile. These data suggest that
cadmium is much less toxic in saltwater than freshwater. Saltwater chronic cadmium toxicity data
29
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were very limited (four species). The 10th percentile was 0.25 ug/L based on these limited data
points.
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SECTION 4
RISK CHARACTERIZATION
4.1 Characterizating Risks
One simple and commonly used method for characterizing risks to aquatic biota is the use
of risk quotients. Risk quotients are simple ratios of exposure and effects concentrations where the
susceptibility of the most sensitive species is compared with the highest environmental exposures.
If the exposure concentration equals or exceeds the effects concentration then an ecological risk is
suspected. The quotient method is a valuable first tier assessment that allows a determination of a
worst case effects and exposure scenario for a particular contaminant. However, some of the major
limitations of the quotient method for ecological risk assessment are that it fails to consider
variability of exposures among individuals in a population, ranges of sensitivity among species in
the aquatic ecosystem and the ecological function of these individual species. The probabilistic
approach addresses these various concerns as it expresses the results of an exposure or effects
characterization as a distribution of values rather than a single point estimate. Quantitative
expressions of risks to aquatic communities are therefore determined by using all relevant single
species toxicity data in conjunction with exposure distributions. A detailed presentation of the
principles used in a probabilistic ecological risk assessment are presented by Solomon et al. (1996).
The following sections will summarize the results of the risk characterization phase of this
probabilistic ecological risk assessment of copper and cadmium in the Chesapeake Bay watershed.
The toxicity benchmark used for the risk characterization will be either the freshwater or saltwater
acute 10th percentile for each metal, depending on whether freshwater or saltwater is present within
the basin. The acute 10th percentile was selected for the following reasons: (I) based on laboratory
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experimental data, dissolved and bioavailable copper and cadmium are only in the water column of
the aquatic environment for short periods of time (due to complexation with natural organic
particulates) which are more closely related to acute exposures that chronic exposures; (2) exposure
duration data presented in Section 2 showed that spike concentrations of copper and cadmium are
short-lived (days) in the environment and (3) toxicity data are much more numerous and represent
a wider range of trophic groups for acute studies than chronic studies. In addition to using the acute
10th percentile for all species in freshwater or saltwater, the trophic group with the lowest acute 10th
percentile with at least 8 data points was also used as an additional benchmark (more conservative
approach) to assess possible ecological risk. The U.S. Environmental Protection Agency uses a
minimum value of 8 for development of acute numeric water quality criteria (Stephan et al., 1985).
4.2 Risk Characterization of Copper in the Chesapeake Bay Watershed
Potential ecological risk from copper exposure (and cadmium in section 4.3) was
characterized by using freshwater acute effects data for freshwater areas and saltwater effects data
for saltwater areas. The highest potential ecological risk area for copper exposures in the Chesapeake
Bay watershed was reported in the C and D Canal (Table 13; Appendix A). The percent probability
of exceeding the acute freshwater 10th percentile for all species was 86%. For the most sensitive
trophic group (based on acute freshwater exposures), the probability of exceeding the 10th percentile
for benthos was even higher (90%). The second highest risk area for copper exposures in the Bay
watershed was the Middle River (Table 13). The probability of exceeding the 10th percentile for all
species and the probability of exceeding the 10th percentile of the most sensitive trophic group with
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at least eight species (based on acute saltwater exposures) was 47 and 74%, respectively. The third
highest risk area for copper exposures was the Choptank River. The percent probability of exceeding
the 10th percentile for all species and most sensitive trophic group with at least eight species
(benthos = 6.9 ug/L) was 29 and 32 %, respectively. The Potomac River was the fourth highest area
for ecological risk. The probability of exceeding the 10th percentile for all species and the most
sensitive trophic group with at least eight species (benthos) was 16 and 20%, respectively. The
rankings of the fifth, sixth and seventh highest ecological risk areas were as follows: Upper
mainstem Bay, James River and Baltimore Harbor. The percent probability of exceeding the 10th
percentile for all species ranged from 1.2 to 9.3% for these three areas. . The other 11 basins
evaluated had either very low ecological risk (e.g. Susquehanna River, lower mainstem Bay,
Nanticoke River, Patuxent River or middle mainstem Bay) or data were lacking to determine if
ecological risk existed (Appendix A and Table 2).
4.3 Risk Characterization of Cadmium in the Chesapeake Bay Watershed
The highest potential ecological risk area for cadmium in the Chesapeake Bay watershed
was the C and D Canal area (Table 14; Appendix B). The percent probability of exceeding the acute
freshwater 10th percentile for all species was only 7.5% in the C and D Canal; however, the percent
probability of exceeding the 10th percentile for the most sensitive freshwater trophic group (10th
percentile = 0.9 ug/L for fish) was 88%. The five next highest areas for ecological risk based on the
10th percentile for all species were the upper mainstem Bay, Chester River, Potomac River,
Choptank River and West Chesapeake. The potential of ecological risk in these five areas was low
(< 3.5% using the 10th percentile for all species). Using the 10th percentile for the most sensitive
33
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trophic group (fish) with at least eight species increased the potential risk (11 to 33 %) for these
areas but this level of risk was still judged to be low to moderate. The ecological risk for the other
12 basins was either very low or data were inadequate to assess possible ecological risk (Appendix
B and Table 2).
4.4 Uncertainty in Ecological Risk Assessment
Development of exposure benchmarks, such as the 90th percentile for environmental
concentrations, or toxicity benchmarks, such as the 10th percentile for species susceptibility, may
seem to be exact. However, these values involve uncertainty when extrapolating risks from
laboratory data to aquatic ecosystems. Uncertainty plays a particularly important role in ecological
risk assessment as it impacts problem formulation, analysis of exposure and effects data and risk
characterization. Evaluation of uncertainty in this risk assessment was critical in determining data
gaps (research needs) as described in the final section of the report. Addressing these various
research needs in future efforts will reduce uncertainty.
Uncertainty in ecological risk assessment has three basic sources: (1) lack of knowledge in
areas that should be known; (2) systematic errors resulting from human or analytical error and (3)
non-systematic errors resulting from the random nature of the ecosystem ( e.g. Chesapeake Bay
watershed). The following sections will address specific uncertainty from the above three sources
as associated with exposure data, effects data and risk characterization.
4.4.1 Uncertainty Associated with Exposure Characterization
Copper and cadmium exposure data used for this risk assessment were obtained from 6
different data sources from 1985 to 1996 as described in Section 2. The spatial scale of these data
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(102 stations in 18 basins/mainstem areas) was somewhat limited considering that there are at least
50 major rivers that discharge into the Chesapeake Bay. Exposure data from basins in Virginia
waters of Chesapeake Bay were particularly limited as only the James River Basin and the lower
mainstem Bay were represented. The temporal scale (sampling frequency) of the available data for
the Bay watershed was even more limited. In many cases there were only a few measurements made
for these metals at various stations. Rain event sampling for these metals in tributaries and streams
was not considered in the sampling designs of the various monitoring studies. Although rain event
sampling is more relevant for pesticides that are applied on agricultural crops and enter aquatic
systems during runoff, such events may be important for copper loading resulting from fertilizer use
on crops or copper and cadmium loading from urban stormwater discharges or municipal/ industrial
overflow. Roman-Mas et al. (1994) have recommended a sampling interval of 5% of the duration
of the storm flow as adequate to characterize pesticide concentration distributions in runoff with an
error of less than 5% (for example during an event with storm flow lasting 100 h sampling should
be every 5 h). The sampling frequency of the present exposure data for both metals is clearly
inadequate for rain event sampling.
The copper and cadmium analysis associated with the 6 different laboratories introduces
uncertainty because analytical procedures differed among the laboratories (see Section 2). For
example, samples were collected for analysis using either grab, depth integrated or composite
techniques. In all cases samples were filtered with either 0.4 or 0.45 um filters but the filters were
made of different material ( polycarbonate, polypropylene or nucleopore filters). The method of
metal analysis was somewhat consistent among laboratories as an Atomic Absorption - Furnace
method (AA-F) was used for all data sets except for the Fall Line Data (Inductively Coupled Plasma
35
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Spectrometer - ICP-MS). The detection limits varied among the different laboratories as copper
ranged from < 0.01 to 5.0 ug/L and cadmium ranged from < 0.001 to 3.5 ug/L. Fortunately, the
maximum detection limits for copper (5 ug/L) and cadmium (3.5 ug/L) only occurred during one
year of monitoring data in the Potomac River and Upper Chesapeake Bay in 1988.
4.4.2 Uncertainty Associated with Ecological Effects Data
Due to the relatively small number of species that can be routinely cultured and tested in
laboratory toxicity studies, there is uncertainty when extrapolating these toxicity data to responses
of natural taxa found in the Chesapeake Bay watershed. In the case of copper in the Chesapeake Bay
watershed, freshwater and saltwater acute toxicity were available for 73 and 57 species, respectively,
for use in the calculation of the 10th percentile. Although these data seem adequate for all species,
the distribution among the various trophic groups was weighted more with fish and benthos. Acute
copper data were particularly limited for plants (phytoplankton and macrophytes), zooplankton and
amphibians. Chronic data were limited for both types of water but particularly for saltwater species
(n - 4).
Acute cadmium toxicity data used for the calculation of the 10th percentile were available
for 65 freshwater species and 88 saltwater species. The freshwater acute data were limited for
zooplankton and no data were available for aquatic plants. The saltwater acute cadmium data base
did not include any macrophyte data and the phytoplankton and zooplankton data were also limited.
The freshwater cadmium chronic data did not include any plants or benthos. The saltwater chronic
data base did not include any fish or plants; all species used were benthos.
In addition to more data with an expanded list of species, more ecologically relevant copper
and cadmium toxicity data are needed to reduce uncertainty and address comparisons of laboratory
36
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and field data. Metal speciation, dissolved organic carbon, suspended particulates and bedded
sediments should be considered with laboratory to field extrapolations.
Variability in the results of toxicity tests for a given species tested in different experiments
or by different authors is a potential source of random and systematic errors. In this assessment, the
most conservative (lowest) effect value was used when multiple data points were available for a
given species. The range of toxicity data among trophic groups differed by metal, water type and
exposure period. For example, the acute copper freshwater 10th percentile values among trophic
groups was fairly consistent (6.9 to 10.8 ug/L) for benthos, zooplankton and fish. In contrast, the
saltwater acute cadmium 10th percentile values ranged from 15 ug/L for zooplankton to 163 ug/L
for fish. Using the distribution of susceptibility accounts for this range of data points. Distributions
will be flatter, with greater chance of overlap with exposure distributions, when the range is large.
Acute freshwater and saltwater copper and cadmium toxicity data were primarily used in the
risk characterization as previously discussed. The use of acute data for predicting ecosystem effects
is often questioned and assumed to be an area of significant uncertainty. However, Slooff et al.
(1986) in their review of single species and ecosystem toxicity for various chemical compounds
have reported that there is no solid evidence that predictions of ecosystem level effects from acute
tests are unreliable. The result of Slooff et al. (1986) coupled with the use of a distribution of acute
toxicity data reduces some of the uncertainty associated with using acute data.
Although single species laboratory toxicity tests are valuable in risk assessment, microcosm
and mesocosm data provide the following useful information for assessing the impact of a stressor
on aquatic communities in an ecosystem: (1) aggregate responses of multiple species; (2) observation
of population and community recovery after exposure and (3) indirect effects resulting from
37
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changes in food supply. Unfortunately, microcosm and mesocosm studies that determined No
Observed Effect Concentrations (NOEC) were limited for both copper and cadmium. The lack of
these type data, where the interaction of biotic communities have been assessed under metal
exposure, was a source of uncertainty in this risk assessment since microcosm/mesocosm toxicity
benchmarks were not available for risk characterization.
4.4.3 Uncertainty Associated with Risk Characterization
Many of the uncertainties associated with the variability in the exposure and effects
characterizations discussed above are incorporated in the probabilistic approach used in this risk
assessment (SETAC, 1994). Quantitative estimation of risks are analyzed as a distribution of
exposure and effects data.
Ecological uncertainty includes the effects of confounding stressors such as other
contaminants and the ecological redundancy of the functions of affected species. In the Chesapeake
Bay watershed, numerous contaminants may be present simultaneously in the same aquatic habitats;
therefore, "joint toxicity"may occur. The concurrent presence of various contaminants along with
copper and cadmium makes it difficult to determine the risk of each metal in isolation.
Ecological redundancy is known to occur in aquatic systems. Field studies have shown that
resistant taxa tend to replace more sensitive species under stressful environmental conditions
(Solomon et al., 1996; Giddings et al., 1992) The resistant species may replace the sensitive species
if it is functionally equivalent in the aquatic ecosystem and the impact on overall ecosystem function
is reduced by these species shifts. For this risk assessment, information on the ecological
interactions among species would help to reduce this area of uncertainty.
38
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SECTION 5
CONCLUSIONS AND RESEARCH NEEDS
Potential ecological risk from copper exposure was greater than for cadmium in the
Chesapeake Bay watershed. Potential ecological risk from copper exposures were reported to be
greatest in the C and D Canal area with relatively high risk also predicted in the Middle River.
Other areas where potential ecological risks from copper exposures were judged to be moderate
were the Choptank River and Potomac River. For the other fourteen basins, the ecological risk from
copper exposures was either low or data were lacking in order to assess ecological risk. As reported
above for copper, the area with the highest potential ecological risk from cadmium exposures was
also the C and D Canal area. Low to moderate potential ecological risk from cadimum exposures
to the most sensitive trophic group (fish) was reported in the Potomac River, upper mainstem Bay,
West Chesapeake, Choptank River and Chester River. In the other twelve basins, ecological risk
from cadmium exposures was either low or insufficient data were available for assessing ecological
risk.
The following research is recommended to supplement existing data for assessing the
ecological risks of copper and cadmium in the Chesapeake Bay watershed:
(1) Exposure assessments for copper and cadmium using randomly selected stations are needed on
a broad spatial and temporal scale in the Chesapeake Bay watershed. On a spatial scale, copper and
cadmium data are needed for the major rivers (tributaries) and representative freshwater streams
where these data are lacking, particularly in Virginia waters of the Chesapeake Bay watershed (e.g.
Rappahannock and York basins). Exposure assessments with increased sampling frequency
39
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covering all seasons of the year at representative locations in the Bay watershed (including some of
the basins in this report where data are lacking) are also needed to improve our ability to determine
risk of aquatic biota to these metals. Specifically, rain event sampling (e.g. samples every 2 to 4 h
during the duration of the event) and subsequent measurement of metals in streams or tributaries near
known sources of copper and cadmium are needed. All exposure assessments of copper and
cadmium should be conducted by laboratories using the most updated analytical methods (with
documented and approved Quality Assurance/Quality Control procedures) with detection limits
slightly below the toxicity thresholds for the most sensitive species.
(2) An extensive spatial and temporal exposure assessment of both copper and cadmium is
recommended in the C and D canal area over multiple years. Since the C and D Canal was the
highest risk area for these metals based on data collected in 1985 and 1987, the obvious question is
whether this area still has concentrations that may pose a risk to aquatic biota. Biological
communities should also be sampled in the C and D Canal area to see if they are impaired when
compared to communities in similar habitats.
(3) Acute toxicity data for various trophic groups for both metals in freshwater and saltwater are
recommended for improving the present toxicity data base. Specifically, acute freshwater and
saltwater toxicity data for copper are needed with plants (phytoplankton and macrophytes). For
cadmium, acute freshwater toxicity data are needed for zooplankton and aquatic plants; acute
saltwater cadmium data are lacking for macrophytes, phytoplankton and zooplankton.
40
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(4) Microcosm/mesocosm toxicity data that include the calculation of NOEC, LOEC and chronic
values for both copper and cadmium in freshwater and saltwater environments are needed to provide
insight on the interaction of aggregate species assemblages during metals exposure, recovery
potential of exposed species and possible indirect effects on higher trophic groups. These studies
should be designed to simulate environmentally realistic pulsed exposures of these metals
documented to occur in the environment.
(5) Assessments of biological communities (Index of Biotic Integrity for fish, invertebrates etc) in
aquatic systems that receive the highest exposures of copper and cadmium are recommended to
determine if the predicted ecological risk for these metals can be confirmed with actual field data.
41
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80
-------
TABLES
-------
Table 1. Summary of the six copper and cadmium data sources for this risk assessment.
Detection Limit
Qig/L)
Reference
Data ID
Total#
samples
Sample Period
copper
cadmium
Hall etal., 1991a
AMBTOX90
12
Aug-Sep 1990
2
1-2
Hall etal., 1992a
AMBTOX91
13
Aug-Sep 1991
2
2
Hall et al., 1994a
AMBTOX93
14
Oct 1992 & Apr 1993
1-2
1-2
Hall et al., 1996
AMBTOX94
12
Oct 1994
1
0.5
MDE, 1993, 1995
Fall Line Monitoring
164
monthly 1990-93
0.02
0.1
G.F Reidel, pers. comm.
NOAA/COASTES
60
quarterly 1995-96
<0.01
<0.001
Hall, 1985
Striped Bass Study '85
51
Apr 1985
2
0.5
Hall etal., 1986
Striped Bass Study '86
39
Apr 1986
5
1
Hall et al., 1987
Striped Bass Study '87
40
Apr 1987
1
0.5
Hall etal., 1989
Striped Bass Study '88
49
Apr-May 1988
3
3
Hall etal., 1991b
Striped Bass Study '89
71
Apr-May 1989
1
1
Hall et al., 1992b
Striped Bass Study '90
36
Apr-May 1990
1
0.5
Hall et al., 1994b, 1995a
Md Coastal Plain (CPS)
120
Apr, Jun, Oct 1992-93
0.5-2
0.1-0.5
Culberson & Church, 1988
UDE
20
Aug 1985
<0.4
<0.006
81
-------
Table 2. Summary of copper and cadmium data for all basins and stations. Maximum concentrations and 90th percentile values
(minimum of 4 detected concentrations) are presented by station and basin.
Basin Station Concentration (ng/L)
Samples # Detections Maximum 90th percentile
Data ID
Cu
Cd
Cu
Cd
Cu
Cd
Cu
Cd
Baltimore Harbor
AMBTOX90.91
Patapsco R.
5
5
3
2
3.7
1.4
-
-
AMBTOX94
Bear Creek
1
I
1
0
3.85
BLD
-
-
AMBTOX94
Cuitis Bay
1
1
1
0
2.47
BLD
-
-
AMBTOX94
Middle Branch
I
1
1
0
2.40
BLD
-
-
AMBTOX94
Northwest Harbor
1
1
1
0
2.17
BLD
-
-
AMBTOX94
Outer Harbor
1
1
1
0
1.90
BLD
-
-
AMBTOX94
Sparrows Point
I
1
1
0
2.08
BLD
-
-
Baltimore Harbor
Stations combined
II
11
9
2
3.85
1.4
4.1
-
CAP
Striped Bass Studies
Chesapeake City
37
37
37
36
68
4.3
56
4.2
Striped Bass Studies
Delaware City
16
16
16
16
64
6.1
73
4.9
Striped Bass Studies
Courthouse Pt.
18
18
18
18
53
3.4
50
3.4
C&D Canal
Stations combined
71
71
71
71
68
6.1
70
4.6
Cluster
CPS
URL
5
5
1
3
1.10
1.40
-
-
CPS
USE
5
5
1
1
0.91
0.14
-
-
Chester
Stations combined
10
10
2
4
1.10
1.40
-
1.07
Clwptwk
Striped Bass Studies
Martinak
20
20
20
6
40
3.0
24
2.2
CPS
KGC
5
5
2
2
1.30
0.52
-
-
CPS
UTK
5
5
0
1
BLD
0.16
-
-
Choptank
Stations combined
30
30
22
9
40
3.0
22
1.4
James
AMBTOX90
Elizabeth River
2
2
2
0
3.7
BLD
-
-
Fall Line Monitoring
02035000
71
23
66
0
9.00
BLD
4.48
-
James
Stations combined
73
25
68
0
9.00
BLD
4.5
-
Lower Bav Mainstem
UDE
CB1
1
1
1
1
0.48
0.050
-
-
UDE
CB2
1
1
1
1
0.41
0.064
-
-
UDE
CB3
1
1
1
1
0.40
0.028
-
-
UDE
CB5
1
1
1
1
0.48
0.027
-
-
UDE
CB6
1
I
I
0.72
0.032
-
-
-------
Table 2. continued.
Basin Station
ft Samples
Data ID
Cu
Cd
UDE
CB7
1
1
UDE
CB8
1
1
Lower Bay Mainstem
Stations combined
7
7
Middle Bav Mainstem
UDE
CB9
1
1
UDE
CB10
1
1
UDE
CBM
1
1
UDE
CB12
I
1
UDE
CBI3
1
I
UDE
CB14
1
1
UDE
CR1D
1
1
Middle Bay Mainstem
Stations combined
7
7
Upper Bav Mainstem
Striped Bass Studies
Grove
19
19
Striped Bass Studies
Howell
18
ts
Striped Bass Studies
Spesutie
19
19
Striped Bass Studies
Eikton
6
6
Striped Bass Studies
Kentmorc
5
5
Striped Bass Studies
Havre de Grace
6
6
UDE
CBI5
1
1
UDE
CBI6
1
I
UDE
CB17
1
1
UDE
CB18
I
I
UDE
CB19
1
1
UDE
CB20
!
1
Upper Bay Mainstem
Stations combined
79
79
Magothv
1
AMBTOX94
Gibson Island
I
AMBTOX94
South Ferry
1
I
Magothy
Stations combined
2
2
Middle
AMBTOX93
Frog Mortar
3
3
AMBTOX93
Wilson Point
3
3
Middle
Stations combined
6
6
Concentration (pg/L)
# Detections Maximum 90"* percentile
Cu Cd Cu Cd Cu Cd
1
1
1.39
0.047
-
-
1
1
0.63
0.033
-
-
7
7
1.39
0.064
1.27
0.07
1
I
0.65
0.016
1
1
0.51
0.008
-
-
1
1
0.49
0.006
-
-
1
1
0.60
0.009
-
1
1
0.68
0.022
-
1
1
0.74
0.0! 5
-
-
I
1
1.14
0053
-
-
7
7
1.14
0.053
1.08
005
19
0
9.5
BLD
6.9
18
1
10.0
f.3
6.5
-
19
2
67.0
6.7
164
-
5
0
8
BLD
12
-
4
0
5
BLD
6
-
2
0
13
BLD
-
-
1
1
1.13
0.019
-
-
1
]
100
0.043
-
-
1
1
t.35
0.060
-
-
I
1
2.47
0.066
-
-
1
1
1.35
0.024
-
-
I
1
1.60
0.053
-
-
73
9
67
6.7
8
2.4
1
0
2.66
BLD
.
.
t
0
1 38
BLD
-
-
2
0
2.66
BLD
-
-
3
0
9.9
BLD
-
-
3
1
10.1
2.7
-
-
6
I
10.1
2.7
12.9
-
-------
Table 2. continued.
3?>sin
Station
Concentration (ng/L)
# Samples
# Detections
Maximum
90*
percentile
Data ID
Cu
Cd
Cu
Cd
Cu
Cd
Cu
Cd
AMBTOX93
Bivalve
2
2
0
0
BLD
BLD
-
.
AMBTOX93
Sandy Hill Beach
2
2
1
0
2.0
BLD
-
-
CPS
DMP
5
5
0
3
BLD
0.55
-
-
CPS
FBB
5
5
1
3
0.74
0.32
-
-
CPS
FBI
5
5
2
5
2.00
1.00
-
1.46
CPS
NDB
5
5
0
3
BLD
0.22
-
-
CPS
TLB
5
5
1
2
1.20
0.37
-
.
CPS
UMH
5
5
1
3
1.30
0.78
-
-
Nanticoke
Stations combined
39
39
6
22
2.0
1.00
1.2
0.95
CPS
CAB
5
5
0
5
BLD
1.70
-
3.34
CPS
LYC
5
5
0
5
BLD
1.05
-
2.72
CPS
SEW
5
5
0
3
BLD
1.01
-
-
NOAA/COASTES
LPXT0I73
4
4
4
4
0.60
0.008
0.69
0.012
NOAA/COASTES
PTXCF8747
4
4
4
4
0.90
0.024
1.25
0.029
NOAA/COASTES
PTXCF9575
4
4
4
4
0.89
0.025
1.63
0.039
NOAA/COASTES
PTXDE2792
4
4
4
4
0.80
0.068
0.91
0.010
NOAA/COASTES
PTXDE5339
4
4
4
4
0.74
0.082
1.38
0.114
NOAA/COASTES
PTXDE940I
4
4
4
4
0.79
0.094
0.87
0.134
NOAA/COASTES
PTXDF0407
4
4
4
4
0.83
0.053
1.60
0.074
NOAA/COASTES
PTXED4892
4
4
4
4
1.03
0.117
1.28
0.141
NOAA/COASTES
PTXED9490
4
4
4
4
0.99
0.074
1.17
0.096
NOAA/COASTES
PXT0402
4
4
4
4
1.17
0.086
1.59
0.123
NOAA/COASTES
PXT0494
4
4
4
4
1.43
0.122
1.66
0.193
NOAA/COASTES
PXT0603
4
4
4
4
1.49
0.078
1.79
0.111
NOAA/COASTES
PXT0809
4
4
4
4
1.14
0.014
1.27
0.018
NOAA/COASTES
PXT0972
4
4
4
4
0.47
0.006
0.49
0.008
NOAA/COASTES
WBPXT0045
4
4
4
4
0.88
0.434
1.17
0.895
Patuxent Basin
Stations combined
75
75
60
73
1.49
1.70
1.11
0.47
Potomac
AMBTOX90
Freestone Point
1
1
1
1
6.7
1.48
-
-
AMBTOX90
Indian Head
1
1
1
1
5.9
1.32
-
-
AMBTOX90
Morgantown
5
5
2
2
5.5
1.00
-
-
AMBTOX90
Possum Point
1
1
1
0
3.9
BLD
-
-
AMBTOX90
Dahlgren
5
5
3
3
4.5
1.80
-
-
-------
Table 2. continued.
Basin
Station
Concentration (pg/L)
» Samples
# Detections
Mwimuni
po*
percentile
Data ID
Cu
Cd
Cu
Cd
Cu
Cd
Cu
Cd
CPS
BTM
5
5
0
3
BLD
1.15
.
CPS
CHP
5
5
1
3
2.4
066
_
CPS
COF
5
5
2
4
2.9
0.8S
3.83
CPS
DYN
5
5
0
3
BLD
1.03
CPS
FOR
5
5
1
5
1.1
1.00
-
2.00
CPS
MTW
5
5
2
5
2.3
120
-
1.63
Striped Bass Studies
Cheny Hill
13
13
8
8
47
1.5
32
1.4
Striped Bass Studies
Maryland
25
25
20
6
10
13.0
7
5.6
Striped Bass Studies
Mid
26
26
22
4
9
14.0
7
4.9
Striped Bass Studies
Virginia
32
32
28
8
10
5.0
9
2.9
Striped Bass Studies
Quantico
13
13
10
9
60
6.6
36
3.4
Striped Bass Studies
Widewater
13
13
11
7
72
3.4
36
2.7
Potomac
Stations combined
165
165
165
72
72
14.0
12
2.43
Sassafras
AMBTOX94
Betterton
1
1
1
0
1.35
BLD
.
-
AMBTOX94
Turners Creek
1
1
1
0
2.26
BLD
.
-
CPS
MLC
5
5
0
2
BLD
0.67
-
.
Sassafras
Stations combined
7
7
2
2
2.26
0.67
-
-
Susquehanna
Fall Line Monitoring
01578310
93
55
90
5
8.0
1.24
3.1
0.78
Severn
AMBTOX94
Junction Rt. 50
1
1
1
0
1.39
BLD
-
-
AMBTOX94
Annapolis
1
1
1
0
2.12
BLD
-
-
Severn
Stations combined
2
2
2
0
2.12
BLD
-
-
West Chesapeake
CPS
BEB
5
5
0
4
BLD
1.10
-
2.38
CPS
BRB
5
5
1
3
1.1
0.62
-
-
CPS
NRV
5
5
1
5
1.9
1.40
-
2.43
West Chesapeake
Stations combined
15
15
2
12
1.9
1.4
-
1.55
Wve
AMBTOX90,91,93
Manor House
7
7
3
0
5.4
BLD
-
-
AMBTOX93
Quarter Creek
2
2
0
0
BLD
BLD
-
-
Wye
Stations combined
9
9
3
0
5 4
BLD
-
-
-------
Table 3. Freshwater acute copper toxicity data presented in order from most sensitive to least sensitive species.
FRESHWATER ACUTE COPPER TOXICITY TABLE
Species Method Chemical Hardness LC50 Hard adj Duration Reference
(mg/L as
CaC03)
(ug/L)
LC50
(ug/L)
& effect
Cladoceran,
Daphnia pulex
-
Copper
—
1.3
-
24 hr
LC50
Wakabayashi, et al.
1988
Fathead minnow,
Pimephales promelas
-
Copper
sulfate
18.5
2
5.10
96 hr
LC50
Welsh, etal. 1993
Cladoceran,
Daphmia similis
S
Copper
sufate
-
4.1
-
96 hr
LC50
Soundrapandian &
Venkataraman, 1990
Cladoceran,
Daphnia magna
S
Copper
sulfate
-
4.9
-
48 hr
LC50
Ziegenfuss, et al.
1986
Water flea,
Moina macrocopa
S
Copper
sulfate
-
5.9
-
48 hr
LC50
Hatakeyama &
Sugaya, 1989
Arctic grayling,
Thymallus arcticus
s
Copper
sulfate
41.3
5.93
7.06
24 hr
LC50
Buhl & Hamilton,
1990
Columbia river spire snail,
Fluminicola virens
FT
Copper
chloride
23
7
14.55
14 day
LC50
Nebeker, et al. 1986
Snail,
Juga plicifera
FT
Copper
chloride
21
8
18.12
11 day
LC50
Nebeker, et al. 1986
Guppy,
Poecilia reticulata
s,
Copper
-
8.7
-
96 hr
LC50
Ismail, 1988
-------
Tabic 3. continued.
Species
Giant freshwater prawn,
Macrobrachium rosenbergii
Cladoceran,
Daphnia pulicaria
Cladoceran,
Daphnia lumholzi
Chinook salmon,
Oncorhynchus tshawytscha
Snail,
Bellamya bengalensis
Cladoceran,
Ceriodaphnia dubia
Rainbow/Donaldson trout,
Oncorhynchus mykiss
Invertebrates,
species not reported
Coho Salmon,
Oncorhynchus kisutch
Cutthroat trout,
Salmo clarki
Method Chemical Hardness
(mg/L as
CaCOj)
S,M
FT, M
R
Copper
sulfate
Copper
Copper
sulfate
Copper
sulfate
Copper
sulfate
art. Copper
stream sulfate
S Copper
sulfate
FT, M Copper
chloride
48
13
57.07
41.3
55
41.3
26
LC50 Hard adj Duration Reference
(ug/L) LC50 Sc. effect
(ug/L)
9 _ 96 hr Natarajan, et al.
LC50 1992
9.06 9.46 _ Lind, et al.
Manuscript
94 _ 96 hr Vardia,etal. 1988
LC50
10 35.58 _ Chapman &
McCrady, 1977
11 _ 96 hr Rao & Jayasree,
LC50 1987
13.4 11.82 48 hr Oris,etal. 1991
LC50
13.8 16.52 96 hr Buhl & Hamilton,
LC50 1990
14 12.8 96 hr Clements, et al.
LC50 1989
15.1 18.08 96 hr Buhl & Hamilton,
LC50 1990
15.7 29.07 _ Chakoumakos,
etal. 1979
-------
Table 3. continued.
Species
Cladoceran,
Ceriodaphnia reticulata
Rainbow trout,
Salmo gairdneri
Northern Squawfish,
Ptychocheilus oregonensis
Rotifer,
Brachiortus rubens
S Amphipod,
Gammarus pseudolimnaeus
Striped Bass,
Morone saxatilis
Rotifer,
Brachiortus calyciflorus
Pond snail,
Lymnaea luteola
Shrimp,
Paratya australiensis
Midge,
Chironomus sp.
Method Chemical Hardness
(mg/Las
CaC03)
S, U _ 45
FT, M Copper 23
chloride
FT, M Copper 54
chloride
S Copper 90
sulfate
FT,M Copper 45
sulfate
S, U Copper 34.5
sulfate
S Copper
R Copper 195
sulfate
FT Copper _
sulfate
S, M Copper 50
sulfate
LC50 Hard adj Duration Reference
(ug/L) LC50 & effect
(ug/L)
17 18.77 _ Mount &
Norberg, 1984
17 35.33 _ Chapman, 1975,
1978
18 16.74 _ Andros & Garton,
1980
19 10.92 24 hr Snell & Persoone,
LC50 1989B
20 22.09 _ Arthur &
Leonard, 1970
25 35.46 _ Hughes, 1973
26 _ 24 hr Snell, etal.
LC50 1991
27 7.49 96 hr Khangarot & Ray,
LC50 1988A
29 _ 9 day Daly, etal. 1990
LC50
30 30 _ Rehwoldt, et al.
1973
-------
Table 3. continued.
Species
Atlantic salmon,
Salmo salar
Goldfish,
Carassius auratus
Amphipod,
Gammarus pulex
Snail,
Physa integra
Frog,
Rarta hexadactyla
Astatic clam,
Corbicula Jluminea
Floater mussel,
Anodonta grandis
Midge,
Polypedi}um nubifer
Channel catfish,
Ictalurus punctatus
Alga,
Chlorella vulgaris
Method Chemical Hardness
(nig/Las
CaCOj)
FT, M _ 14
S, U Copper 20
sulfate
R Copper 151
FT, M Copper 45
sulfate
S Copper 20
sulfate
S, U Copper 64
sulfate
Copper 70
sulfate
S Copper _
sulfate
Copper 16
sulfate
LC50
(ug/L)
32
36
37
39
39
40
44
50
54
62
Hard adj Duration Reference
LC50 & effect
(ug/L)
106.18
85.36
13.06
43.07
92.47
31.7
32.05
157.99
96 hr
LC50
96 hr
LC50
24 hr
LC50
48 hr
LC50
96 hr
LC50
96 hr
IC50
Sprague &
Ramsey, 1965
Pickering &
Henderson, 1966
Taylor, etal. 1991
Arthur &
Leonard, 1970
Khangarot, et al.
1985
Rodgers, et al. 1980
Jacobson, et al. 1993
Hatakeyama, 1988
Straus & Tucker,
1993
Ferard, et al. 1983
-------
Table 3. continued.
Species Method Chemical Hardness
(mg/L as
CaC03)
Green algae,
Scenedesmus dimorphus
S
Copper
-
Common carp,
Cyprinus carpio
R, U
Copper
sulfate
19
Snail,
Physa heterostropha
s.u
Copper
sulfate
100
Red sea bream,
Chrsophrys major
NR
Copper
-
Rainbow,
Villosa iris
-
Copper
sulfate
190
Mussel,
Anodonta imbecillis
S
Copper
sulfate
39
Two spotted barb,
Barbus ticto
s
Copper
sulfate
160
Worm,
Nais sp.
S, M
-
50
Silver barb,
Barbus gonionotus
R
Copper
sulfate
-
Mosquitofish,
Gambusia qffinis
S,U
Copper
nitrate
34
LC50 Hard adj
(ug/L) LC50
(ug/L)
62.3
63 156.77
69 35.91
70
83 23.59
86 108.68
88.6 29.61
90 90
91.96
93 133.75
Duration Reference
& effect
72 hr Balasubrahmanyam,
LC50 etal. 1987
Khangarot, et al.
1983
_ Wurtz & Bridges,
1961
96 hr Lan &
LC50 Chen, 1991
24 hr Jacobson, et al.
LC50 1993
96 hr Keller &
LC50 Zam, 1991
96 hr Wagh, et al. 1985
LC50
_ Rehwoldt, et al.
1973
96 hr Jangchudjai, et al
LC50 1987
_ Joshi&Rege, 1980
-------
Table 3. continued.
Species
Midge,
Chironomus tertians
Big claw river shrimp,
Macrobrachium carcitius
Brook trout,
Salvelinus fontinalis
White cloud mountain
minnow,
Tanichthys albonubes
Tubificid worm,
Limnodrilus hoffmeisteri
Sockeye salmon,
Oncorhynchus nerka
Snail,
Gyraulus circumstriatus
Grass carp,
Ctenopharyngodon idella
Mozambique tilapia,
Tilapia mossambica
Method Chemical Hardness
(mg/Las
CaC03)
S Copper _
sulfate
S Copper _
sulfate
FT, M Copper 45
sulfate
_ Copper 0
sulfate
S, U Copper 100
sulfate
R, M Copper 41
chloride
S, U Copper 100
sulfate
S Copper _
sulfate
R Copper _
LC50 Hard adj
(ug/L) LC50
(ug/L)
100
100
100 110.44
100
102 53.08
103 124.18
108 56.21
108
110
Duration Reference
& effect
48 hr Ziegenfuss, et al.
LC50 1986
96 hr Correa, 1987
LC50
_ McKim & Benoit,
1971
48 hr Kitamura, 3 990
LC50
Wurtz & Bridges,
1961
_ Davis & Shand,
1978
Wurtz & Bridges,
1961
96 hr Zhang, et al. 1988
LC50
120hr Rajkumar&
LC50 Das, 1991
-------
Table 3. continued.
Species
Oligochaete,
Lumbriculus variegatus
Ramshom snail,
Helisoma Irivolvis
Bryozoan,
Lophopodelia carteri
Bryozoan,
Plumafella emarginata
Chiselmouth,
Acrocheiius alutaceus
Scud,
Gammarus fasciatus
Brown Bullhead,
Ameirus nebuloosits
Leech,
Erpobdella octoculata
Bluegill,
Lepomis macrochirus
Bluntnose minnow,
Pimephales notatus
Method Chemical Hardness
(mg/L as
CaCOj)
S Copper _
sulfate
S Copper
sulfate
S,U
S,U
FT, M Copper
chloride
S Copper
sulfate
FT, M Copper
sulfate
S
S.U
Copper
sulfate
Copper
sulfate
205
205
54
202
FT, M Copper
sulfate
20
194
LC50 Hard adj
(ug/L) LC50
(ug/L)
130
130
140 37.05
140 37.05
143 133
160
170 45.62
200
200 474.21
210 58.54
Duration Reference
& effect
96 hr Ewell, etal. 1986
LC50
96 hr Ewell, etal. 1986
LC50
_ Pardue & Wood,
1980
_ Pardue & Wood,
1980
_ Andros &
Garton, 1980
96 hr Ewell, et al. 1986
LC50
_ Brangs,etal. 1973
96 hr Yang & Zhang,
LC50 1989
Tarzwell &
Henderson, I960
_ Homing &
Neiheisel, 1979
-------
Table 3. continued.
Species
Scud,
Gammarns lacustris
Ostracod,
Cypris subglobosa
Central Stoneroller,
Camposioma anomalum
Creek Chub,
Semotilus atromaculatus
Blacknose Dace,
Rhinichtys atratuius
Rainbow Darter,
Etheostoma caeruleum
Common Indian toad,
Bufo melanostictus
Fan tail darter,
Etheostoma Jlabeltare
Snail,
Goniobasis livescens
Medaka,
Oryzias latipes
Method Chemical Hardness
(mg/L as
CaCOj)
FT Copper _
R Copper _
FT, M Copper 200
sulfate
FT, M Copper 200
sulfate
FT, M Copper 200
sulfate
FT, M Copper 200
sulfate
S Copper 185
sulfate
S Copper
sulfate
S, M Copper 154
sulfate
S Copper _
acetate
LC50 Hard adj Duration Reference
(ug/L) LC50 & effect
(ug/L)
212 _ 96 hr De March, 1988
LC50
277.3 _ 96 hr Vardia, et al. 1988
LC50
290 78.55 _ Geckler, et al. 1976
310 83.97 _ Geckler, et al. 1976
320 86.67 _ Geckler, et al. 1976
320 86.67 _ Geckler, et al. 1976
320 93.28 96 hr Khangarot & Ray,
LC50 1987
330 _ 96 hr Lydy & Wissing,
LC50 1988
390 135.13 _ Paulson, et al. 1983
410 _ 48 hr Tsuji,etal. 1986
LC50
-------
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-------
Table 3. continued.
Species
Crayfish,
Procambarus clarkii
Pearlspot,
Etroplus maculatus
Midge,
Chironomus decorus
Japanese eel,
Anguilla japonica
Catfish,
Mystus bleekeri
Striped Shiner,
Notropis chrysocephalus
Banded Killifish,
Fundulus diaphanus
Orangethroat Darter,
Etheostoma spectabile
Snail,
Amnicola sp.
Snail,
Viviparus bengalensis
Method Chemical Hardness
(mg/L as
CaCOj)
17
FT, M
S
S
R
FT, M
S, M
S, M
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
240
200
55
FT, M Copper 200
sulfate
50
R Copper 52
sulfate
LC50
(ug/L)
720
732
739
750
776
790
840
850
Hard adj Duration
LC50 & effect
(ug/L)
1989.63
96 hr
LC50
48 hr
LC50
48 hr
LC50
10 day
LC50
177.01
213.98
767.85
230.23
Reference
Rice & Harrison,
1983
Gaikwad, 1989A
Kosalwat & Knight,
1987
Yokoyama, et al.
1988
Khangarot & Ray,
1988B
Geckler, et al. 1976
Rehwoldt, et al.
1972
Geckler, et al. 1976
900
960
900
925.17 96 hr
LC50
Rehwoldt, et al.
1973
Seth et al. 1990
-------
Table 3. continued.
Species
White sucker,
Catostomus commersoni
Pumpkinseed,
Lepomis gibbosus
Turbellarian flatworm,
Dugesia tigrina
Snail,
Campeloma decisum
Prawn,
Macrobrachium
hendersodayanus
Barb,
Barbus arulius
Snake-head catfish,
Channa punctatus
American eel,
Anguilla rostrata
Turbellarian flatworm,
Dugesia dorotocephala
Method Chemical Hardness
(mg/L as
CaCO,)
FT Copper 386
sulfate
FT, M Copper 125
sulfate
S Copper
sulfate
FT, M Copper 45
sulfate
R Copper
sulfate
R Copper 65
sulfate
S Copper _
sulfate
S, U Copper 44
sulfate
R Copper _
sulfate
LC50 Hard adj
(ug/L) LC50
(ug/L)
1210 176.39
1240 522.98
1300
1700 1877.42
1750
1900 1483.87
2130
2540 2865.12
3000
Duration Reference
& effect
6 day Munkittrick &
LC50 Dixon, 1989
_ Spear, 1977;
Anderson & Spear,
1980
96 hr Ewell, et al. 1986
LC50
_ Arthur &
Leonard, 1970
96 hr Patil & Kaliwal,
LC50 1986
24 hr Shivaraj & Patil,
LC50 1988
96 hr Singh & Munshi,
LC50 1990
_ Hinton &
Eversole, 1978
14 day Hall, etal. 1986
LC50
-------
Table 3. continued.
Species Method Chemical Hardness
(mg/Las
CaC03)
Crayfish,
Orconectes rusticus
FT, M
Copper
sulfate
112.5
Catfish,
Clarias lazera
S
Copper
sulfate
-
Snail,
Pomacea canaliculata
S
Copper
sulfate
96
Zebra mussel,
Dreissena potymorpha
-
Copper
sulfate
40
Catfish,
Clarias anguittaris
S
Copper
sulfate
-
Damsel fly,
unidentified
S, M
—
50
Mussel,
Lamellidens marginalis
R
Copper
-
Frog,
Microhyla ornata
R
Copper
sulfate
-
Caddisfly,
unidentified
S, M
-
50
White Perch,
Morone americana
S, M
Copper
nitrate
53
LC50 Hard adj
(ug/L) LC50
(ug/L)
3000 1397.32
3200
3480 1882.14
4000 4935.93
4300
4600 4600
5000
5040
6200 6200
6200 5868.79
Duration Reference
& effect
Hubschman, 1967
96 hr El-Domiaty, 1987
LC50
4.08 hr Estebenet &
LC50 Cazzaniga, 1990
48 hr Waller, et al. 1993
LC50
96 hr Ebele, et al. 1990
LC50
_ Rehwoldt, et al.
1973
96 hr Raj &
LC50 Hameed, 1991
96 hr Rao & Madhastha,
LC50 1987
_ Rehwofdt, et al.
1973
Rehwoldt, et at.
1971
-------
Table 3. continued.
Species
Stonefly,
Acroneuria lycorias
Harlequinfish,
Rasbora heteromorpha
Indian Catfish,
Heteropneustes fossilis
Diatom,
Navicula incerta
Snakehead catfish,
Channa striata
Aquatic sowbug,
Asellus intermedius
Method Chemical Hardness
(mg/L as
CaC03)
S, M Copper 40
sulfate
S Copper _
chloride
_ Copper 128
sulfate
S Copper
S Copper
sulfate
LC50
Hard adj
Duration
Reference
(ug/L)
LC50
(ug/L)
& effect
8300
10242.05
-
Warnick & Bell,
1969
8880
-
48 hr
LC50
Svobodova &
Vykusova, 1988
9440
3893.39
96 hr
LC50
Gupta &
Rajbanshi. 1991
10450
-
96 hr
EC50
Rachlin,et al. 1983
12400
-
72 hr
LC50
Gopal & Devi, 1991
13000
-
96 hr
LC50
Ewell, etal. 1986
-------
Table 4. The 10th percentile intercepts for freshwater and saltwater copper toxicity data by test
duration and trophic group. These values represent protection of 90% of the test species.
Water type
Acute or Chronic
Trophic Group
n
10th Percentile (^g/L)
Freshwater*
acute
All species
73
8.3
zooplankton
4
7.0**
benthos
31
6.9
fish
36
10.8
Freshwater*
chronic
All species
21
3.8
zooplankton
3
0.8**
benthos
7
3.8**
fish
10
3.9
Saltwater
acute
All species
57
6.3
phytoplankton
3
2.1**
zooplankton
7
9.3**
benthos
30
4.1
fish
15
16.1
Saltwater
chronic
All species
4
6.4**
* Hardness adjusted values are used (50 mg/L).
** Due to small data sets (n < 8) these 10th percentiles have a high degree of uncertainty and
were therefore not used for risk estimates.
99
-------
Table 5. Saltwater acute copper toxicity data presented in order from most sensitive to least sensitive species.
SALTWATER ACUTE COPPER TOXICITY TABLE
Species
Bivalve,
Villorita cyprinoides cochi
Alga,
Thalassiosira pseudonana
Pacific oyster,
Crassostrea gigas
Blue mussel,
Mytilus edulis
Sea urchin,
Arbacia punctulata
Summer flounder,
Paralichthys dental us
Alga,
Asterionella japonica
Eastern oyster,
Crassostrea virgirtica
Copepod,
Acartia tonsa
Rotifer,
Brachionus plicatilis
Striped bass,
Morone saxatilis
Method Chemical
S Copper
sulfate
S,U
S,U
FT,M
S,U
S,U
S
R
Copper
sulfate
Copper
sulfate
Copper
Copper
nitrate
Copper
chloride
Copper
chloride
Copper
sulfate
Copper
LC50
(ug/L)
1.214
5.3
5.8
7.3
11.9
12.7
15.1
17
20
24
Duration
& Effect
96 hr LC50
72 hr EC50
growth rate
1.5 hr EC50
reproduction
72 hr EC50
growth rate
24 hr LC50
96 hr LC50
Reference
Abraham, et al.
1986
Erickson, 1972
Martin, etal. 1981
Martin, etal. 1981
Neilheisel &
Young, 1992
Cardin, 1982
Fisher & Jones,
1981
Maclnnes &
Calabrese, 1978
Sosnowski &
Gentile, 1978
Snell & Persoone,
1989A
Wright, 1988
-------
Table 5. continued.
Species
Topsmelt,
Atherinops affinis
Alga,
Nitschia closterium
Softshell clam,
Mya arenaria
American lobster,
Homarus americanus
Dungeness crab,
Cancer magister
Black abalone,
Haliotis cracherodii
Copepod,
Acartia clausi
Winter flounder,
Pseudopleuronectes americanus
Giant freshwater prawn,
Macrobrachium rosenbergii
Red abalone,
Haliotis ru/escens
Atlantic silverside,
Menidia menidia
Method Chemical
S Copper
S,U Copper
chloride
S,U Copper
nitrate
S,U Copper
sulfate
S,U Copper
sulfate
S,U Copper
chloride
FT,M Copper
nitrate
S Copper
S,U Copper
sulfate
FT,M Copper
nitrate
LC50 Duration
(ug/L) & Effect
24 48 hr EC50
reproduction
33 96 hr EC50
growth rate
39
48
49
50
52
52.7
55 96 hr LC50
65
66.6
Reference
Anderson, et al.
1991
Rosco & Rachlin,
1975
Eisler, 1977
Johnson &
Gentile, 1979
Martin, et al. 1981
Martin, et al. 1977
Gentile, 1982
Cardin, 1982
Ismail, etal. 1990
Martin, et al. 1977
Cardin, 1982
-------
TableS. continued.
Species Method Chemical
Copepod, S Copper
Eurytemora affinis chloride
Opposum shrimp, FT Copper
Neomysis mercedis sulfate
Polychaete worm, FT,M Copper
Neanthes arenaceodentata nitrate
Water flea, FT Copper
Moina mongolica sulfate
Giant kelp, _ _
Macrocystis pyri/era
Polychaete worm, S,U Copper
Philoduce maculata sulfate
Copepod, S,U Copper
Pseudodiaptomus coronatus chloride
Tidewater silverside, S,U Copper
Menidia peninsulae nitrate
Mysid, FT,M Copper
Mysidopsis bigelowi nitrate
Greasyback shrimp, R Copper
Metapenaeus ensis sulfate
Fleshy prawn, S Copper
Penaeus chinensis sulfate
LC50 Duration Reference
(ug/L) & Effect
69.4 96 hr LC50 Hall etal. wilh
Eds.
71 96hrLC50 Brandt,et al. 1993
77 _ Pesch & Morgan,
1978
88.8 48 hr LC50 An & He, 1991
100 96hrEC50 Clendenning&
inhibition of North, 1959
photosynthesis
120 _ McLusky &
Phillips, 1975
138 _ Gentile, 1982
140 _ Hansen, 1983
141 _ Gentile, 1982
160 48 hr LC50 Wong, et al. 1993
170 96 hr LC50 Wu & Chen, 1988
-------
Table 5. continued.
Species
Mysid,
Mysidopsis bahia
Polychaete worm,
Nereis diversicolor
Mussel,
Mytilus sp.
Guppy,
Poecilia reticulata
Sheepshead minnow,
Cyprinodon variegatus
Hirame flounder,
Paralichtyhs olivaceus
Florida Pompano,
Trachinotus carolinus
Herring,
Clupedae
Anchovy family,
Engraulididae
Amphipod,
Allorchestes compressa
Brine shrimp,
Artemia salina
Method Chemical LC50
(ug/L)
FT,M Copper 181
nitrate
S,U Copper 200
sulfate
FT Copper 200
S Copper 240
S,U Copper 280
nitrate
_ Copper 360
sulfate
S,U Copper 360
sulfate
FT Copper 440
FT Copper 460
FT Copper 480
sulfate
S Copper 485
sulfate
Duration
& Effect
96 hr LC50
96 hr LC50
96 hr LC50
48 hr LC50
24 hr LC50
48 hr LC50
96 hr LC50
48 hr LC50
Reference
Lussier, et al.
1985
Jones, et al. 1976
Harrison, 1985
Ismail, 1988
Henson, 1983
Wu et al. 1990
Birdsong &
Avavit, 1971
Harrison, 1985
Harrison, 1985
Ahsanullah, et al.
1988
Verriopoulos, et al
1987
-------
Table 5. continued.
Species Method Chemical
Green crab, S,U Copper
Carcinus maenas sulfate
Kadal shrimp, R Copper
Metapenaeus dohsoni sulfate
Rivulus, FT Copper
Rivulus marmoratus sulfate
Mummichog, FT Copper
Fundulus heteroclttus sulfate
Daggerblade grass shrimp, S Copper
Palaemonetes pugio sulfate
Dogfish, S Copper
Scyliorhinus canicula sulfate
Common rangia S,U _
Rartgia cuneata
Snail, _ Copper
Monodonta turbinata sulfate
Fiddler crab, R Copper
Uca triangulariis sulfate
Kuruma shrimp, _ Copper
Penaeus japonicus sulfate
Horn shell, R Copper
Cerithidea cingulata sulfate
LC50 Duration
(ug/L) & Effect
600
840 96 hr LC50
1250 96 hr LC50
1690 96 hr LC50
2100 48 hr LC50
4000 48 hr LC50
7400
8080 48 hr LC50
8280 96 hr LC50
10116 96 hr LC50
12500 120 hr LC50
Reference
Connor, 1972
Sivadasan, et al.
1986
Lin & Dunson,
1993
Lin & Dunson,
1993
Burton & Fisher,
1990
Torres, etal. 1987
Olson & Harrel,
1973
Catsiki, et al. 1993
Devi, 1987
Kuo, etal. 1992
Rao, et al. 1988
-------
Table 5. continued.
Species
Arrowhead,
Sagittaria montevidensis
Crab,
Scylla serrata
Method Chemical LC50
(ug/L)
R Copper 13270
sulfate
S Copper 346700
sulfate
Duration
& Effect
Reference
48 hr LC50
96 hr LC50
Devi, 1987
Nagabhushanam,
et al. 1986
-------
Tabic 6. Freshwater chronic copper toxicity data presented in order from most sensitive to least sensitive species.
FRESHWATER CHRONIC COPPER TOXICITY TABLE
Species
Brook trout,
Saive/musfontinaiis
Columbia river spire snail
Fluminicola virens
Rotifer,
Brachionus calyciflorus
Invertebrates,
species not reported
Snail,
Juga piicifera
Amphipod,
Gammarus pseudoiimnaeus
Chinook salmon,
Oncorhynchus (shawytscha
Biuntnose minnow,
Pimephales notatus
Rotifer,
Brachionus rubens
Method Chemical Hardness Duration, effect Hard adj.
(mg/L as Chronic value Chronic value
CaC03) (ug/L)
ELS Copper
sulfate
FT Copper
chloride
Copper
sulfate
art. Copper
stream sulfate
FT
LC
ELS
LC
S
Copper
chloride
Copper
sulfate
Copper
chloride
Copper
sulfate
Copper
sulfate
37.5 3.873
23 30 day NOEC
mortality
4
Hard <5.04 hrs
LOEC
mortality
5
55 10 day LC50
6
23 30 day NOEC
mortality
6
45 6.066
23 7.4
)94 8.798
90 24 hr NOEC
9.4
(ug/L)
4.987
7.767
11.65
6.675
14.368
2.763
9.4
Reference
Sauter, elal. 1976
Nebeker, et al. 1986
Janssen, et al. 1993
Clements, et al. 1989
Nebeker, et al. 1986
Arthur &
Leonard, 1970
Chapman,
1975,1982
Horning &
Neiheisel, 1979
Snell & Persoone,
1989B
-------
Table 6. continued.
Species
Ciadoceran,
Daphnia magna
Caddisfly,
Clistornia magnified
Snail,
Campeloma decisum
Snail,
Physa integra
Green Algae,
Chlamydomonas reinhardtii
Fathead minnow,
Pimephales promelas
Rainbow trout,
Salmo gairdneri
Puiple Spotted Gudgeon,
Mogurnda mogurnda
White sucker,
Catostomus commersoni
Bluegill,
Lepomis macrochirus
Method Chemical Hardness
(mg/L as
CaCOj)
LC Copper 211
chloride
LC Copper 26
chloride
LC Copper 45
sulfate
LC Copper 45
sulfate
LC Copper 111.5
LC Copper 30
sulfate
ELS Copper 45.4
sulfate
R Copper _
sulfate
ELS Copper 45.4
sulfate
LC Copper 45
sulfate
Duration, effect Hard adj.
Chronic value Chronic value
(ug/L)
9.525
10.39
10.88
10.88
72h NOEC
Pop. growth
12.2
13.97
19.01
20
20.88
(ug/L)
2.805
18.185
11.927
11.927
6.148
21.662
20.742
22.697
Reference
Chapman, et al.
Manuscript
Nebeker, et al.
1984b
Arthur &
Leonard, 1970
Arthur &
Leonard, 1970
Winner &
Owen, 1991
Mount &
Stephan, 1969
McKim,
et al. 1978
Rippon &
Hyne, 1992
McKim,
et al. 1978
28.98
31.732
Benoit, 1975
-------
Table 6. continued.
Species
Lake trout,
Salvelimts namaycush
Water Flea,
Ceriodaphnia dubia
Brown trout,
Sal mo trutta
Scud,
Hyalela azteca
Scud,
Gammarus pulex
Oligochaete,
Lumbriculus variegatus
Midge,
Chironomus tentans
Northern pike,
Esox lucius
Green algae,
Scenedesmus dimorphus
Method Chemical Hardness
(mg/L as
CaC03)
45.4
ELS Copper
sulfate
R
FT
R
FT
FT
ELS
S
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
57.07
ELS Copper 45.4
sulfate
Copper 45.5
sulfate
Copper 151
45.5
45.5
45.4
Green alga,
Selenastrum capricornutum
Duration, effect Hard adj. Reference
Chronic value Chronic value
(ug/L) (ug/L)
30.51 33.122 McKim,
etal. 1978
30.7 27.407 Oris, etal. 1991
30.83 33.448 McKim,
etal. 1978
10 day LC50 _ West, etal. 1993
31
10 day LC50 _ Taylor, etal. 1991
33
10 day LC50 _ West, etal. 1993
35
54 58.5319 West, etal. 1993
60.36 65.592
6 day LC50
61.7
14 day EC50
(cell volume)
85
McKim,
etal. 1978
Balasubrahmanyam,
etal. 1987
Christensen,
etal. 1979
-------
Table 6. continued.
Species Method Chemical Hardness
(mg/L as
CaCOj)
Duckweed,
Lemna minor
Alga,
ChloreUa vulgaris
Midge,
Chironomus riparius
Grass carp,
Ctenopharyngodon idella
Eurasian watermilfoil,
Myriophyllum spicatum
Diatom,
Nitzschia linearis
Snake-head catfish,
Channa striata
S Copper 151
S Copper _
sulfate
S Copper _
Duration, effect
Chronic value
(ug/L)
7 day EC50
119
33 day EC50
growth
180
10dayLC50
200
30 day LC50
240
32 day EC50
root weight
250
5 day EC50
795-815
Hard adj.
Chronic value
(ug/L)
Reference
Walbridge, 1977
Rosko & Rachlin,
1977
Taylor, etal. 1991
Zhang, etal. 1988
Stanley, 1974
Academy of Natural
Sciences, I960.,
Patrick, et al. 1968
91.3 day LC50
5192
Gopal &
Devi. 1991
-------
Table 7. Saltwater chronic copper toxicity data presented in order from most sensitive to least sensitive species.
Species
SALTWATER CHRONIC COPPER TOXICITY TABLE
Method Chemical Duration, effect Reference
Chronic value
(ug/L)
Common bay mussel, FT,U Copper
Mytilus edulis sulfate
Alga, S,U
Scrippsietta faeroense
Green algae,
Enteromorpha sp.
Alga,
Prorocentrum micans
S,U Copper
S,U
Giant kelp, S Copper
Macrocystis pyrifera
Alga, S,U
Gymnodinium splendom
Amphipod, FT Copper
Allorchestes compressa sulfate
30 day EC50
reproduction
2
5 day EC50
growth rate
5
5 day LC50
mortality
9.9
5 day EC5G
growth rate
10
19-20 day
NOEC reprod.
10.2
5 day EC50
growth rate
20
28 day LOEC
mortality
24
Stromgren &
Nielson, 1991
Saifullah, 1978
Fletcher, 1989
Saifullah, 1978
Anderson, et al.
1990
Saifullah, 1978
Ahsanullah &
Williams, 1991
-------
Table 7. continued.
Species
Alga,
Amphidinium carleri
Alga,
Olisthodiscus luteus
Alga,
Skeletonema costatum
Mysid,
Mysidopsis bahia
Copepod
Eurytemora qffinis
Chemical
Duration, effect
Chronic value
(ug/L)
Reference
Copper
nitrate
Copper
chloride
14 day EC50
growth rate
<50
14 day EC50
growth rate
<50
14 day EC50
growth rate
50
54.09
Erickson, et al.
1970
Erickson, et al.
1970
Erickson, et al.
1970
Lussier, et al.
manuscript
Hall etal. With
Eds.
-------
Table 8. Freshwater acute cadmium toxicity data presented in order from most sensitive to least sensitive species.
FRESHWATER ACUTE CADMIUM TOXICITY TABLE
Species
Rainbow/donaldson trout,
Oncorhynchus mykiss
Striped bass,
Morone saxatilis
Rainbow trout,
Salmo gairdneri
Chinook salmon,
Oncorhynchus tshawytscha
Brown trout,
Salmo trutta
Brook trout,
Salvelinus fontinalis
Coho salmon,
Oncorhynchus kisutch
Diatom,
Asterionella formosa
Alga,
mixed spp.
Method Chemical Hardness
(mg/L as
CaC03)
FT, U Cadmium 9.2
chloride
S, U Cadmium 55
chloride
FT,M Cadmium 23
chloride
FT.M Cadmium 21
sulfate
S,M Cadmium 43.5
chloride
S,M Cadmium 42
sulfate
S Cadmium 42
chloride
Cladoceran,
Daphnia pulex
Cadmium 11.1
chloride
Cadmium
chloride
LC50
(ug/L)
0.5
1
1
1.1
1.4
1.5
1.5
2
5
Hard adj.
LC50
(ug/L)
3.37
0.9
2.4
Duration Reference
& effect
1.83
27.31
168 hr
LC50
72 hr
LC50
2.93 96 hr
LC50
1.64
1.83
96 hr
LC50
Cusimano, et ai.
1986
Hughes, 1973
Chapman, 1978
Finlayson &
Verrue, 1982
Spehar & Carlson,
1984
Carroll, et al. 1979
Buhl & Hamilton,
1991
reduction Conway, 1978
in growth
reduct. in Giesy, et al. 1979
popula-
tion
48 hr Lewis &
LC50 Horning II, 1991
-------
Table 8. continued.
Species Method Chemical Hardness
(mg/L as
CaCOj)
Amphipod,
Hyalella azteca
-
Cadmium
chloride
290
Diatom,
Scenedesmus quadracauda
-
Cadmium
chloride
-
Arctic grayling,
Thymallus arcticus
S
Cadmium
chloride
43.5
Amphipod,
Gammarus fossarum
S
Cadmium
chloride
-
Cladoceran,
Simocephalus serrulatits
S,M
Cadmium
chloride
11.1
Mussel,
Anodonta imbecillis
S
Cadmium
chloride
39
Fathead minnow,
Pimephales promelas
S,M
Cadmium
chloride
48
Mummichog,
Fundulus heteroclitus
S
Cadmium
chloride
5
Amphipod,
Gammarus pulex
R
Cadmium
chloride
94.6
Cladoceran,
Ceriodaphnia dubia
S
Cadmium
chloride
-
Cladoceran,
s,u
45
Simocephalus vetulus
LC50
(ug/L)
5
6.1
6.1
6.2
Hard adj.
LC50
(ug/L)
0.69
7.14
Duration Reference
& effect
96 hr Schubauer-Berigan,
LC50 etal. 1993
reduct. in KJass, et al. 1974
cell count
96 hr
LC50
96 hr
LC50
38.23
Buhl & Hamilton,
1991
Musko, et al. 1990
Giesy, etal. 1977
11.7
11.91
12.25
96 hr Keller & Zam,
LC50 1991
_ Spehar, 1982
12.2
13
17
24
163.82
6.33
27.03
96 hr
LC50
96 hr
LC50
48 hr
LC50
Gill & Epple, 1992
McCahon &
Pascoe, 1988
Carlson, et al. 1986
Mount & Norberg,
1984
-------
Table 8. continued.
Species
Prawn,
Macrobrachium
hendersodayanus
Am phi pod,
Gammarus lacustris
Goldfish,
Carassius auratus
Green alga,
Chlorella vulgaris
Green alga,
Selenastrum capricornutum
Mayfly,
Baetis rhodani
Aquatic sowbug,
Asellus aquaticus
Amphipod,
Gammarus pseudolimnaeus
Cladoceran,
Echinisca triserialis
Nematode,
Caenorhabditis elegans
Method Chemical Hardness
(mg/L as
CaC03)
R
FT
FT
FT
R
S,M
R
Cadmium
chloride
Cadmium
Cadmium
chloride
Cadmium
chloride
Cadmium
Cadmium 104.8
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
67
LC50
(ug/L)
34
Hard adj.
LC50
(ug/L)
Duration
& effect
96 hr
LC50
Reference
Patil & Kaliwal,
1986
40.1
48.9
50
50
50
53
54.4
58
60
23
39.1
96 hr
LC50
180 hr
LC50
reduction
in growth
reduction
ingrowth
96 hr
LC50
96 hr
LC50
96 hr
LC50
96 hr
LC50
De March, 1988
Birge, etal. 1985
Hutchinson &
Stokes, 1975
Bartlett, et al. 1974
Williams, et al.
1985
Green, et al. 1986
Spehar & Carlson,
1984
Chandini, 1988
Williams &
Dusenbery, 1990
-------
Table 8. continued.
Species
Amphipod,
Diporeia sp.
Crayfish,
Orconectes virilis
Cladoceran,
Ceriodaphnia reticulata
Amphipod,
Gammarus sp.
Cladoceran,
Moina macrocopa
Bladder snail,
Physa fontinalis
Midge,
Chironmus tertians
Cladoceran,
Daphnia lumholzi
Snail,
Aplexa hypnorum
Large duckweed,
Spirodela polyrhiza
Grass carp,
Cfenophoryngodon idelia
Method Chemical Hardness
(mg/L as
CaCOj)
S Cadmium _
chloride
FT Cadmium 26
chloride
S,U
S.U
S Cadmium
chloride
FT Cadmium
45
50
Cadmium 175
Cadmium
FT,M Cadmium
chloride
S Cadmium
chloride
S Cadmium
chloride
45.3
LC50 Hard adj. Duration Reference
(ug/L) LC50 & effect
(ug/L)
60 _ 96 hr Gossiaux, et al.
LC50 1992
60 125.46 14 day Mirenda, 1986
LC50
66 74.33 _ Mount & Norberg,
1984
70 70 _ Rehwoldt, et al.
1973
71.4 _ 48 hr Hatakeyama&
LC50 Sugaya, 1989
80 _ 96 hr Williams, et al.
LC50 1985
80 19.47 96 hr Hooftman, et al.
Lc50 1989
83 _ 96 hr Vardia,etal. 1988
LC50
93 103.95 _ Holcombe,et al.
1984
100 _ 168 hr Charpentier, et al.
LC50 1987
100 96 hr Zhang, et al i 988
LCSO
-------
Table 8. continued.
Species
Green alga,
Chlorelia saccharophilia
Cladoceran,
Daphnia carinata
Banded killifish,
Fundulus diaphanus
Alga,
Anabaena Jlos-aquae
Common carp,
Cyprinus carpio
Bryzoan,
Lophopodella carteri
Isopod,
Lirceus alabamae
Tubificid worm,
Limnodrilus hoffmeisteri
Tic tac toe barb,
Barbus ticto
Tubificid worm,
Branchiura sowerbyi
Largemouth bass,
Micropterus salmoides
Method Chemical Hardness
(mg/L as
CaCOj)
Cadmium _
chloride
R
S,M
FT
S.U
FT,M
S,M
S
S,M
FT
Cadmium
chloride
Cadmium
sulfate
Cadmium
sulfate
Cadmium
sulfate
Cadmium
chloride
55
Cadmium _
chloride
Cadmium _
chloride
205
Cadmium 152
chloride
5.3
5.3
LC50 Hard adj. Duration
(ug/L) LC50 & effect
(ug/L)
105 _ 96 hr
EC50
no _ 96 hr
LC50
110 98.79
120 _ 96 hr
EC50
138.9 _ 120 hr
LC50
150 30.54
150 42.8
170 2137.49
180.7 _ 96 hr
LC50
240 3017.63
244.1 _ 96 hr
LC50
Reference
Rachlin, et al. 1984
Chandini, 1988
Rehwoldt, et al.
1972
Rachlin, et al. 1984
Birge, etal. 1985
Pardue & Wood,
1980
Bosnak & Morgan,
1981
Chapman, et al.
1982
Wagh, et al. 1985
Chapman, et al.
1982
Birge, etal. 1985
-------
Table 8. continued.
Species
Green alga,
Chlorella pyrenidosa
Diatom,
Navicula incerta
Tubificid worm,
Quistadrilus multsetosus
Tubificid worm,
Tubifex lubifex
Channel catfish,
Ictalurus punctatus
Tubificid worm,
Spirosperma ferox
Tubificid worm,
Varichaeta pacifica
Crayfish,
Orconectes limosus
Snail,
Physa gyrina
Mayfly,
Paraleptophiebia praepedita
Tubificid worm,
Spirosperma rtikolskyi
Method Chemical Hardness
(mg/L as
CaC03)
_ Cadmium _
chloride
S,M Cadmium 5.3
sulfate
S,M Cadmium 5.3
sulfate
FT Cadmium _
chloride
S,M Cadmium 5.3
sulfate
S,M Cadmium 5.3
sulfate
S,M Cadmium
chloride
S,M _ 200
S,M Cadmium 67
chloride
S,M Cadmium 5.3
sulfate
LC50 Hard adj. Duration
(ug/L) LC50 & effect
(ug/L)
250 _ reduction
in growth
310 _ 96 hr
EC50
320 4023.51
320 4023.51
338.3 _ 228 hr
LC50
350 4400.71
380 4777.92
400
410 85.83
449 322.75
450 5658.06
Reference
Hart & Schaife,
1977
Rachlin, et al. 1982
Chapman, et al.
1982
Chapman, et al.
1982
Birge, et al. 1985
Chapman, et al.
1982
Chapman, et al.
1982
Boutet &
Chaisemartin, 1973
Wier & Walter,
1976
Spehar & Carlson,
1984
Chapman, et al.
1982
-------
Table 8. continued.
Species
Leech,
Glossiphonia complanala
Diatom,
Nitzschia costerium
Tubifitid worm,
Stylodrilus heringianus
Tubificid worm,
Rhyacodrilus montana
Rotifer,
Brachionus calyciflorus
Ostracod,
Cypris subglobosa
Bryzoan,
Pectinatetta magnified
Oligochaete,
Lumbriculus variegatus
Loach,
Lepidocephalus thermalis
Rotifer,
Brachionus rubens
American Eel,
Anguilla rostrata
Method Chemical Hardness
(mg/L as
CaC03)
R
SJW
S,M
S
R
s,u
R
S
S,M
Cadmium
chloride
Cadmium
chloride
Cadmium
sulfate
Cadmium
sulfate
5.3
5.3
Cadmium 36.2
chloride
Cadmium
205
Cadmium 290
chloride
Cadmium _
chloride
Cadmium _
chloride
55
LC50 Hard adj
(ug/L) LC50
(ug/L)
480
480
550 6915.41
630 7921.28
650 935.68
687.4
700 142.52
780 107.39
800
810
820 736.42
Duration Reference
& effect
96 hr Brown & Pascoe,
LC50 1988
96 hr Rachlin, et al. 1982
EC50
_ Chapman, et aL
1982
Chapman, et al.
1982
24 hr Couillard,et al.
LC50 1989
96 hr Vardia, et al. 1988
LC50
_ Pardue & Wood,
1980
96 hr Schubauer-Berigan,
LC50 etal. 1993
96 hr Victor, et al. 1986
LC50
24 hr Snell & Persoone,
LC50 1989B
_ Rehwoldt, et al.
1972
-------
Table 8. continued.
Species Method Chemical Hardness
(mg/L as
CaC03)
White sucker,
Catostomus commersoni
FT
Cadmium
sulfate
-
Channel fish,
Nuria danrica
s
Cadmium
nitrate
-
Mosquitofish,
Gambusia affinis
FT,M
Cadmium
chloride
ll.i
Leech,
Erpobdella octoculata
R
Cadmium
chloride
-
Red swamp crayfish,
Procambarus clarki
R
Cadmium
chloride
30.32
Bryzoan,
Plumaiella emarginata
S,U
-
205
Northern squawfish,
Ptychocheilus oregonensis
FT,M
Cadmium
chloride
25
Freshwater crab,
Baryielphusa guerini
S
Cadmium
chloride
-
Midge,
Chironomus sp.
S,U
-
50
Guppy,
Poecilia reticulata
S,U
Cadmium
chloride
20
Midge,
Chironomus riparius
R
Cadmium
chloride
-
LC50
(ug/L)
826
860
900
1000
1040
1090
1092
1120
1200
1270
1350
Hard adj.
LC50
(ug/L)
4915.37
1828.44
221.93
2386.63
1200
3570.1
Duration Reference
& effect
96 hr Munkittrick &
LC50 Dixon, 1988
18 day Abbasi & Soni,
LC50 1986
Giesy, et al. 1977
96 hr Brown & Pascoe,
LC50 1988
96 hr Naqvi & Howell,
LC50 1993
_ Pardue & Wood,
1980
_ Andros & Garton,
1980
Reddy, etal. 1989
96 hr
LC50
Rehwoldl, et al.
1973
_ Pickering &
Henderson, 1966
10.1 hr Williams, et al.
LC50 1986
-------
Table 8. continued.
Species
Indian freshwater perch,
Ambassis ranga
Pumpkinseed,
Lepomis gibbosus
Frog,
Microhyla ornata
Worm,
Nais sp.
Bluegill,
Lepomis macrochirus
Mayfly,
Ephemerella grandis
I so pod,
Asellus bicrenata
Toad,
Bufo arenarun
Green alga,
Scenedesmus obliquus
Green alga,
Ankistrodesmus fasciatus
Alga,
Chlorococcum spp.
Method Chemical Hardness
(mg/L as
CaCOj)
R
S,M
R
S,U
s,u
S,U
FT,M
R
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
sulfate
55
50
20
44
Cadmium 220
chloride
Cadmium _
chloride
Cadmium _
chloride
Cadmium _
chloride
Cadmium _
chloride
LC50 Hard adj. Duration
(ug/L) LC50 & effect
(ug/L)
1350 96 hr
LC50
1500 1347.1
1580 _ 96 hr
LC50
1700 1700
1940 5453.53
2000 2310.22
2130 400.47
2190 _ 96 hr
LC50
2500 _ reduction
in growth
2500 _ reduction
in growth
2500 _ reduction
in growth
Reference
Gaikwad, 1989B
Rehwoldt, et al.
1972
Rao &
Madhyastha, 1987
Rehwoldt, et al.
1973
Pickering &
Henderson, 1966
Warnick & Bell,
1969
Bosnak & Morgan,
1981
Ferrari, et al. 1993
Prasad &
Prasad, 1982
Prasad &
Prasad, 1982
Prasad &
Prasad, 1982
-------
Table 8. continued.
Species
Flag fish,
Jordanella jloridae
Golden shiner,
Notemigonus crysoleucas
Green sunfish,
Lepomis cyanellus
Minnow - carp family,
Cyprinidae
Caddisfly,
(Unidentified)
Mayfly,
Leptophlebia marginata
Frog,
Rana sp.
Snail,
Amnicola sp.
Pearlspot,
Etroplus maculatus
Amphipod,
Gammarus italicus
Pea cockle,
Pisidiumsp.
Method Chemical Hardness
(mg/L as
CaC03)
FT,M Cadmium 44
chloride
FT
S,U
S,U
FT
S,U
R
S
FT
Cadmium
chloride
Cadmium
chloride
Cadmium
sulfate
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
sulfate
20
4.6
50
50
LC50
(ug/L)
2500
Hard adj.
LC50
(ug/L)
2887.78
Duration
& effect
Reference
Spehar, 1976
2800
2840
3000
3400
3600
3700
3800
4400
4750
5000
96 hr
LC50
7983.54
44255.64
3400
3800
96 hr
LC50
120 hr
LC50
96 hr
LC50
96 hr
LC50
24 hr
LC50
120 hr
LC50
Hartwell, et al.
1989
Pickering &
Henderson, 1966
Nishihara, et al.
1985
Rehwoldt, et al.
1973
Gerhardt, 1992
Zcttergren, et al.
1991
Rehwoldt, et al.
1973
Gaikwad, 1989B
Pantani, et al. 1990
Gerhardt, J 992
-------
Table 8. continued.
Species
White cloud mtn minnow,
Tanichthys albonubes
Nile tilapia,
Tilapia nilotica
Mozambque tilapia,
Tilapia mossambica
Threespine stickleback,
Gasterosteus aculeatus
Red shiner,
Notropis lutrensis
Snake-head catfish,
Channa punctatus
Barb,
Barbus conchonius
Damselfly,
(unidentified)
Common indian toad,
Bufo melanostictus
White Perch,
Morone americana
Clawed toad,
Xenopus laevis
Method Chemical Hardness
(mg/L as
CaCOj)
_ Cadmium 0
chloride
S Cadmium _
chloride
R Cadmium _
chloride
Cadmium 115
chloride
Cadmium _
sulfate
Cadmium 147
sulfate
Cadmium _
chloride
50
S,U
S.U
S,M
Cadmium 185
sulfate
55
Cadmium
nitrate
LC50 Hard adj.
(ug/L) LC50
(ug/L)
5200
5200
6000
6500 2540.3
6620
6810 2017.68
7800
8100 8100
8180 1869.91
8400 7543.77
9600
Duration Reference
& effect
48 hr Kitamura, 1990
LC50
96 hr Al-Akel, et al. 1988
LC50
96 hr Gaikwad, 1989B
LC50
Pascoe & Cram,
1977
96 hr Carrier &
LC50 Beitinger, 1988
96 hr Gupta & Rajbanshi,
LC50 1988
96 hr Gill, etal. 1988
LC50
_ Rehwoldt, et al.
1973
96 hr Khangarot & Ray,
LC50 1987
_ Rehwoldt, et al.
1972
48 hr De Zwart & Sloof,
LC50 1987
-------
Table 8. continued.
Species
Mussel,
Lamellidens marginal is
Crayfish,
Orconectes imunis
Mayfly,
Ephemerella ignita
Medaka,
Orzias latipes
Indian catfish,
Heteropneustes fossilis
Stonefly,
Pteronarcella badia
Snake-head catfish,
Channa striata
Midge,
Chironomus plumosus
Catfish,
Mystus vittatus
Turbellarian,
Polycelis felina
Barb,
Bar bus arulius
Method Chemical
R
FT
FT
S
S
FT,M
S
S
R
R
Cadmium
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
sulfate
Cadmium
chloride
Cadmium
Cadmium 175
Cadmium _
chloride
Cadmium _
chloride
Hardness
(mg/L as
CaCOj)
44.4
Cadmium
chloride
65
LC50
(ug/L)
10000
10200
12000
13000
14600
18000
19400
21530
25820
29000
39000
Hard adj.
LC50
(ug/L)
11662.46
Duration
& effect
96 hr
LC50
96 hr
LC50
96 hr
LC50
48 hr
LC50
96 hr
LC50
Reference
Hameed & Raj,
1989
Phipps &
Holcombe, 1985
Brown & Pascoe,
1988
Tsuji, etal. 1986
Gupta, 1988
Clubb, etal. 1975
5240.05
72 hr
LC50
24 hr
LC50
55 hr
LC50
96 hr
LC50
29009.25 96 hr
LC50
Gopal & Devi,
1991
Hooftman, et al.
1989
Datta & Sinha,
1988
Brown & Pascoe,
1988
Shivaraj & PatiJ,
1988
-------
Table 8. continued.
Species
Featherback,
Notopterus notopterus
Turbellarian,
Dendrocoelum lacteum
Turbellarian,
Polycelis tenuis
Caddisfly,
Hydropsyche angustipennis
nj Climbing perch,
Artabas testudineus
Method Chemical Hardness
(mg/L as
CaC03)
S Cadmium _
chloride
S Cadmium _
chloride
FT Cadmium
FT Cadmium
Cadmium
chloride
Caddisfly, R Cadmium
Rhyacophilia dorsaiis chloride
Stonefly, R Cadmium
Dinocras cephalotes chloride
Damselfly, R Cadmium
Enallagma cyathigerum chloride
Dragonfly, R Cadmium
Calopteryx splendens chloride
Water bug, R Cadmium
Sigara dorsaiis chloride
LC50
(ug/L)
Hard adj.
LC50
(ug/L)
Duration
& effect
Reference
44540
-
24 hr
LC50
Ghosh &
Chakrabarti, 1990
46000
-
48 hr
LC50
Brown & Pascoe,
1988
74000
-
96 hr
LC50
Williams, et al.
1985
200000
-
24 hr
LC50
Williams, et al.
1985
300000
-
24 hr
LC50
Banerjee &
Kumari,
1988
400000
-
96 hr
LC50
Brown & Pascoe,
1988
560000
-
96 hr
LC50
Brown & Pascoe,
1988
650000
-
96 hr
LC50
Brown & Pascoe,
1988
1500000
-
96 hr
LC50
Brown & Pascoe,
1988
2400000
-
96 hr
LC50
Brown & Pascoe,
1988
-------
Table 8. continued.
Species
Method Chemical Hardness
(mg/L as
CaC03)
Alderfly, S Cadmium
Sialis luteria chloride
LC50
(ug/L)
18000000
Hard adj.
LC50
(ug/L)
Duration
& effect
24 hr
LC50
Reference
Brown & Pascoe,
1988
-------
Table 9. The 10th percentile intercepts for freshwater and saltwater cadmium toxicity data by test
duration and trophic group. These values represent protection of 90% of the test species.
Water type
Acute or Chronic
Trophic Group
n
10th Percentile (ng/L)
Freshwater*
acute
All species
65
5.1
zooplankton
4
4.0**
benthos
35
12.3
fish
24
0.9
Freshwater*
chronic
All species
18
0.4
zooplankton
4
0.03**
fish
13
1.8
Saltwater
acute
All species
88
31.7
phytoplankton
5
17.0**
zooplankton
7
15.0**
benthos
58
23.3
fish
17
163
Saltwater
chronic
All species - benthos
4
0.25**
* Hardness adjusted values are used (SO mg/L).
** Due to the small data set (n < 8) these 10th percentiles have a high degree of uncertainty and
were therefore not used for risk estimates.
126
-------
Table 10. Saltwater acute cadmium toxicity data presented in order from most sensitive to least sensitive species.
SALTWATER ACUTE CADMIUM TOXICITY TABLE
IS)
•sj
Species
Daggerblade grass shrimp,
Palaemonetes pugio
Opossum shrimp,
Neomysis integer
Mysid,
Mysidopsis bahia
Bivalve,
Villorita cyprinoides cochi
Amphipod,
Eohaustorius estaurius
Striped bass,
Morone saxatilis
Red alga,
Chamoia parvula
Copepod,
Acartia tonsa
Copepod,
Eurytemora affinis
Method Chemical
R
R
R
S
R
R
S
s
Cadmium
Cadmium
chloride
Cadmium
chloride
Cadmium
nitrate
Cadmium
chloride
Cadmum
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
LC50
(ug/L)
1.1
1.38
2.05
2.7
14.5
19
22.8
29
51.6
Duration
& Effect
Reference
96 hr LC50 Thorpe, 1988
96 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
no sexual
reproduction
96 hr LC50
96 hr LC50
Emson & Crane,
1994
Emson & Crane,
1994
Abraham, et al.
1986
Meador, 1993
96 hr LC50 Wright, 1988
Steele &
Thursby, 1983
Toudal &
Riisgard, 1987
Hall et al. 1995b
-------
Table 10. continued.
Species
Method
Chemical
LC50
(ug/L)
Diatom,
Ditylum brightwellii
-
Cadmium
chloride
60
Isopod,
Jaeropsis sp.
S
Cadmium
chloride
67
American lobster,
Homarus americanus
s,u
Cadmium
chloride
78
Pacific oyster,
Crassostrea gigas
s,u
Cadmium
chloride
85
Polychaete worm,
Neanthes arenaceodentata
FT
Cadmium
chloride
86
Amphipod,
Chelura terebrans
S
Cadmium
chloride
100
Mysid,
Mysidopsis bigelowi
FT.M
Cadmium
chloride
110
Amphipod,
Rhepoxynius abronius
S
Cadmium
chloride
150
Diatom,
Thalassiosira pseudonana
-
Cadmium
chloride
160
Polychaete,
Nereis virens
R
Cadmium
chloride
170
Diatom,
Skeletonema costatum
-
Cadmium
chloride
175
Duration
& Effect
Reference
120 hr EC50
growth
168 hr LC50
Canterford &
Canterford, 1980
Hong & Reish,
1987
Johnson &
Gentile, 1979
Watling, 1982
96 hr LC50
168 hrLC50
96 hr LC50
96 hr EC50
growth rate
144 hr LC50
96 hr EC50
growth rate
Pesch, et al.
1986
Hong & Reish,
1987
Gentile, et al.
1982
Hong & Reish,
1987
Gentile &
Johnson, 1982
Mcleese & Ray,
1986
Gentile &
Johnson, 1982
-------
Table 10. continued.
Species
Sheepshead minnow,
Cyprinodon variegatus
Amphipod,
Hyalella azteca
Polychaete worm,
Capitella capitata
Amphipod,
Ampelisca abdita
Copepod,
Amphiascus tenuiremis
Diatom,
Asterionetta japonica
Dungeness crab,
Cancer magister
Rock crab,
Cancer irroratus
Red sea bream,
Chrysophrys major
Amphipod,
Leptocheirus plumulosus
Mangrove oyster,
Isognomort californicum
Method Chemical
S
S
S,U
S,U
FT,M
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
Cadmium
chloride
Cadmium
chloride
LC50
(ug/L)
180.3
190
200
200
224
224.8
247
250
270
300
300
Duration
& Effect
Reference
96hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
72 hr EC50
growth rate
96 hr LC50
96 hr LC50
48 hr LC50
Halletal. 1995b
Schlekat, et al.
1992
Reish, et al.
1976
Redmond, et al.
1994
Green, et al.
1993
Fisher & Jones,
1981
Martin, et al.
1981
Johns & Miller,
1982
Lan & Chen,
1991
Schlekat, et al.
1992
Ringwood, 1990
-------
Table 10. continued.
Species
Method
Chemical
LC50
(ug/L)
Amphipod,
Corophitun irtsidiosum
S
Cadmium
chloride
310
Sand shrimp,
Crangort septemspinosa
S,U
Cadmium
chloride
320
Hermit crab,
Pagurus longicarpus
s,u
Cadmium
chloride
320
Grass shrimp,
Palaemonetes vulgaris
s,u
Cadmium
chloride
420
Copepod,
Nitocra spinipes
FT
Cadmium
chloride
430
Common shrimp,
Crangon crtmgon
S
Cadmium
460
Shrimp,
Leptomysis lingvura
S
Cadmium
chloride
500
Pink shrimp,
Penaeus duorarum
S
Cadmium
chloride
509
Atlantic silverside,
Menidia menidia
S,U
Cadmium
chloride
577
Winter flounder,
Pseudopleuronectes
americanus
S,U
Cadmium
chloride
602
Amphipod,
Grandidierella japonica
s
Cadmium
chloride
717
Duration
& Effect
Reference
168 hr LC50
96 hr LC50
96 hr LC50
48 hr LC50
96 hr LC50
96 hr LC50
Hong & Reish,
1987
Eisler, 1971
Eisler, 1971
Eisler, 1971
Bengtsson &
Bergstrom, 1987
S.Goncalves, et
al. 1989
Gaudy, et al.
1991
Cripe, 1994
Cardin, 1982
Cardin, 1982
Hong & Reish,
1987
-------
Table 10. continued.
Species
Method
Chemical
LC50
(ug/L)
Amphipod,
Allorchestes compressa
FT
Cadmium
chloride
780
Starfish,
Asteria forbesi
S,U
Cadmium
chloride
820
Soft-shell clam,
Mya arenaria
S,U
Cadmium
chloride
850
Kelp,
Laminana saccharina
-
Cadmium
chloride
860
Blue mussel,
Mytilus edulis
R
Cadmium
chloride
960
Aesop shrimp.
Pandalus montagui
R
Cadmium
chloride
1300
Wood borer,
Limnoria tripunctata
S
Cadmium
chloride
1310
Bay scallop,
Argopecten irradians
s,u
Cadmium
chloride
1480
Coho salmon,
Oncorhynchus kisutch
s
Cadmium
chloride
1500
Clam,
Macoma balthica
R
Cadmium
chloride
1700
Copepod,
Pseudodiaptomus coronatus
S,U
Cadmium
chioride
1708
Duration
& Effect
Reference
96 hr LC50
192 hr EC50
growth rate
96 hr LC50
144 hr LC50
168 hr LC50
96 hr LC50
144hrLC50
Ahsanullah, et
al. 1988
Eisler, 1971
Eisler, 1977
Markham, et al.
1980
Nelson, et al.
1988
McLeese & Ray,
1986
Hong & Reish,
1987
Nelson, et al.
1976
Dinnel, et al.
1989
McLeese & Ray,
1986
Gentile, 1982
-------
Table 10. continued.
Species
Ark shell,
Anadara granosa
Hirame flounder,
Paralichthys olivaceus
Mayfly,
Ephemera japonica
Caridean shrimp,
Crangon sp.
Porgy,
Acanthopagrus schiegeli
Green mussel,
Perm viriduis
Cone worm,
Pectinaria californiensis
Ri villus,
Rivulus marmoratus
Amphipod,
Marinogammarus obtusatus
Polychaete,
Ophryotrocha labronica
Eastern oyster,
Crassostrea virginica
Method Chemical LC50
(ug/L)
R Cadmium 1800
sulfate
Cadmium 2000
_ Cadmium 2200
S Cadmium 2300
chloride
_ Cadmium 2300
S Cadmium 2500
chloride
S Cadmium 2600
chloride
FT Cadmium 2890
sulfate
S,M Cadmium 3500
chloride
S Cadmium 3700
chloride
S,U Cadmium 3800
chloride
Duration
& Effect
96 hr LC50
48 hr LC50
24 hr LC50
96 hr LC50
48 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
Reference
Patei &
Anthony, 1991
Wu, et al. 1990
Koyama, et al.
1992
Dinnel, et al.
1989
Koyama, et al.
1992
Mohan, et al.
1986
Reish & LeMay,
1991
Lin & Dunson,
1993
Wright & Frain,
1981
Reish & LeMay,
1991
Calabrese, et al.
1973
-------
Table 10. continued.
Species
Water flea,
Moina mongolica,
Green crab,
Carcinus maenas
Polychaete,
Neanthes grubei
Blue crab,
Callinectes sapidus
Agohaze goby,
Chasmichthys
dolichognathus
Lesser blue crab,
Calinectes similis
Oyster drill,
Urosalpinx cinerea
Striped mullet,
Mugil cephalus
Fiddler crab,
Uca pugilator
Fiddler crab,
Uca triangularis
Oligochaete worm,
Linmodriloides verrucosus
Method Chemical
S.U
s
s,u
s
R
s,u
s.u
R
R,U
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
Cadmium
chloride
Cadmium
chloride
Cadmium
sulfate
LC50
(ug/L)
3890
4100
4700
4700
5500
6350
6600
6600
6800
7660
10000
Duration
& Effect
48 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
48 hr LC50
96 hr LC50
Reference
An & He, 1991
Eisler, 1971
Reish & LeMay,
1991
Frank &
Robertson, 1979
Kuroshima &
Kimura, 1990
Ramirez, et al.
1989
Eisler, 1971
Koyama, et al.
1992
O'Hara, 1973
Devi, 1987
Chapman, et al.
1982
-------
Table 10. continued.
Species
Nematode,
Monhystera disjuncta
Pinfish,
Lagodon rhomboides
Mud snail,
Nassarius obsoletus
Shiner perch,
Cymatogaster aggregata
Green fish,
Girella punctata
Fiddler crab,
Uca annulipes
Mummichog,
Fundulus heteroclitus
Striped killifish,
Fundulus majalis
Freshwater clam,
Egerla radiata
Oligochaete worm,
Tubiflcoides gabriellae
Cunner,
Tautogolabrus adspersus
Method Chemical LC50
(ug/L)
S Cadmium 10000
chloride
S Cadmium 10000
S,U Cadmium 10500
chloride
S Cadmium 11000
chloride
S Cadmium 15700
chloride
R Cadmium 15910
chloride
FT Cadmium 18200
sulfate
S,U Cadmium 21000
chloride
S Cadmium 21400
sulfate
R,U Cadmium 24000
sulfate
R Cadmium 25900
chloride
Duration
& Effect
120 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
96 hr LC50
Reference
Vranken, et al.
1985
Sharp, 1988
Eisler, 1971
Dinnel, et al.
1989
Kuroshima &
Kimura, 1990
Devi, 1987
Lin & Dunson,
1993
Eisler, 1971
Udoidiong &
Akpan, 1991
Chapman, et al.
1982
Robohm, 1986
-------
Table 10. continued.
Species
Rotifer,
Brachionus plicalilis
Oligochaete worm,
Monophylephorus
cuticalatus
Method Chemical LC5Q
(ug/L)
S Cadmium 36300
chloride
R,U Cadmium 135000
sulfate
Duration
& Effect
Reference
24 hr LC50
Snell &
Persoone,
1989A
Chapman, et al.
1982
-------
Table 11. Freshwater chronic cadmium toxicity data presented in order from the most sensitive to least sensitive species.
FRESHWATER CHRONIC CADMIUM TOXICITY TABLE
Species
Method
Chemical
Hardness
(mg/L as
CaC03)
Duration, effect
Chronic value
(ug/L)
Hard adj.
Chronic value
(ug/L)
Reference
Cladoceran,
Daphnia magna
LC
Cadmium
chloride
53
0.1523
0.1455
Chapman, et al.
manuscript
Cladoceran,
Moina macrocopa
LC
Cadmium
chloride
82
0.2828
0.1918
Hatakeyama &
Yasuno, 1981
Rainbow/donaldson trout,
Oncorhynchus mykiss
FT
Cadmium
46.5
100 day NOEC
1.25
1.3233
Davies, et al. 1993
Chinook salmon,
Oncorhynchus
tshawytscha
ELS
Cadmium
chloride
25
1.563
2.6936
Chapman, 1975
Brook trout,
Salvelinus fontinalis
ELS
Cadmium
chloride
37
1.732
2.194
Sauter, etal. 1976
Coho salmon,
Oncorhynchus kisutch
ELS
Cadmium
chloride
44
2.102
2.3239
Eaton, et al. 1978
Snail,
Aplexa hypnorum
LC
Cadmium
chloride
45.3
3.46
3.7389
Holcombe, et al.
1984
Ftagflsh,
Jordanella floridae
LC
Cadmium
chloride
47.5
4.416
4.5975
Carlson, et al. 1982
Atlantic salmon,
Salmo salar
ELS
Cadmium
chloride
23.5
4.528
8.1917
Rombough &
Garside, 1982
Cladoceran,
Ceriodaphnia reticulata
LC
Cadmium
chloride
67
4.948
3.9321
Spehar & Carlson,
1984
-------
Table 11. continued.
Species
Cladoceran,
Daphnia pulex
Method Chemical
R
Cadmium
sulfate
Hardness
(mg/L as
CaCOj)
106
Brown trout, ELS Cadmium 44
Salmo trutta chloride
White sucker, ELS Cadmium 44
Catostomus commersoni chloride
Lake trout, ELS Cadmium 44
Salvelinus namaycush Chloride
Northern pike, ELS Cadmium 44
Esox lucius chloride
Smallmouth bass, ELS Cadmium 44
Micropterus dolomieui chloride
Fathead minnow, ELS Cadmium 67
Pimephales promelas chloride
Amphipod, R Cadmium soft
Gammarus fossarum chloride
Duckweed, R Cadmium _
Lemna trisulca
Bluegiil, LC Cadmium
Lepomis macrochirus sulfate
201
Duration, effect Hard adj. Reference
Chronic value Chronic value
(ug/L) (ug/L)
70 day NOEC 2.7716 Goerke & Weber,
reproduction 1990
5
6.668 7.372 Eaton, et al. 1978
7.099 7.8485 Eaton, et al. 1978
7.357 8.1338 Eaton, et al. 1978
7.361 8.1382 Eaton, et al. 1978
7.39 8.1703 Eaton, et al. 1978
18.92 15.0355 Spehar & Carlson,
1984
14 day LC50 _ Abel & Baerlocher,
20 1988
14dayEC50 _ Huebert & Shay,
pop. growth 1991
26
49.8 16.3215 Eaton, 1974
-------
Table 11. continued.
Species
Large duckweed,
Spirodela poiyrhiza
Rotifer,
Bmchio/ius calyeiflarus
Zebra mussel,
Dreissena polymorpha
Method Chemical Hardness
(mg/L as
CaC03)
S Cadmium _
chloride
S Cadmium _
R Cadmium 150
chloride
Snake-head catfish,
Chatma striata
S
Cadmium
chloride
Duration, effect Hard adj. Reference
Chronic value Chronic value
(ug/L) (ug/L)
50 _ Charpentier, et al.
1987
60 _ Snell 8l Moffat, 1992
77 day LC50 54.8666 Kraak, etal. 1992
130
91.3 day LC50 _ Gopal & Devi, 1991
9497
-------
Table 12. Saltwater chronic cadmium toxicity data presented in order from the most to least sensitive species.
SALTWATER CHRONIC CADMIUM TOXICITY TABLE
Species
Method Chemical
V0
Mysid,
Mysidopsis bahia
Copepod,
Nitocra spinipes
Copepod,
Tigriopus brevicornis
Mysid,
Mysidopsis bigelowi
Amphipod,
Allorchestes compressa
Sea urchin,
Lytechinns pictus
Green sea urchin,
Stronglyocentrotus
droebachie
Polychaete,
Neanihes arenaceodentata
FT
FT
R
LC
FT
FT
Cadmium
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
Duration, effect
Chronic value
(ug/L)
28 day NOEC
mortality
4
13 day EC50
reproduction
6
240 hr EC50
reprodution
6.12
7.141
28 day LOEC
mortality
25
.5 hr EC50
reproduction
33
.5 hr£C50
reproduction
36
28 day LC50
39
Reference
Voyer &
McGovern,
1991
Bengtsson &
Bergstrom,
1987
Le Dean &
Devineau,
1985
Gentile, et
al. 1982
Ahsanullah
& Williams,
1991
Jonczyk, et
al. 1991
Jonczyk, et
aJ. 1991
Pesch, et al.
1986
-------
Table 12. continued.
Species Method Chemical Duration, effect
Chronic value
(ug/L)
Prawn, R Cadmium 45 day LC50
Palaemon serratus chloride 90
Sea urchin, S Cadmium
Echinmetra mathaei chloride
Barnacle, R Cadmium
Semibalanus balanoides chloride
Nematode, S Cadmium
Monhystera disjuncta chloride
Nematode, S Cadmium
Monhystera microphthalma chloride
Sand dollar, S Cadmium
Dendraster excentricus chloride
Red sea urchin, S Cadmium
Stronglyocentrotus chloride
jranciscan
Purple sea urchin, S Cadmium
Stronglyocentotus chloride
purpuratus
3 hr EC50
reproduction
100
15 day LC50
490
120 hrLOEC
reproduction
1000
240 hr LC50
1000
13 hr EC50
reproduction
8000
13 hr EC50
reproduction
12000
13 hr EC50
reproduction
18000
Reference
Le Dean &
Devineau,
1985
Ringwood,
1992
Powell &
White, 1989
Vranken, et
al. 1991
Vranken, et
al. 1985
Dinnel, et al.
1989
Dinnel, et al.
1989
Dinnel, et al.
1989
-------
Table 13. The percent probability of exceeding the copper acute freshwater or saltwater 10th
percentile for all species and the percent probability of exceeding the acute 10th
percentile for the most sensitive trophic group with n > 8.
Acute 10th Percentile
% Probability >
Location
0-ig/L)
10th percentile
()-
most sensitive trophic group
10th percentile
C and D Canal
8.3
(6.9 - benthos)
86 (90)
Middle River
6.3
(4.1 - benthos)
47 (74)
Choptank River
8.3
(6.9 - benthos)
29 (32)
Potomac River
8.3
(6.9 - benthos)
16 (20)
Upper mainstem Bay
8.3
(6.9 - benthos)
9.3 (13)
James River
8.3
(6.9 - benthos)
1.4 (2.8)
Baltimore Harbor
6.3
(4.1 - benthos)
1.2 (10)
Susquehanna River
8.3
(6.9 - benthos)
0.3 (0.7)
Lower mainstem Bay
6.3
(4.1 - benthos)
<0.1 (<0.1)
Nanticoke River
8.3
(6.9 - benthos)
<0.1 (0.2)
Patuxent River
6.3
(4.1 - benthos)
<0.1 (<0.1)
Middle mainstem Bay
6.3
(4.1 - benthos)
<0.1 (<0.1)
141
-------
Table 14. The percent probability of exceeding the cadmium acute freshwater or saltwater 10th
percentile for all species and the percent probability of exceeding the acute 10th
percentile for the most sensitive trophic group with n > 8.
Acute 10th Percentile (^g/L)
Location () - most sensitive trophic group 10th % Probability >
Pontile 10th percentile
C and D Canal
5.1 (0.9-fish)
7.5 (88)
Upper mainstem Bay
5.1 (0.9-fish)
3.4 (29)
Chester River
5.1 (0.9-fish)
3.3 (11)
Potomac River
5.1 (0.9-fish)
2.8 (33)
Choptank River
5.1 (0.9-fish)
1.5(17)
West Chesapeake
5.1 (0.9-fish)
1.4(20)
Nanticoke River
5.1 (0.9-fish)
0.5 (11)
Susquehanna River
5.1 (0.9-fish)
<0.1 (6.2)
Patuxent River
5.1 (0.9-fish)
0.5 (5)
Lower mainstem Bay
31.7 (23.3 - benthos)
<0.1 (<0.1)
Middle mainsteam Bay
31.7 (23.2 - benthos)
<0.1 (<0.1)
142
-------
FIGURES
143
-------
Figure 1. Ecological risk assessment approach.
144
-------
Figure 2. Location of the 102 stations where copper and cadmium
were measured from 1985 to 1996. See key to map where
stations are described.
145
-------
Kev to map for Figure 2 Stations where copper and cadmium were sampled from 1985 to 1996.
Latitude and longitude coordinates are given in decimal degrees. Station number corresponds to station
location on Figure 2. Abbreviated station names are in parentheses.
ber
Station
Latitude
Longitude
1
Susquehanna River Fall Line (1578310)
39.6586
76.1744
2
James River Fall Line (2035000)
37.6708
78.0861
3
Elizabeth River
36.8081
76.2933
4
Freestone Point
38.5833
77.2667
5
Indian Head
38.6000
77.2167
6
Morgantown
38.3337
77.0157
7
Patapsco River
39.2167
76.5000
8
Possum Point
38.5362
77.2920
9
Wye River (Manor House)
38.9028
76.1298
10
Bell Branch (BEB)
38.9917
76.6333
11
Bacon Ridge Branch (BRB)
38.9992
76.6136
12
Burnt Mill Creek (BTM)
38.3322
76.6369
13
Bear Creek
39.2358
76.4961
14
Curtis Bay
39.2064
76.5803
15
Middle Branch
39.2528
76.5883
16
North West Harbor
39.2767
76.5742
17
Outer Harbor
39.2089
76.5247
18
Sparrows Point
39.2081
76.5075
19
Cabin Branch (CAB)
38.7694
76.6528
20
CB1
36.9950
75.9467
21
CB10
38.2467
76.2617
22
CB11
38.3717
76.3233
23
CB12
38.5633
76.4317
24
CB13
38.7517
76.4350
25
CB14
38.9183
763883
26
CB15
38.0717
763233
27
CB16
39.1883
762883
28
CB17
39.2567
76.2400
29
CB18
39.3683
76.1433
30
CB19
39.5500
76.0800
31
CB2
37.0833
76.0950
32
CB20
39.4300
76.0333
33
CB3
37.1883
76.1633
34
CB5
37.3650
76.0750
35
CB6
37.5267
76.0433
36
CB7
37.6200
76.1200
37
CB8
37.8217
76.1750
38
CB9
38.1000
76.2200
39
Marti nak
38.8750
75.8417
40
Chaptico Creek (CHP)
38.3817
76.7822
41
Coffee Hill (COF)
38.3614
76.7578
42
CR1D
38.5700
76.3833
43
Davis Millpond (DMP)
38.6708
75.7639
44
DYN (DYN)
38.3164
76.7344
45
Dahlgren
38.3012
77.0660
46
Faulkners Branch - Bradley Rd. (FBB)
38.6989
75.7853
146
-------
Station number Station
Latitude Longitude
47
Faulkners Branch - [setter Rd (FBI)
38.7214
75.8261
48
Forest Hall (FOR)
38.3989
76.7492
49
Kings Creek (KGC)
38.7897
76.0094
50
LPXT0173
39.1333
76.8183
51
Lyons Creek (LYC)
38.7689
76.6239
52
Mill Creek (MLC)
39 2825
76.1436
53
Mattawoman Creek (MTW)
38.6161
77.0486
54
Gibson Island
39 0600
76.4350
55
South Feny
39.0767
76.5014
56
Frog Mortal
39.3083
76 4028
57
Wilson Point
39.3083
76.4125
58
North Davis Branch (NDB)
38.6783
75.7478
59
North River (NRV)
38.9878
76.6233
60
Bivalve
38.3214
75.8894
61
Sandy Hill Beach
38 3567
75.8558
62
Cherry Hill
38.5667
77.2583
63
Maryland
38.5167
77.2583
64
Mid
38.5222
77.2667
65
Virginia
38.4917
77.3083
66
Quantico
38.5278
77.2750
67
Widewatei
38.4333
77.3250
68
PTXCF8747
38.3133
76.4222
69
PTXCF9575
38.3265
76.3713
70
PTXDE2792
38.3800
76.5150
71
PTXDE5339
38.4243
76.6008
72
PTXDE9401
38.4940
76.6645
73
PTXDF0407
38.3413
76.4858
74
PTXED4892
38.5828
76,6783
75
PTXED9490
38.6582
76.6845
76
PXT0402
3 %1\\%
76.6858
77
PXT0494
38.8062
76.7075
78
PXT0603
38.9500
76.6950
79
PXT0809
39 1083
76.8617
80
PXT0972
39.2350
77.0583
81
Sewell Branch (SEW)
38.6083
76.5867
82
Betterton
39.3742
76.0503
83
Turners Creek
39.3631
75 9842
84
Junction Rt. 50
39.0056
76.5067
85
Annapolis
38.9669
76.4717
86
Tull Branch (TLB)
38.7194
75.7719
87
Twiford Meadow (TWM)
38.7236
75.7625
88
Trib. to Marshyhope Creek (UMH)
38.7631
75.7431
89
Grove
39.4000
76.0500
90
Howell
39.3583
76.0833
91
Spesutie
39.3917
76.1250
92
Delaware City
39.5417
75.7250
93
Chesapeake City
39.5167
75.8000
94
Courthouse Point
39.5000
75.8750
95
Elkton
39.5667
75.8500
96
Kentmore
39.3750
76 9583
147
-------
Station number Station Latitude Longitude
97 Havre de Grace 39.5417 76.0667
98 Trib. to Red Lion Branch (URL) 39.1767 75.8992
99 Trib. to Southeast Creek (USE) 39.1308 75.9794
100 Trib. to Tuckahoe Creek (UTK) 38.8831 75.9269
101 WBPXT0045 38.8085 76.7507
102 Quarter Creek 38.9167 76.1667
148
-------
Figure 3. Quarterly copper measurements from the Patuxent River (May 1995 to February 1996).
Patuxent River
NOAA/COASTES Copper Sampling
PTXCF9575
• O - PTXCF8747
—T— PTXDF0407
—PTXDE2792
~m~ PTXDE5339
~€1 • PTXDE9401
—* - PTXED4892
-O- PTXED9490
• A - PXT0402
PXT0494
-*•- PXT0603
-O- PXT0809
-• PXT0972
-O - WBPXT0045
LPXT0173
25MAY95 23AUG95 27NOV95 22FEB96
Quarterly Samples
-------
Figure 4. Quarterly cadmium measurements from the Patuxent River (May 1995 to February 1996).
Patuxent River
NOAA/COASTES Cadmium Sampling
-~ PTXCF9575
O PTXCF8747
- PTXDF0407
-V PTXDE2792
PTXDE5339
-D PTXDE9401
PTXED4892
-C^- PTXED9490
A PXT0402
—£*— PXT0494
-• PXT0603
-O- PXT0809
PXT0972
-O WBPXT0045
-r- LPXT0173
25MAY95 23AUG95 27NOV95 22FEB96
Quarterly Samples
-------
Figure 5. Copper measurements from the James River (1990 to 1993).
Copper Values in James R.
9
8
7
6
S
iliii§iSiiii?iif§ssisss3isi§ssssssss
s5ssis§slll|sss"ss»sssss|ss5ssss|ass
Dates
-------
Figure 6. Copper measurements from the Susquehanna River (1990 to 1993).
Copper Values in Susquehanna R.
Dates
-------
7
6
5
§
3 4
a
e
*
£
a
V 3
O J
a
©
(J
2
1
0
7. Cadmium concentrations measured every 24 h at three stations during two
lents in the C and D Canal in April of 1985.
O" Courthouse Pt. Exp. 1
Q • Courthouie Pt Exp. 2
-0 - Chesapeake City Exp. 1
-0- - Cbeaapeake CUy Exp. 2
A Delaware City Eip. ]
A Delaware City Eip. 2
Cadmium - CAD Canal 1985
A
v-
&
Eip1
—0
ja~-
y
s' A
A
/
"e-X- £
or
-e-
/
Ex
f 1 1 '
24 48 72 96
TIME (hours)
-------
Figure 8. Copper concentrations measured every 24 h at three stations during two 96 h
experiments in the C and D Canal in April of 1985.
80
£
3
70 -
60 -
50
e
o
- 40
u<
* £
e
-------
Figure 9. Cadmium concentrations measured daily for 9 days at Chesapeake City in the C and D
Canal during April and May of 1987.
Cadmium - C&D Canal 1987
(Chesapeake City)
—I—
4/28
Date
t
5/1
4/24 4/25
4/26
4/27
4/29
4/30
5/2
-------
Figure 10. Copper concentrations measured daily for 9 days at Chesapeake City in the C and D
Canal during April and May of 1987.
10
VI
Ov
9 -
i
a
o
•G
«0
b
a
4>
a
o
U
8
7 -
6 -
5 -
Copper - CAD Canal 1987
(Chesapeake City)
T
4/24
4/25
4/26 4/27
4/28
Date
4/29 4/30
T
5/1
5/2
-------
Figure 11. Cadmium concentrations from successive 24 h samples during three 96 h experiments
at three stations in the Potomac River in April of 1986.
-O- Cherry Hill
—~ - Quaatfco
-A- Widewater
/
/
/
Exp. I
ft
\
\
4/9 4/10 4/11 4/12
Cadmium - Potomac River -1986
Exp. 3
i 1 1 1 1 1 r
4/14 4/15 4/16 4/17 4/18 4/19 4/20 4/21
O Q Q-
r T i
*
4/22 4/23 4/24 4/25 4/26 4/27
Date
-------
Fi
th
80
70
60
50
40
30
20
10
0
e 12. Copper concentrations from successive 24 h samples during three 96 h
stations in the Potomac River in April of 1986.
-O- Cherry HB1
—O - Quantko
-A- Widewater
Exp. I
Z&—0 O—Q
Copper - Potomac River -1986
Exp. 3
1 1 1 1 1 1
4/22 4/23 4/24 4/25 4/26 4/2
i 1 1 r~
4/9 4/10 4/11 4/12
1iiiiiiI
4/14 4/15 4/16 4/17 4/18 4/19 4/20 4/21
Date
-------
Fi
in
14
13
12
11
10
9
8
7
6
5
4
3
2
1
0
13. Cadmium concentrations from a 27 day period at three stations in the Potomac
il and May of 1988.
-O- Virginia
-O - Middle
—£t— Maryland
Cadmium - Potomac River -1988
J*--
vr
—r~
4/8
4/10
4/14
4/18
I
4/21
Date
4/25
4/27
5/3
5/5
-------
Figure 14. Copper concentrations from a 27 day period at three stations in the Potomac River
April and May of 1988.
12
11
10
9
8 -
^ 7-1
a
©
S 6
b
a
8 5 H
a
©
3
2
1
0
—O- VIrffnta
-~ - Middle
Maryland
T
4/8
4/10
Copper - Potomac River - 1988
4/14
4/18
4/21
Date
4/25
4/27
5/3
5/5
-------
Figure 15. Cadmium concentrations from a 29 day period at three stations in the Potomac River
in April and May of 1989.
4 -
3 -
» e
- TS
«
b
a
o>
w 2
—O- VlrftnLi
—~ - Middle
-A- Marylaad
Cadmium - Potomac River - 1989
a
o
U
1 -
-o-
-O-
-Q-
-O-
-O-
-O-
-o-
-Q-
-O-
-a
4/9
T
4/11 4/13 4/18 4/20
4/22
Date
T
4/24 4/30
5/4
5/6
5/8 5/10
-------
Figure 16. Copper concentrations from a 29 day period at three stations in the Potomac River
April and May of 1989.
Date
-------
Figure 17. Cadmium concentrations during a 22 day period at three station in the Potomac River
in April and May of 1990.
4/12 4/14 4/18 4/20 4/22 4/25 4/27 4/30 5/2 5/4 5/6
Date
-------
Figure 18. Copper concentrations during a 22 day period at three stations in the Potomac River
in April and May of 1990.
50
—O— VlrgJnU
-O - Middle
—A— Maryland
Copper - Potomac River - 1990
40 -
1
30 -
»- a
ON o
** -C
as
b
a
o
a
o
U
20 -
10 -
0
4/12 4/14 4/18 4/20 4/22 4/25 4/27 4/30
5/2
5/4
5/6
Date
-------
Figure 19. Acute geometric means for copper toxicity data by trophic
group for freshwater and saltwater species.
Freshwater
Saltwater
1000 -
macTophytes (a = 2)
- 1000
100 -
-benthos (n = 31)
• fish (n « 36)
-amphibians (n = 2)
benthos (n = 30)
fish (n = 15)
zooplankton (n = 7) ¦
- 100
zooplankton (n = 4) ;Ptytoplsnkton (n = 3>-
10 -L
10
165
-------
Figure 20. Acute copper toxicity data for families of freshwater fish.
Freshwater Acute Copper data for Fish
10000
o»
<*>
/—
§
a
.2
c3
€
0>
o
C
o
O
9
~J
1000 —
100
10 --
CypiimdMe - Cp 11»12, Stlmooidte -St a "9, MoroaidiC - Mo a » 2, fctaiiiridje - Ic n»2, Centr«rcliid*e - Cc a = 2, Percidic - Pc a « 2,
Bigridie - B« n » 1, Poeciiiidae - Po n » 1, Cttostomidae - Ci n « I, Cyprinodontidte - Cy o « 1. Anguillidje - Ag n « l
-------
Figure 21. Acute copper toxicity data for various groups of freshwater benthic species.
Freshwater Acute Copper data for Benthos
i
a
.2
5 h
8
8
o
O
hJ
10,000 -r
1,000
100 -r
10 -r
Am
Amphipodi - Am n - 9, Gastropods - Ga n - 4, Bivalves - Bi n - 4, Insects - In n - 3, Midges - Mi n «3,
BryzMat - Br n - 3, Crayfish - Cr n - 2, Annelids -An n - 2.
-------
Figure 22. Acute copper toxicity data for various families of saltwater fish species.
Saltwater Acute Copper data for Fish
10000
i
c
i
I
o
g
O
9
i-l
1000
100 --
Pleurooectidie - PI n - 3, Cypiinodootidje - Cy n » 3, Atherinidae - At n * 3, Moronidae - Mo n = I, Poociiiidae - Po n
CtnngjdMe - Ca o »1, Ciupeidae - CI b~1, Eograulidae - En n » 1, Scyliorhinidie - Sc a - 1.
-------
Figure 23. Acute geometric means for cadmium toxicity data by
trophic group for freshwater and saltwater species.
Freshwater
Saltwater
(n = 17) fish-
amphibians (n = 1)
1000 -
i
benthos (n = 35)
(n = 1) macrophytes
(n = 58) benthos.
(n = 7) zooplankton
- 1000
c
.2
"S
w
C
i
100 -
fish (n = 24)
zooplankton (n - 4) • (» = 5) pbytoplankton
- 100
-phytoplankton (n * 1)
10
10
169
-------
Figure 24. Freshwater acute cadmium toxicity data for various groups of benthic species.
Freshwater Acute Cadmium data for Benthos
10000 — r
1000 -r
100 -r
Annelids - An n = 11, Insects - In n = 4, Amphipods - Am n =4, Midges - Mi n.= 3, fiiyzoans - Br n = 3,
Gastropods -Gi n ¦ 3,Crayfish - Cr n * 3, fsopods n = 3, Bivalves - Bi n = I
-------
Figure 25.
100,000 -jr
Saltwater acute cadmium toxicity data for various families of fish species.
Saltwater Acute Cadmium data for Fish
a
10,000 - -
9
a
o
-I
1,000 -r
§
U
00
o
H-l
100 --
10
r~
Mo
~T
Pl
At
Mu
r
Cy
Sa
r
Sp
~~r
Em
r
u
Ky
Go
Moronidae • Mo n ¦ 1, Pleurooectidae • PI n - 2, Atherinidae - At n
Cyprinodootidae - Cy a *4, Salmonidae- Sa n - 1, Sparidae - Sp n
Labridae - La n - 1, Kyphosidae - Ky n - 1, Gobiidae - Go a ¦ I.
•1, Mugilidae - Mu n - 1,
3, Exabiotiocidac * Em n
1.
-------
Figure 26. Saltwater acute cadmium toxicity data for various zooplankton species.
Saltwater Acute Cadmium data for Zooplankton
100,000
ro
a
a
0
1
10,000
§ 1000
§
u
I
Copepods - Co n = 5, Cladocerans - CI n = 1, Rotifers - Ro n = 1.
-------
APPENDIX A
Copper risk characterization by basin
-------
C & D Canal Exposures
Copper Concentration (pg/L)
A-l
-------
Middle River Basin Exposures
Copper Concentration (pg/L)
A-2
-------
Choptank Basin Exposures
Copper Concentration (pg/L)
A-3
-------
Potomac Basin Exposures
Copper Concentration (pg/L)
A-4
-------
Upper Bay Mainstem
Copper Concentration (jjg/L)
A-5
-------
99 -
90 -
4)
8 70
0)
a
£ 30
0£
50 -
10 -
James Basin Exposures
Probability of
exceedence ¦ 2.8%
Probability of
exceedence ¦ 1.4%
10
Copper Concentration (mq/L)
A- 6
-------
Baltimore Harbor Exposures
Copper Concentration (pg/L)
-------
Susquehanna Station Exposures
Copper Concentration (pg/L)
A-8
-------
Lower Chesapeake Bay Exposures
Copper Concentration (pg/L)
A-9
-------
Nanticoke River Basin Exposures
Copper Concentration (pg/L)
A-10
-------
Patuxent River Basin Exposures
Copper Concentration (mq/L)
A-ll
-------
Middle Chesapeake Bay Mainstem Exposures
Copper Concentration (pg/L)
A-12
-------
APPENDIX B
Cadmium risk characterization by basin
-------
C&D Canal Exposures
B-l
-------
Potomac Basin Exposures
Cadmium Concentration ((jg/L)
B-2
-------
Upper Chesapeake Mainstem Exposures
Cadmium Concentration (pg/L)
B-3
-------
West Chesapeake Basin Exposures
Cadmium Concentration (pg/L)
B-4
-------
Choptank River Basin Exposures
Cadmium Concentration (pg/L)
B-5
-------
Chester River Basin Exposures
Cadmium Concentration (pg/L)
B-6
-------
Nanticoke River Basin Exposures
Cadmium Concentration (pg/L)
B-7
-------
Susquehanna Fall Line Exposures
Cadmium Concentration (M9/L)
B-8
-------
Patuxent River Basin Exposures
Cadmium Concentration (pg/L)
-------
Lower Chesapeake Mainstem Exposures
Cadmium Concentration (pg/L)
B-10
-------
99 -
Middle Chesapeake Mainstem Exposures
90 -
O
E
O
O)
0)
Q.
(0
0)
o
£.
<0
CO
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