SrEPA
United States
Environmental Protection
Agency
Office of Water
Regulations and Standards
Criteria and Standards Division
Washington, DC 20460
EPA 440/5-84-031
January 1985
Water
Ambient
Water Quality
Criteria
for
Copper -1984
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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
COPPER
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
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DISCLAIMER
This report has been reviewed by che Criteria and Standards Division,
Office of Water Regulations and Standards, U.S. Environmental Protection
Agency, and approved for publication. Mention of trade names or commercial
products does not constitute endorsement or recommendation for use.
AVAILABILITY NOTICE
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Pore Royal Road, Springfield, VA 22161.
io»o V-VjuvNba* - "P&QS- 227 O23
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FOREWORD
Section 304(a)(l) of the Clean Water Act of 1977 (P.L. 95-217) requires
the Administrator of the Environmental Protection Agency to publish criteria
for water quality accurately reflecting the latest scientific knowledge on
the kind and extent of all identifiable effects on health and welfare which
may be expected from the presence of pollutants in any body of water,
including ground water. This document is 3 revision of proposed criteria
based upon a consideration of comments received from other Federal agencies,
State agencies, special interest groups, and individual scientists. The
criteria contained in this document replace any previously published EPA
aquatic life criteria.
The term "water quality criteria" is used in two sections of the Clean
Water Act, section 304(a)(l) and section 303(c)(2). The term has a different
program impact in each section. In section 304, the term represents a
non-regulatory, scientific assessment of ecological effects. The criteria
presented in this publication are such scientific assessments. Such water
quality criteria associated wich specific stream uses when adopted as State
water quality standards under section 303 become enforceable maximum
acceptable levels of a pollutanc in ambient waters. The water quality
criteria adopted in the State water quality standards could have the same
numerical limits as the criteria developed under section 304. However, in
many situations States may want to adjust water quality criteria developed
under section 304 co reflect local environmental conditions and human
exposure patterns before incorporation into water quality standards. It is
not until their adoption as part of che State water quality standards that
the criteria become regulatory.
Guidelines to assist the Scaces in the modification of criteria
presented in this document, in the development of water quality standards,
and in other water-related programs of this Agency, have been developed by
EPA.
Edwin L. Johnson
Director
Office of Water Regulations and Scandards
111
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ACKNOWLEDGMENTS
Robert W. Andrew
(freshwater author)
Environmental Research Laboratory
Duluth, Minnesota
John H. Gentile
(saltwater author)
Environmental Research Laboratory
Narragansett, Rhode Island
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluch, Minnesota
David J. Hansen
(saltwater coordinator)
Environmental Research Laboratory
Narragansett, Rhode Island
Statistical Support: John U. Rogers
Clerical Support: Terry L. Highland
IV
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CONTENTS
Page
Foreword iii
Acknowledgments iv
Tables vi
Introduction 1
Acuce Toxicicy co Aquaeic Animals 6
Chronic Toxicicy co Aquacic Animals 11
Toxicicy to Aquatic Planes 16
Bioaccumulacion 17
Ocher Data 18
Unused Data 20
Summary 22
National Criteria 23
References 85
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TABLES
Page
1. Acute Toxicicy of Copper to Aquatic Animals 26
2. Chronic Toxicity of Copper to Aquatic Animals 48
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios 51
4. Toxicity of Copper to Aquatic Plants » 58
5. Bioaccumulacion of Copper by Aquatic Organisms 62
6. Other Data on Effects of Copper on Aquatic Organisms 65
VI
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Inproduction*
Copper, which occurs in nacural wacers primarily as che divalent cupric
ion in free and complexed forms (Callahan, ec al. 1979), is a minor nucrienc
for boch planes and animals ac low concencracions but is coxic co aquaeic
life ac concencracions only slighcly higher. Concencracions of 1 co 10 ug/1
are usually reporced for unpolluced surface wacers in che Uniced Scaces
(Boyle, 1979), buc concencracions in che vicinity of municipal and induscrial
effluencs, parcicularly from sraelcing, refining, or raecal placing induscries,
may be much higher (Harrison and Bishop, 1984; Hucchinson, 1979).
A cwo-volume review of various aspeccs of "Copper in che Environment*
(Nriagu, 1979) contains several chapcers on che effeccs of copper on boch
freshwater and saltwater species. Reviews by Black, ec al,. (1976), Deraayo,
ec al. (1982), and Spear and Pierce (1979a) summarize most of the available
data an che aquacic toxicology of copper chrough 1982. These reviews form
che scientific basis for Canadian environmental quality criteria for copper.
Harrison and Bishop (1984) reviewed che pocencial impacc of copper in power
plant cooling wacers on freshwater environments. Rai, ec al. (1981) and
Sprague (1985) reviewed effeccs of wacer qualicy parameters on copper
toxicicy.
The toxicicy of copper co aquacic life has been shown co be relaced
primarily co activity of che cupric (Cu ) ion, and possibly co some of
*An understanding of che "Guidelines for Deriving Numerical National Wacer
Qualicy Criceria for che Proceccion of Aquacic Organisms and Their Uses"
(Scephan, ec al. 1985), hereafcer referred co as che Guidelines, is necessary
in order co understand che following text, tables, and calculations.
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che hydroxy complexes (Andrew, ec al. 1977; Chakoumakos, ec al. 1979; Dodge
and Theis, 1979; Howarth and Sprague, 1978; Pagenkopf, 1983; Pecersen, 1982;
Ruecer, 1983). The cupric ion is highly reaccive and forms moderate co scrong
complexes and precipicaces wich many inorganic and organic constituents of
natural waters, e.g., carbonate, phosphate, ami no acids, and hutnac.es, and is
readily sorbed onco surfaces of suspended solids. The proportion of copper
present as the free cupric ion is generally low and may be less than 1 percent
in eucrophic waters where complexation predominates. Most organic and inor-
ganic copper complexes and precipitates appear to be much less toxic than free
cupric ion and tend to reduce toxicity attributable co total copper (Andrew,
1976; Borgmann and Ralph, 1983). This greatly complicates the interpretation
and application of available toxicity data, because the proportion of free
cupric ion present is highly variable and is difficult co measure except under
laboratory conditions. Except for bacteria and plankton, few toxicicy data
have been reported using measurements other than coral or dissolved copper.
Because a majority of the reported test results (Tables 1 and 2) have
been conducted in waters having relatively low complexing capacities, the
criteria derived herein may be at or below ambient cocal copper concencracions
in some surface wacers of che United States. Seasonally and locally, toxicicy
in chese wacers may be mitigated by che presence of naturally occurring
complexing and precipitating agents. In addition, removal from the water
column may be rapid due to settling of solids and normal growth of aquatic
organisms. The various forms of copper are in dynamic equilibrium and any
change in chemical conditions, e.g., pH, can rapidly alter the proportion of
che various forms presenc and, therefore, toxicity.
In most natural wacers, alkalinicy and pH increase wich wacer hardness
and che relative influence of these parameters on coxicicy is noc easily
2
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determined. Because increasing calcium hardness and associated carbonate
alkalinity are both known to reduce the acute toxicity of copper, expression
of the criteria as a function of hardness allows adjustment for these water
quality effects. This results in a much better fit with the available
toxicity data, i.e., the criteria are higher at high hardness to reflect
calcium antagonism and carbonate complexation. A similar approach, i.e.,
expressing acute toxicity as an exponential function of hardness, was used by
Spear and Pierce (1979a) as a basis for the Canadian criteria. Some data on
the relationship of toxicity to other factors, i.e., temperature, pH,
alkalinity, size of organism, and total organic carbon, are available for a
limited number of species and will be discussed later.
Because of the variety of forms of copper (Callahan, et al. 1979) and
lack of definitive information about their relative toxicities, no available
analytical measurement is known to be ideal for expressing aquatic life
criteria for copper. Previous aquatic life criteria for copper (U.S. EPA,
1980) were expressed in terms of total recoverable copper (U.S. EPA, 1983a),
but this measurement is probably too rigorous in some situations.
Acid-soluble copper (operationally defined as the copper that passes through
a 0.45 ,jra membrane filter after the sample is acidified to pH a 1.5 to 2.0
with nitric acid) is probably the best measurement at the present for the
following reasons:
1. This measurement is compatible with nearly all available data concerning
toxicity of copper to, and bioaccuraulation of copper by, aquatic
organisms. Very few test results were rejected just because it was
likely that they would have been substantially different if they had been
reported in terms of acid-soluble copper. For example, results reported
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in cerras of dissolved copper were noc used if che concencracion of
precipitated copper was subscancial.
2. On samples of ambient water, measurement of acid-soluble copper should
measure all forms of copper that are coxic co aquatic life or can be
readily converted co coxic forms under natural conditions. In addicion,
chis measurement should noc measure several forms, such as copper chat is
occluded in minerals, clays, and sand or is scrongly sorbed co parcicu-
late raaccer, that are noc toxic and are not likely to become coxic under
natural conditions. Alchough this measurement (and many others) will
measure soluble, complexed forms of copper, such as the EDTA complex of
copper, chat probably have low coxicities to aquatic life, concentrations
of these forms probably are negligible in most ambient water.
3. Alchough wacer qualicy criteria apply co ambient water, the measurement
used co express criteria is likely co be used co measure copper in
aqueous effluents. Measurement of acid-soluble copper should be
applicable co effluents because it will measure precipitates, such as
carbonate and hydroxide precipitates of copper, chat might exisc in an
effluent and dissolve when che effluenc is diluted with receiving wacer.
If desired, dilution of effluent with receiving water before raeasuremenc
of acid-soluble copper might be used to determine whether che receiving
wacer can decrease che concencracion of acid-soluble copper because of
sorpcion.
4. The acid-soluble measurement should be useful for most metals, chus
minimizing che number of samples and procedures chat are necessary.
5. The acid-soluble measurement does noc require filcracion at the time of
collection, as does the dissolved measurement.
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6. The only treatment required at the cLme of collection is preservation by
acidification to pH » 1.5 to 2.0, similar co that required for the cocal
recoverable measurement.
7. Durations of 10 minutes to 24 hours between acidification and filcration
probably will not affect the result substantially.
8. The carbonate system has a much higher buffer capacity from pH • 1.5 to
2.0 than it does from pH » 4 co 9 (Weber and Stumm, 1963).
9. Differences in pH within the range of 1.5 to 2.0 probably will not affecc
the result substantially.
10. The acid-soluble measurement does not require a digestion seep, as does
the total recoverable measurement.
11. After acidification and filtration of the sample to isolate the
acid-soluble copper, the analysis can be performed using either atomic
absorption spectroscopy or ICP-eraission spectroscopy (U.S. EPA, 1983a),
as wich the total recoverable measurement.
Thus, expressing aquatic life criteria for copper in terms of the acid-
soluble measurement has both toxicological and practical advantages. On che
other hand, because no measurement is known to be ideal for expressing
aquatic life criteria for copper or for measuring copper in ambient water or
aqueous effluents, measurement of both acid-soluble copper and total
recoverable copper in ambient water or effluent or both might be useful. For
example, there might be cause for concern if cotal recoverable copper is much
above an applicable limit, even chough acid-soluble copper is below che
1 imi t.
Unless otherwise noted, all concentrations reported herein are expecced
to be essentially equivalent to acid-soluble copper concentrations. All
concentrations are expressed as copper, not as the chemical tested. The
5
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criteria presented herein supersede previous aquacic life wacer quality
criteria for copper (U.S. EPA, 1976, 1980) because these new criteria were
derived using improved procedures and additional information. Whenever
adequately justified, a national criterion may be replaced by a site-specific
criterion (U.S. EPA, 1983b), which may include not only site-specific
criterion concentrations (U.S. EPA, 1983c), but also site-specific durations
of averaging periods and site-specific frequencies of allowed exceedences
(U.S. EPA, 1985). The latest literature search for information for chis
document was conducted in May, 1984; some newer information was also used.
Acute Toxicicy to Aquatic Animals
Most of the available tests on the toxicity of copper to freshwater
animals have been conducted with four salmonid species, fathead and bluntnose
minnows, and the bluegill. Acute values range from 6.5 Mg/L for Daphnia
magna in hard water to 10,200 gg/L for the bluegill in hard water. The
majority of tests conducted since about 1970 have been flow-through tests
with measurements of both total and dissolved copper. Many recent tests have
included measurement or calculation of cupric ion activity (Andrew, 1977;
McKnight and Morel, 1979; Petersen, 1982; Rueter, 1983; Sunda and Gillespie,
1979; Zevenhuizen, et al. 1979). All the values in Table 1 are for tocal
copper, except that the values obtained by Howarth and Sprague (1978) were
dissolved copper. These are included in Table 1 because Chakouraakos, et al.
(1979) showed that at low hardness in this water almost all the copper is
dissolved. Values obtained by Howarth and Sprague (1978) in hard water are
in Table 6.
Acute tests by Cairns, et al. (1978) indicate that daphnids are more
resistant to copper at low than at high temperatures (Table 6). Because such
6
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daca are noc available for ocher species or for longer tests, no
generalizations can be made for criceria derivacion. Chakoumakos, ec al.
(1979) and Howarth and Sprague (1978) (Tables 1 and 6) have reporced that
larger (10 to 30 g) rainbow crouc are approximately 2.5 co 3.0 times more
resistant co copper than juveniles. Tsai and Chang (1981, 1984) showed a
similar size effect for che guppy and the bluegill. This factor is obviously
a source of variation in Table 1. However, insufficient data are available
for other species to allow adjustment of test results or on which to base
criteria. An additional complicating factor is the general lack of knowledge
of the range of sensitivity of various life stages of most invertebrate
species, or the effects on susceptibility of starvation and other stresses
under natural conditions.
Lind, et al. (Manuscript) and Brown, et al. (1974) demonstrated
quantitative relationships between the acute toxicicy of copper and naturall-y
occurring organic coraplexing agents (Tables 1 and 6). Although these
relationships have been shown for only a few species (Daphnia pulicaria,
fathead minnow, and rainbow trout), the effects should be generalizable
through chemical effects on cupric ion activity and bioavailability. Lind,
et al. (Manuscript) measured the toxicicy of copper co Daphnia pulicaria in a
variety of surface waters and found that total organic carbon (TOC) is a more
important variable than hardness, with acute values varying approximately
30-fold over the range of TOC covered. Similar results were obtained wich
the fathead minnow. This indicates that criteria should be adjusted upward
for surface waters with TOC significantly above the 2 to 3 rag/L usually found
in waters used for toxicity tests. Results obtained by Lind, et al.
(Manuscript) in waters with low TOC are in Table 1; values obtained in water
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wich high TOC are in Table 6. Rehwoldt, et al. (1971, 1972, 1973) obtained
subscantially higher acute values than other investigacors did with an
amphipod, the common carp, striped bass, and pumpkinseed. This may have been
an effect of water quality on toxicicy.
To account for the apparent relationship of copper toxicity to hardness,
an analysis of covariance (Dixon and Brown, 1979; Neter and Wasserman, 1974)
was performed using the natural logarithm of the acute value as the dependent
variable, species as the treatment or grouping variable, and the natural
logarithm of hardness as the covariate or independent variable. This
analysis of covariance model was fit to the data in Table 1 for the eight
species for which acute values are available over a range of hardness such
chat the highest hardness is at least three times the lowest and the highest
is also at least 100 rag/L higher than the lowest. Seven of the slopes ranged
from 0.6092 to 1.3639 (Table 1). The slope for Daphnia magna was 0.4666 with
wide confidence limits if all the data for this species were used, but the
slope was 1.0438 with narrower confidence limits if the value from Dave
(1984) was not used. Therefore, this value was not used. An F-test showed
that, under the assumption of equality of slopes, the probability of
obtaining eight slopes as dissimilar as these is P»0.11. This was
interpreted as indicating that it is not unreasonable to assume that the
slopes for all eight species are the same. The pooled slope of 0.9422 is
close to the slope of 1.0 that is expected on the basis that copper, calcium,
magnesium, and carbonate all have a charge of two.
The pooled slope of 0.9422 was fitted through the geometric mean
toxicity value and hardness for each species to obtain Species Mean Acute
Values at a hardness of 50 mg/L (Table 1), which were used to calculate Genus
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Mean Acute Values (Table 3). Of the 41 genera for which acuce values are
available, che most sensitive, Pcychocheilus, is 610 times more sensitive
than the moat resistant, Acroneuria. The seven most sensitive genera are
within a factor of 3 and both fishes and invertebrates are among the most
sensitive and most resistant genera. Acute values are available for more
than one species in each of nine genera, and the range of Species Mean Acute
Values within each genus is less than a factor of 6.6. A freshwater Final
Acute Value of 18.46 jg/L (at a hardness of 50 rag/L) was obtained for copper
using the Genus Mean Acute Values in Table 3 and the calculation procedure
described in the Guidelines. Thus, the freshwater Criterion Maximum
Concentration (in gg/L) - e<0.9422[In(hardness)]-l.464)^
Embryos of the blue mussel and Pacific oyster are the most sensitive
saltwater animal species tested with acute values of 5.8 and 7.8 ,Jg/L,
respectively (Table 1). Differences in life-stage sensitivity with the
Pacific oyster are clearly evident because the adults of this species studied
in a flow-through test had an LC50 of 560 ;Jg/L, which is about two orders of
magnitude greater than the values for the embryos. This suggests that
embryos may be the most sensitive life stage of these two species. Eisler
(1977) demonstrated that copper toxicity to Mya arenaria varied according co
the seasonal temperature, being at least 100 times more toxic at 22 C than at
4 C. The calanoid copepods, Acartia tonsa and Acart ia clausi, were the most
sensitive crustacean species tested with LC50s in the range of 17 to 55 ;Jg/L.
Sosnowski, et al. (1979) showed that the sensitivity of field populations of
A_. tonsa to copper was strongly correlated with population density and food
ration (Table 6), whereas cultured ^. consa manifested a reproducible
toxicological response to copper (Table 1) through six generations (Sosnowski
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and Gentile, 1978). Life-stage sensitivity differences also occurred wich
crustaceans as evidenced by the acute values of 100 ug/L for lobscer aduLcs
(McLeese, 1974) and 48 ug/L for larvae (Johnson and Gentile, 1979). The
range of crustacean sensitivity to copper is further highlighted by larvae of
the green crab, Carcinus maenus, whose LC50 of 600 ug/L is the highest of all
reported saltwater acute values. Adult Neanthes arenaceodentata had a range
of acute values from 77 to 200 ;Jg/L (Pesch and Morgan, 1978) and adult Nereis
diversicolor acute values ranged from 200 to 480 iJg/L over a salinity range
of 5 to 34 g/kg, respectively (Jones, et al. 1976).
Acute values for saltwater fishes ranged from 13.93 to 411.7 Mg/L and as
with invertebrates, the lowest value was obtained in a test with embryos. In
addition, tests with embryos of Atlantic cod resulted in a 14-day LC50 of 10
rig/L (Table 6). Birdsong and Avavit (1971) found that copper may hie more
toxic to adult pompano at a salinity of 10 g/kg than at 30 g/kg. A number of
anadromous species, such as the coho salmon, have been exposed to copper in
fresh water. These data were utilized in deriving the freshwater, but not
the saltwater, criterion.
The 19 available saltwater Genus Mean Acute Values ranged from 5.8 tJg/L
for Mytilus to 7,694 ;jg/L for Rangia for a factor of over 1,000. Acuce
values are available for more than one species in each of five genera and che
range of Species Mean Acute Values within each genus is less than a factor of
3.7. A saltwater Final Acuce Value of 5.832 yg/L was obtained using the
Genus Mean Acute Values in Table 3 and the calculation procedure described in
the Guidelines. This is close to the acute value of 5.8 Mg/L for the blue
mussel and the value of 7.807 Jg/L for the Pacific oyster.
10
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Chronic Toxicicy to Aquacic Animals
Chronic coxicicy tests have been conducted on copper in fresh water with
five invertebrate and ten fish species (Table 2). In addition, results of
seven life-cycle tests with daphnids are listed in Table 6, because the
copper concentrations were not measured during the tests. Winner (1984a,b)
demonstrated that both humic acid and selenium decreased the chronic toxicity
of copper to Daphnia pulex. A Life-cycle test with the fathead minnow was
conducted in a stream water of variable quality (Brungs, et al. 1976). This
result is in Table 6, because the dilution water for the test was obtained
downstream of a sewage treatment plant and contained varying, high concentra-
tions of organic material, phosphates, etc. Long-term tests by Seira, et al.
(1984) with rainbow trout and by Nebeker, et al. (1984) with the midge,
Chironomus tentans, are also in Table 6, because the studies did not include
reproductive effects. Seim, et al. (1984) and McKim, et al. (1978) obtained
nearly identical results with the trout at slightly different hardnesses.
The 20-day EC50 for the mid<»e, Chironomus tentans, indicates that this
species is slightly more resistant to copper than other invertebrates in
long-term tests .
The fifteen chronic values for the ten fish species range from 3.873
Jg/L in an early life-stage test with brook trout to 60.36 ^g/L in an early
life-stage test with northern pike (Table 2). The seven values for the five
invertebrate species range from 6.066 to 29.33 'jg/L. The range for fishes is
greater than the range for invertebrates, but this is largely due to the fact
that the three chronic values for brook trout range from 3.873 to 31.15 Jg/L.
The only fish species with a chronic value greater than 31.15 pg/L is the
northern pike at 60.36 ;Jg/L. Although 22 chronic tescs have been conducted
on copper with freshwater species (Table 2), comparable acute values are not
11
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available for eighc of che chronic ces^s, and one addicional chronic cesc did
noc actually produce a chronic value.
The range of che thirteen acute-chronic ratios that can actually be
calculated is 153, and the range of the thirteen individual acute values is a
factor of 85. However, the range of the thirteen chronic values is only a
factor of 4.8, indicating that for copper, che chronic values, rather than
che acute-chronic ratio, is nearly constant across species. Most of che
range in che acute-chronic racio is obviously due to che range in che acute
values, and che correlation coefficient (r) between che logarichm of che
acute-chronic racio and the logarichm of che acute value is 0.94. The
increase in che acuce-chronic racio for resistant species might be due to an
increase in precipicacion of copper in acute tests as che senaicivicy of che
species co copper decreases. If che chronic cescs for chese same species are
generally conducced ac concencracions below che solubilicy limit of che
common hydroxy-carbonaces, che racio would be increased when precipicacion
occurs in che acuce cescs.
Because che Final Acute-Chronic Ratio is meant to be used to calculate a
Final Chronic Value from the Final Acute Value and because che Species Mean
Acuce Values for Daphnia magna and Gammarus pseudolimnaeus (Table 3) are only
slightly higher than the Final Acute Value, it seems reasonable co use che
geometric mean of che Species Mean Acute-Chronic Ratios for chese two species
as the Final Acute-Chronic Ratio. Division of the Final Acute Value by che
Final Acute-Chronic Racio of 2.823 results in a Final Chronic Value of 6.539
•jg/L at a hardness of 50 mg/L.
The available information concerning the effect of hardness on the
chronic toxicity of copper is inconclusive. The four chronic tests with che
12
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fachead minnow show a consiscenc relationship, and che slope of 0.2646 is
much lower chan che pooled slope of 0.9422 for Che effecc of hardness on
acuce coxicicy. On che other hand, in cescs wich Daphnia magna Chapman, ec
al. (Manuscripc) found a slope of 1.075 when hardness was increased from 51
co 104 mg/L, buc a very negacive slope when hardness was increased from 104
co 211 mg/L. Ic seems reasonable co assume chac chronic coxicicy decreases
as hardness increases for cwo reasons. First, che available daca seem co
suggesc ic. Second, che small acuce-chronic racio and che scrong effecc of
hardness on acuce coxicicy require an effecc of hardness on chronic coxicicy
if che Final Chronic Value is co be below che Cricerion Maximum Concencracion
ac very low hardnesses. On che ocher hand, if che chronic slope is assumed
co be equal co che acuce slope of 0.9422, che Final Chronic Value would be 24
lJg/L ac a hardness of 200 mg/L. This seems a liccle high based on che
chronic values ac high hardness in Table 2. The combinacion of a chronic
incercepc of -1.465 and a chronic slope of 0.8545 provides che lowesc chronic
slooe chac will keep che Final Chronic Value below che Cricerion Maximum
Concencracion down co a hardness of 1 tng/L and will resulc in a Final Chronic
Value of 6.539 Jg/L ac a hardness of 50 mg/L. This corabinacion resulcs in a
Final Chronic Value of 21 ;Jg/L ac a hardness of 200 rag/L, which seems more
appropriace chan che value of 24 ^jg/L.
The only salcwacer chronic value available is for che mysid, Mysidopsis
bahia (Table 2). The chronic coxicicy of copper co chis salcwacer inverce-
brace was decerrained in a flow-chrough life-cycle cesc in which che
concencracions of copper were measured by acomic absorpcion speccroscopy.
Survival was reduced ac 140 Jg/L, and che number of spawns recorded ac 77
was significancly (P<0.05) fewer chan ac 38 ,Jg/L. The number of spawns
13
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ac 24 and 38 Mg/L was not significantly different from che number of spawns
in the controls. Brood size was significantly (P<0.05) reduced at 77 ug/L,
but not at lower concentrations, and no effects on growth were detected at
any of the copper concentrations. Based upon reproductive data, unacceptable
effects were observed at 77 ug/L, but not at 38 Jg/L, resulting in a chronic
value of 54.09 ^ig/L. Using the acute value of 181 ^ig/L, the acute-chronic
ratio for this species is 3.346 (Table 2).
Use of 3.346 as the saltwater Final Acute-Chronic Ratio does not seem
reasonable because Mysidopsis bahia is relatively acutely insensitive to
copper. The lowest saltwater acute values are from tests with embryos and
larvae of molluscs and embryos of summer flounder, which are possibly the
most sensitive life stages of these species. It seems likely that
concentrations that do not cause acute lethality to these life stages of
these species will not cause chronic toxicity either. Thus, for salt water
the Final Chronic Value for copper is equal to the Criterion Maximum
Concentration of 2.916 ;jg/L (Table 3).
Several recent studies have attempted to test the validity of the
"two-number" basis of the 1980 copper criteria (U.S. EPA, 1980). Ingersoll
and Winner (1982) and Seim, et al. (1984) tested che effects of daily pulses
at the copper LC50 to Daphnia pulex and rainbow trout, respectively. Both
studies maintained the "average concentration" at or below the "no effect"
concentration of a comparable long-term test with continuous exposure.
Ingersoll and Winner (1982) observed a reduction in brood size and decreased
survival of daphnids in the pulsed exposure. Similarly, Seim, et al. (1984)
noted decreases in both survival and growth of trout with pulsed exposures-.
Buckley, et al. (1982) exposed coho salmon continuously to copper levels of
14
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1/4 and 1/2 the LC50, while periodically testing acute toxicity (168-hr
LC50), which is equivalent to short "pulses" above the long-term average
concentration. Both groups of fish acclimated to the long-term copper
exposure, and increased tolerance to acuce exposures. At the end of 16 weeks
the 168-hr LC50 of fish exposed ac 1/2 the original LC50 increased 2.5 fold.
Exposure to 1/4 the LC50 increased the 168-hr LC50 by 40%. These results
were shown to be related to storage of copper in the liver and the induction
of metallothionein or other hepatoproteins (Dixon and Sprague, 1981b;
McCarter and Roch, 1984; McCarter, et al. 1982).
Acclimation to chronic exposure to copper is a protective mechanism, as
is the induction of chelate excretion by algae (McKnight and Morel, 1979) and
the development of copper-resistant strains of phytoplankton (Foster, 1982).
All of the above studies indicate, however, that acclimation of either
individuals, species, or populations requires sublethal exposures of several
days or weeks duration, and that rapid excursions to near-lethal levels are
more harmful than continuous low-level exposure.
LaPoint, et al. (1984) conducted field studies of effects of metal
concentrations on benthic communities in 15 streams impacted to varying
degrees by raining and industrial wastes. Their results at each sampling site
were compared to hardness-relaced criteria calculated for each mecal based on
the 1980 criteria documents (U.S. EPA, 1980). This comparison indicated
that "for the relatively simple metal pollution problems the resident
fauna responds in a predictable and indicative manner". In these cases,
where only one or two metals were found, impacts on che benthos corresponded
to areas of the stream exceeding the criteria. In a majority of cases,
however, the complexity of the waste and the physical habitat or the
15
-------
influence of nucrient-rich effluencs made che "community scruccural response
less readily predictable". In general, these studies cend to support
the calculated criteria in chose cases where the area impacted by the metals
was defineable and valid upstreax-downstream comparisons could be made. This
report also points up che enormous difficulty of attempting to extrapolate
from laboratory results to complex field situations.
Toxicity to Aquatic Planes
Copper has been widely used as an algicide and herbicide for nuisance
aquatic plants (McKnight, et al. 1983). Although it is known as an inhibitor
of photosynthesis and plant growth, toxicity data on individual species
(Table 4; see also Rai, et al. 1981; Spear and Pierce, 1979a) are not
numerous.
The relationship of copper toxicity to the complexing capacity of the
water or the culture medium is now widely recognized (Gachter, et al. 1973;
Petersen, 1982) and several recent studies have used algae co "assay" the
copper complexing capacity of both fresh and salt waters (Allen, ec al.
1983; Lumsden and Florence, 1983; Rueter, 1983). It has also been shown chat
algae are capable of excreting coraplexing substances in response to copper
stress (McKnight and Morel, 1979; Swallow, et al. 1978; Van den Berg, ec al.
1979). Foster (1982) and Stokes and Hutchinson (1976) have identified
resistant strains and/or species of algae from copper (or other metal)
impacted environments. A portion of this resistance probably results from
induction of the chelate-excretion mechanism. Chelate-excretion by algae may
also serve as a protective mechanism for other aquatic organisms in eutrophic
waters, i.e., where algae are capable of maintaining free copper activities
below harmful concentrations.
16
-------
Copper concentrations from 1 co 8,000 ug/L have been shown to inhibic
growth of various plant species. Several of the values are near or below the
chronic values for fish and invertebrate species, but most are much higher.
No Final Plant Value can be obtained because none of the plant values were
based on tests with important species in which the concentrations of copper
were measured in the test solutions.
Data are available on the toxicity of copper in salt water to two
species of macroalgae and ten species of microalgae (Table 4). A copper
concentration of 100 ^ig/L caused a 50% decrease in photosynthesis in the
giant kelp, Macrocystis pyrefera (Clendenning and North, 1959). Growth
reduction in the red alga, Champia parvula, occurred in both the tetrasporo-
phyte and female plants exposed to copper concentrations of 4.6 and 4.7 ^ig/L
(Steele and Thursby, 1983). Microalgae were equally sensitive to copper.
The growth rates of Thalassiosira pseudonana and Scrippsiella faeroense were
reduced by 50% after exposure to 5.0 ug/L for three and five days,
respectively. Thus, saltwater plant species show similar sensitivity to
copper as animal species, and water quality criteria that protect saltwater
animals should also protect saltwater plants.
Bioaccumulation
Bioconcentration factors (BCFs) in fresh water ranged from zero for the
bluegill to 2,000 for the alga, Chlorella regularis (Table 5). In salt water
the polychaete worm, Neanthes arenaceodentata, bioconcentrated copper 2,550
times (Pesch and Morgan, 1978), whereas in a series of measurements with
algae by Riley and Roth (1971) the highest reported BCF was 617 for
Heteromastix longifillis. The highest saltwater BCFs were obtained with
17
-------
bivalve molluscs. Shuscer and Pringle (1969) found chac che eascern oyscer
could concencrace copper 28,200 ciraes during a 140-day concinuous exposure co
50 nig/L. Even though che tissue of che oyscer became bluish-green,
mortalities were only slightly higher than in che controls. This araounc of
copper is noc known co be harmful to man, but che color would undoubtedly
adversely affect the marketability of oysters. Because no maximum
permissible tissue concentration exists, neither a freshwater nor a saltwater
Final Residue Value can be calculated for copper.
Other Data
Many of che data in Table 6 are acute values for durations other than 96
hours with che same species reported in Table 1, with some exposures lasting
up to 30 days. Acute values for test durations less than 96 hours are
available for several species not shown in Table 1, and these species have
approximately the same sensitivities to copper as species in the same
families listed in Table 1. For example, Anderson, ec al. (1980) report a
10-day value for che midge, Tanycarsus dissimilis, of 16.3 ug/L in soft
wacer. This compares with che 96-hr LC50 of 30 ;jg/L for Chiionomus at a
hardness of 50 mg/L (Rehwoldt, ec al. 1973). Reported LCSOs at 200 hours for
Chinook salmon and rainbow trout (Chapman, 1978) differ only slightly from
96-hr LC50s reported for these same species in the same water.
Many of che other acute tests in Table 6 were conducted in dilution
waters which were known to concain materials which would significantly reduce
che coxicicy of copper. These reduccions were different from those caused by
hardness, but not enough data exist to account for these in the derivation of
criteria. For example, Lind, ec al. (Manuscript) conducced cescs wich
18
-------
Daphnia pulicaria and che fachead minnow in wacers wich concentracions of TOG
ranging up co 34 rag/L. Similarly, Brungs, ec al. (1976) and Geckler, ec al.
(1976) conducced cases wich many species in scream wacer which contained a
large araounc of effluenc from a sewage treacmenc plane. Wallen, ec al.
(1957) cesced mosquicofish in a curbid pond wacer. Until chemical
measurements which correlate well wich che coxicicy of copper in a wide
variety of wacers are idencified and widely used, results of cescs in unusual
dilucion wacers, such as chose in Table 6, will noc be very useful for
deriving wacer qualicy criceria.
Table 6 also includes cescs based on physiological effects, e.g.,
changes in growth, appetice, blood parameters, stamina, etc. These were
included in Table 6, because chey could noc be directly incerpreced for
derivacion of criceria. Only avoidance of 0.1 vig/L by rainbow crouc fry
(Folmar, 1976) appeared co be subscancially lower chan ocher acuce -and
chronic effeccs lisced in Tables 1 and 2. Geckler, ec al. (1976) also
tiencion avoidance of copper at 120 ;Jg/L as a significant factor in cheir
studies on scream populacions. Such resulcs cannoc be translated into-
criceria, because of che paucicy of available daca and che number of poorly
understood factors involved in application of che resulcs, e.g., acclimation,
mixing zones, species specificity, etc.
Waiwood and Beamish (1978) scudied che effecc of copper on growch of
rainbow crouc ac different pHs. Baker, ec al. (1983), Hetrick, et al.
(1979), and Knitcel (1981) found chac exposure co copper increased che
susceptibility of rainbow crouc and chinook salmon co diseases. Ewing, ec
al. (1982) found little change in the infection race of channel cacfish
following sublechal exposure co copper.
19
-------
Mosc noteworthy among saltwater organisms are the values reported for
the bay scallop, Argopecten irradiens, which suffered mortality and reduced
growth when chronically exposed to concentrations of 5 and 5.8 tJg/L,
respectively (Table 6). Also, the 14-day LC50 of 10 ^ig/L for Atlantic cod
embryos further substantiates that this life stage is particularly sensitive.
These results and those from similar studies support the need for a saltwater
Final Chronic Value no greater than 2.9 ug/L.
Unused Data
Some data on the effects of copper on aquatic organisms were not used
because the studies were conducted with species chat are not resident in
North America, e.?., Ahsanullah, et al. (1981), Bougis (1965), Collvin
(1984), Cosson and Martin (1981), Heslinga (1976), Karbe (1972), Majori and
Petronio (1973), Mishra and Srivastava (1980), Negilski, et al. (1981), Pant,
et al. (1980), Saward, et al. (1975), Solbe and Cooper (1976), Verriopoulos
and Moraitou-Apostolopoulou (1982), and White and Rainbow (1982). Data were
not used if copper was a component of a mixture (Wong, et al. 1982). Reviews
by Chapman, et al. (1968), Eisler (1981), Eisler, et al. (1979), Phillips and
Russo (1978), Spear and Pierce (1979b), and Thompson et al. (1972) only
contain data that have been published elsewhere.
Ferreira (1978), Ferreira, et al. (1979), Leland (1983), Lett, et al.
(1976), Ozoh and Jacobson (1979), and Waiwood (1980) investigated effects of
copper on various physiological parameters of aquatic animals, buc che
reports do not contain any interpretable concentration-time relationships
useful for deriving criteria, de March (1979) and Wong, et al. (1977)
presented no useful data on copper. The results of Riedel (1983) and
20
-------
Sanders, ec al. (1983) were noc used because chey could not be interpreted in
cerras of acid-soluble copper.
Papers by Borgmann (1981), Filbin and Hough (1979), Frey, ec al. (1973),
Gillespie and Vaccaro (1978), Guy and Kean (1980), Jennett, ec al. (1982),
Maloney and Palmer (1956), Nakajima, ec al. (1979), Sunda and Lewis (1978),
Swallow, ec al. (1978), Van den Berg (1979), and Wagemann and Barica (1979)
reporc on scudies of various aspects of copper coraplexacion on upcake, »rowth
inhibition, or coxicity to various algae, bacteria, and plankton. Most of
these report data on relative effects, usually in artificial media, and do
not contain useable toxicological data for surface waters. Chelating agents
were used in the tests by Gavis, et al. (1981), Hawkins and Griffith (1982),
Lee and Ku (1984), Reed and Moffat (1983), Ruecer, ec al. (1981), Schenck
(1984), Sullivan, et al. (1983), and Wikfors and Ukeles (1982).
Papers thac dealt with the selection, adaptation, or acclimation of
organisms for increased resistance to copper were not used, e.g., Fisher
(1981), Fisher and Fabris (1982), Hall (1980), Harrison and Lam (1983),
Harrison, et al. (1983), Lumaden and Florence (1983), Lumoa, ec al. (1983),
Myinc and Tyler (1982), Neuhoff (1983), Parker (1984), Phelps, et al.
(1983), Ray, ec al. (1981), Sander (1982), Scarfe, et al. (1982), Schmidt
(1978a,b), Sheffrin, ec al. (1984), Sceele (1983), Viarengo, et al.
(1981a,b), and Wood (1983).
Abbe (1982), Bouquegmean and Martoja (1982), Gibbs, et al. (1981),
Gordon, ec al. (1980), Howard and Brown (1983), Mackey (1983), Martin, et al.
(1984), Pophan and D'Auria (1981), Smith, et al. (1981), and Strong and Luoma
(1981) did noc report sufficienc measurements of copper concencracions in
wacer to allow use of their field studies. Finlayson and Ashuckian (1979),
Labac, ec al. (1977), Mclntosh and Kevern (1974), McKnighc (1980), and Taylor
21
-------
(1978) reported the results of various field scudies wich poorly defined or
experimentally confounded exposure condicions. Papers by Baudouin and Scoppa
(1974), Dodge and Theis (1979), Evans (1980), Furraanska (1979), Muramoco
(1980, 1982), and Verina, ec al. (1980) contain too few experimental details
to allow interpretation of the results. Bringmann and Kuhn (1982) cultured
Daphnia magna in one water and conducted tests in another water. Smith and
Heath (1979) only reported results graphically. Shcherban (1977) did not
report usable results, and Brkovic-Popovic and Popovic (1977a,b) used
questionable dilution water. Data were not used if mortality in the controls
was coo high (Ho and Zubkoff, 1982; Huilsom, 1983; Watling, 1981, 1982,
1983). High control mortalities occurred in all except one test reported by
Sauter, et al. (1976). Control mortality exceeded 10% in one test by Mount
and Norberg (1984). The 96-hr values reported by Buikema, et al. (1974a,b)
were subject to error because of possible reproductive interactions (Buikeraa,
et al. 1977). Bioconcentration factors could not be calculated from the data
of Anderson and Spear (I980a).
Summary
Acute toxicity data are available for species in 41 genera of freshwater
animals. At a hardness of 50 rag/L the genera range in sensitivity from 16.74
pg/L for Ptychocheilus to 10,240 ^ig/L for Acroneuria. Data for eight species
indicate that acute toxicity decreases as hardness increases. Additional
data for several species indicate that toxicity also decreases with increases
in alkalinity and total organic carbon.
Chronic values are available for fifteen freshwater species and range
from 3.873 pg/L for brook trout to 60.36 jjg/L for northern pike. Fish and
22
-------
invercebrace species seem co be about equally sensitive co che chronic
coxicicy of copper.
Toxicity cescs have been conducted on copper with a wide range of
freshwater plants and the sensitivities are similar to those of animals.
Coraplexing effects of the test media and a lack of good analytical data make
interpretation and application of these results difficult. Protection of
animal species, however, appears to offer adequate protection of planes.
Copper does not appear to bioconcentrate very much in the edible portion of
freshwater aquatic species.
The acute sensitivities of saltwater animals to copper range from 5.8
ug/L for the blue mussel to 600 ug/L for the green crab. A chronic
life-cycle test has been conducted with a mysid, and adverse effects were
observed at 77 jg/L but not at 38 ;jg/L, which resulted in an acute-chronic
ratio of 3.346. Several saltwater algal species have been tested, and
effects were observed between 5 and 100 ^ig/L. Oysters can bioaccumulate
copper up to 28,200 times, and become bluish-green, apparently without
significant mortality. In long-terra exposures, the bay scallop was killed ac
5 ug/L.
National Criteria
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" indicate that, except possibly where a locally important species
is very sensitive, freshwater aquatic organisms and their uses should not be
affected unacceptably if the four-day average concentration (in Mg/L.) of
copper does not exceed the numerical value given by
e(0.8545[ln(hardness)]-1.465) more chan once every
23
-------
average and if the one-hour average concencracion (in ug/L) does not exceed
che numerical value given by e<°-94221In(hardness)]-l.464) more chan
once every chree years on che average. For example, ac hardnesses of 50,
100, and 200 mg/L as CaC03 che fo\ir-day average concencracions of copper
are 6.5, 12, and 21 ug/L, respectively, and che one-hour average
concencracions are 9.2, 18, and 34 ug/L.
The procedures described in che "Guidelines for Deriving Numerical
Nacional Wacer Qualicy Criceria for che Proceccion of Aquacic Organises and
Their Uses" indicace chac, excepc possibly where a locally iraporcanc species
is very sensitive, salcwacer aquacic organisms and cheir uses should noc be
affecced unaccepcably if che one-hour average _oncencracion of copper does
noc exceed 2.9 ug/L more chan once every chree years on che average.
EPA believes chac a measurement such as "acid-soluble" would provide a
more scientifically correct basis upon which to establish criceria for
mecals. The criceria were developed on chis basis. However, ac chis time,
no EPA approved methods for such a measuremenc are available co implemenc che
criceria chrough che reguiacory programs of che Agency and che Scaces. The
Agency is considering developmenc and approval of mechods for a measurtemenc
such as "acid-soluble". Until available, however, EPA recommends applying
the criceria using che cocal recoverable mechod. This has cwo impacts: (1)
certain species of some raecals cannoc be analyzed directly because che total
recoverable mechod does noc discinguish becween individual oxidacion scaces,
and (2) chese criceria may be overly proceccive when based on che cocal
recoverable mechod.
The recommended exceedence frequency of chree years is che Agency's besc
sciencific judgraenc of che average amounc of time ic will take an unstressed
system co recover from a pollucion evenc in which exposure co copper exceeds
24
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che criterion. Stressed systems, for example, one in which several outfalls
occur in a limited area, would be expected to require more time for recovery.
The resilience of ecosystems and their ability to recover differ greatly,
however, and site-specific criteria may be established if adequate
justification is provided.
The use of criteria in developing waste treatment facilities requires
the selection of an appropriate wasteload allocation model. Dynamic models
are oreferred for the application of these criteria. Limited data or other
factors may make their use impractical, in which case one should rely on a
steady-state model. The Agency recommends the interim use of 1Q5 or 1Q10 for
Criterion Maximum Concentration (CMC) design flow and 7Q5 or 7Q10 for the
Criterion Continuous Concentration (CCC) design flow in steady-state models
for unstressed and stressed systems respectively. These matters are
discussed in more detail in the Technical Supnort Document for Water
Quality-Based Toxics Control (U.S. EPA, 1985).
25
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TabI* 1. Acute Toxlclty of Copper to Aquatic Animals
Species
Method*
Chemical
Worm,
Lumbrlculus varlegatus
Tubl field worm,
Llmnodrllus hot fmel star I
Worm,
Nals sp.
Snal 1,
Campeloma dec! sum
Snal 1 (embryo) ,
Amnicola sp.
Snail (adult),
Amnicola sp.
Snail,
Gon 1 obas I s 1 1 vescen s
Snail,
Gon 1 obas Is II vescen s
Snail,
Gyraulus clrcumstr latus
Snail,
Physa heterostropha
Snail,
Physa Integra
Asiatic clam,
Corblcula flumlnea
Asiatic clam,
Corblcula flumlnea
Cladoceran,
s,
s.
s.
FT.
s.
s.
s,
s.
s.
s.
FT.
s.
FT,
s.
U
It
M
M
M
M
H
M
U
U
H
U
U
U
Hardness LC50 Species Mean
(mg/L as or EC50 Acute Value
CaCOx)
Reference
Copper
sul fate
Copper
sul fate
-
Copper
sul fate
-
-
Copper
sulfate
Copper
sulfate
Copper
sul fate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sjl fate
-
FRESHWATER SPECIES
30
100
50
35-55
50
50
154
154
100
100
35-55
64
64
45
150 242.7
102 53.08
90 90.00
1,700 1,877
9,300»»»»
900 900.0
590
390 166.2
108 56.21
69 35.91
39 43.07
40
490 •»•••
17 IB. 77
Bailey 4 1
Wurfz 4 Bi
Rehwoldt,
Arthur & 1
Rehwoldt,
Rehwoldt,
Pau 1 son , i
Pau 1 son , i
Wurtz & Bi
Wurtz & Bi
Arthur & 1
Rodgers , i
Rodgers, <
Mount and
Cerlodaphnla retleu I ata
1984
26
-------
Table 1. (Continued)
Spact as
Cladoceran,
Daphnia magna
Ciadoceran,
Daphn1 a magna
Cladoceran,
Paphnja aagna
Ciadoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Oaphnla magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Oaphnla magna
Cladoceran,
Daphnia magna
Method"
S, U
S. u
S, U
S. U
S, U
S, M
S, M
S, M
S. M
S, U
S. M
S, M
S, U
S, U
Chemical
Copper
chloride
Copper
sul fate
Copper
Ch i or i Ci6
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
ch 1 or 1 de
Copper
ch 1 or t de
Copper
sul fate
-
Copper
oxide
Copper
sal fate
-
Hardness
lmg/L as
CaCO,)
-
226.
45.3
99
99
52
105
106
207
45
100
143
250
45
LC50
or EC50
(Mg/L)««
12.7
200
9.8
85
50
26
30
38
69
10
31.8
26
6.5*
54
Species Mean
Acute Valua
-------
Table 1. (Continued)
Species
Cladoceran,
Oaphnla pulex
Cladoceran,
Daphn la pulex
Cladoceran,
Daphn la pull car la
Cladoceran,
Oaphnla pull car la
Cladoceran,
Oaphn 1 a pu 1 1 car 1 a
Cladoceran,
Daphn la pu 1 1 car 1 a
Cladoceran,
Daphn la pull car la
Cladoceran,
Daphn la put tear la
Cladoceran,
Oaphnla pull car la
Cladoceran,
Oaphnla puMcarla
Amph 1 pod,
Ganmarus pseudo 1 1 mnaeus
Amph i pod ,
Gamnarus pulex
Amph 1 pod,
Gammarus pulex
Amph 1 pod,
Gammarus sp.
Method* Chen leal
S, U Copper
sol tata
S, U
S, M
S, M
S, M
S. M
S, M
S. M
S, M
S, M
FT, M Copper
sul fate
R, U Copper
chloride
R, U Copper
chloride
S, M
Hardness
(•9/L as
CaC05)
45
45
48
48
48
44
45
95
145
245
45
104
249
50
LC50
or EC50
-------
TabU 1. (Continued)
Species Method*
Crayfish, S, M
Orconectes llmosus
Crayfish, FT, M
Orconectes rustlcus
Crayfish (larva), FT, M
Procambarus clarkll
Damsel fly, S, H
Unidentified
Stonefly, S, M
Acroneurla Iycor I as
Caddlstly, S, M
Unidentified
Midge (1st Instar), FT, M
Chironomus tentans
Midge (2nd Instar), FT, M
Chlronomus tentans
Midge (3rd Instar), FT, M
Chlronomus tentans
Midge (4th Instar), FT, M
Chlronomus tentans
Midge. S, M
ChIre-nonius sp.
Bryozoan, S, U
Pectinate!la magnlflca
Bryozoan, S, U
Lophopodella carter I
Bryozoan, S, U
PI lima tell a emarglnata
American eel, S, M
ArcgulI la rostrata
Chemical
Copper
chloride
Copper
sulfate
Copper
sul fate
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
sul fate
Copper
nl trate
Hardness
(•g/L as
CaCO)
100-125
17
50
40
50
71-84
71-84
71-84
71-84
50
190-220
190-220
190-220
53
LC50
or EC50
Species Mean
Acute Value
600
3,000
720
4,600
8,300
6,200
298
773"»*»
1,690«*««
30
510
140
140
6,400
1,397
1 ,990
4,600
10,240
6,200
Reference
Boutet &
Chalseraartln, 1973
Hubschman . 1967
Rice 4 Harrison, 1983
Rehwoldt, et al. 1973
Marnlck & Bel 1, 1969
Rehwoldt, et al. 1973
Nebeker, et al. !9S4a
Nebeker, et al. 1984a
Nebeker, et al. I984a
197.2 Nebeker, et al. 1904a
30.00 Rehwoldt, et al. 1973
135.0 Pardue & Wood, 1980
37.05 Pardue A Wood, 1980
37.05 Pardue & Wood, 1980
Rehwoldt, et al . 1971
29
-------
Table 1. (Continued)
Species Method*
American eel, S, H
Annul 1 la rostrata
American eel S. U
(black eel stage),
Angul 1 la rostrata
American eel S, U
(glass aal stage),
Angul 1 la rostrata
Coho salmon (adult), FT, M
Oncorhynchus ki sutch
Coho salmon (parr), FT, M
Oncorhynchus kl sutch
Coho salmon (adult), FT, H
Oncorhynchus klsutch
Coho salmon (yearling), S, H
Oncorhynchus kl sutch
Coho salmon (yearling), S, M
Oncorhynchus k I sutch
Coho salmon (smolt), S, M
Oncorhynchus klsutch
Coho salmon (juvenile), R, M
Oncorhynchus klsutch
Sockeye salmon (smolt), R, M
Oncorhynchus nerka
Sockeye salmon (smolt), R, M
Oncorhynchus nerka
Sockeye salmon ( fl ngerl 1 ng) , R, M
Oncorhynchus nerka
Sockeya salmon < fl ngerl 1 ng) , R, M
Oncorhynchus nerka
Chemical
Copper
sulf ate
Copper
sill tate
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chlorl da
Copper
chloride
Hardness
(sg/L ss,
CaCO,)
55
40-48
40-48
20
23
23
89-99
89-99
89-99
33
36-46
36-46
36-46
36-46
LC50
or EC50
6,000
3. .200
2.540
46
28-38
42.9
74
70
60
164
240
103
220
210
Species Mean
Acute Vaius
(M3/L)1"" Reference
Rehwoldt, et al. 1972
Hlnton & Eversole.
1979
4.305 Hinton & Eversole.
1978
Chapman & Stevens,
1978
Chapman, 1975
Chapman, 1975
Lorz 4 McPherson, 1976
Lorz & McPherson, 1976
Lorz A McPherson, 1976
70.25 Buckley, 1983
Davis & Shand, 1978
Davis & Shand, 1978
Davis & Shand, 1978
Davis 4 Shand, 1978
30
-------
Table I. (Continued)
Spec las
Sockeye salmon (finger ling),
Oncorhynchus nerka
Chinook salmon (alevln),
Oncorhynchus tshawytscha
Chinook salmon (swim-up),
Oncorhynchus tshawytscha
Chinook salmon (parr),
Oncorhynchus tshawytscha
Chinook salmon (smolt),
Oncorhynchus tshawytscha
Chinook salmon (juvenile),
Oncorhynchus tshawytscha
Chinook salmon,
Oncorhynchus tshawytscha
Chinook salmon,
Oncorhynchus tshawytscha
Chinook salmon,
Qncorhyncnus tshawytscha
Chinook salmon,
Oncorhynchus tshawytscha
Chinook salmon,
Oncorhynchus tshawytscha
Cutthroat trout,
Sal no clarkl
Cutthroat trout,
Sal mo clarkl
Cutthroat trout.
Sal mo clarkl
Method*
R,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
FT,
M
M
M
M
M
M
M
M
H
M
H
M
M
M
Chen leal
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
-
-
-
-
Copper
sulfate
Copper
chloride
Copper
chloride
Copper
chloride
Hardness
<«g/L as
CaCO,)
36-46
23
23
23
23
25
13
46
182
359
21
205
70
16
LC50
or EC50
(tifl/L)**
240
26
19
38
26
33.1
10
22
85
130
32
367
186
36.8
Species Mean
Acute Value
dig/D"1 Reference
233.8 Davis & Shand, 1976
Chapman, 1975, 1978
Chapman, 1975, 1978
Chapman, 1975, J978
Chapman, 1975, 1978
Chapman, 1982
Chapman & McCrady,
1977
Chapman & McCrady,
1977
Chapman & McCrady,
1977
Chapman & McCrady,
1977
42.26 Flnlayson & Verrue,
1982
Chakoumakos, et al.
1979
Chakoumakos, et al.
1979
Chakoumakos, et al.
1979
31
-------
Table I. (Continued)
Species
Cutthroat trout,
Sal mo clarkl
Cutthroat trout.
Sal mo dark)
Cutthroat trout,
Salmo clarkl
Cutthroat trout,
Salmo clarkl
Cutthroat trout,
Salmo clarkl
Cutthroat trout,
Salmo clarkl
Rainbow trout,
Salmo galrdnerf
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdner I
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo galrdneri
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Method*
FT, M
FT, M
FT, H
FT, H
FT, H
FT, M
FT, H
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
Chemical
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
ch 1 or i de
Copper
chloride
Copper
sul tate
Copper
sul tate
Copper
sul tate
Copper
sul tate
Copper
sul tate
Copper
sul tate
Copper
sul tate
Copper
sul tate
Hardness
(mg/L as
CaOOxL
204
83
31
160
74
26
30
32
31
31
30
101
101
99
LC50 Species Mean
or EC50 Acute Value
digA)" tMg/L)«M
232
162
73.6
91
44.4
15.7 66.26
19.9
22.4
28.9
30
30
176
40
33.1
Reference
Chakoumakos, et al.
1979
Chakoumakos, et al.
1979
Chakoumakos, et al.
1979
Chakoumakos, et al.
1979
Chakoumakos, et a I.
1979
Chakoumakos, et al.
1979
Howarth & Sprague,
1978
Howarth & Sprague,
1978
Howarth A Sprague,
1978
Howarth & Sprague,
19 76
Howarth & Sprague,
1978
Howarth & Sprague,
1976
Howarth & Sprague,
1978
Howarth & Sprague,
1978
32
-------
Table 1. (Continued)
Spec las
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Sal mo gal rdnerl
Rainbow trout,
Sal mo qal rdnerl
Rainbow trout,
Salmo galrdneri
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo gaf rdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo qal rdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo gairdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Method*
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
Chemical
Copper
suit ate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
chloride
Copper
chloride
Copper
chloride
Copper
ch loride
Hardness
(mg/L as
CeC05>
102
101
99
100
100
98
370
366
371
361
194
194
194
194
tC50 Species Mean
or EC50 Acute Value
-------
TabU I.
-------
Table 1. (Continued)
Species
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo galrdnerl
Atlantic salmon,
Salmo salar
Atlantic salmon,
Salmo salar
Atlantic salmon,
Salmo salar
Brook trout,
Salvellnus font) nails
Chiselmouth,
Acrochellus alutaceus
Central stonerol ler,
Campostoma anomalum
Goldfish,
Carasslus auratus
Goldfish,
Carasslus auratus
Common carp,
Cyprinus carpU)
Method*
FT, M
FT, M
S, M
FT, M
FT, M
S, M
FT, M
FT, M
FT, M
FT, M
S, U
FT, M
S, M
Chemical
Copper
sulfate
Copper
sul fate
Copper
sulfate
Copper
chloride
Copper
sulfate
Copper
sulfate
Copper
chloride
Copper
sulfate
Copper
sulfate
Copper
sul fate
Copper
nl trate
Hardness
(mg/L as
CaCO,)
125
125
290
90
120
20
8-10
14
45
52-56
200
20
52
53
LC50
or EC50
190
210
890
190
80
48
125
32
100
143
290
36
300
8IOn
Species Mean
Acute Value
(yg/L)"* Reference
Spear, 1977; Anderson
& Spear, 1980b
Spear, 1977; Anderson
& Spear, 19806
Calamarl 4 Harchettl ,
1973
Giles 4 Klaverkamp,
1982
42.50 Selre, et al. 1984
Sprague, 1964
HI (son, 1972
196.6 Sprague & Ramsey,
1965
110.4 McKIm & Benolt, 1971
133.0 Andros & Gar ton, 1980
78.55 Geek ler, et al. 1976
Pickering & Henderson,
1966
157.1 Tsal & McKee, 1978,
1980
Rehwoldt, et al .
1971
35
-------
TabU I. (Continued)
Species
Common carp,
Cyprlnus car pi o
Common carp ( 140 mg) ,
Cyprlnus carplo
Common carp ( 3200 mg) ,
Cyprlnus carplo
Common carp,
Cyprlnus carplo
Striped shiner,
Notropls chrysocephalus
Striped shiner.
Notropls chrysocephalus
Bluntnose minnow,
Plmephales notatus
B 1 un tnose i»l nnow ,
Plmephales notatus
Blunt nose minnow,
Plmephales notatus
B Inn tnose Minnow,
Plmephales notatus
Blun tnose minnow,
Plmephales notatus
Blun tnose minnow,
Plmephales notatus
Bluntnose minnow,
Plmephales notatus
Bluntnose minnow,
Plmephales notatus
Method"
S. H
S, U
s. u
R, U
FT, M
FT, M
FT, M
R, M
FT, M
FT, M
FT, M
FT, M
FT, M
FT, M
Chemical
-
Copper
sul fate
Copper
suf fate
Copper
sul fata
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Hardness
(«g/L as
Ca005)
V>
144-188
144-188
19
200
200
200
200
200
200
200
194
194
194
LC50 Species Mean
or EC50 Acute Value
-------
Table 1. (Continued)
Spec las
Fathead winnow,
Plmephales prone las
Fathead minnow,
Plmaphales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plreephales promelas
Fathead minnow,
Plmephales prone) as
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephalea promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Method*
S, U
S, U
FT, M
FT. M
FT, M
FT, H
S, U
S, U
S, U
S, U
S, U
S, U
S, U
FT, M
Chemical
Copper
sul tate
Copper
sul tate
Copper
sul tate
Copper
sul tate
-
-
Copper
sul tate
Copper
sul fate
Copper
sul tate
Copper
sultate
Copper
sul tate
Copper
sul tate
Copper
sul fata
Copper
sul tate
Hardness
(mg/L as
Caco^L
20
400
202
202
200
45
20
20
20
20
360
360
200
200
LC50
or EC50
-------
Table 1. (Continued)
Species
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow (adult),
Plmephales promelas
Fathead minnow (adult),
Plmephales promelas
Fathead minnow (adult),
Plmephales promelas
Fathead minnow (adult),
Plmephales promelas
Northern squawflsh,
Ptychochel lus oregonensls
Blacknose dace,
Rhlnlchthys atratulus
Creek chub,
Semotl lus atromaculatus
Brown bul (head,
Ictalurus nebulosus
Method*
s.
FT,
FT.
FT.
FT,
FT,
FT.
s.
s.
S.
s.
FT,
FT,
FT.
FT,
U
M
M
M
M
M
M
M
M
M
M
M
M
M
M
Chemical
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
-
-
-
Copper
sultate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
chloride
Copper
sul fate
Copper
sul fate
Copper
su 1 fate
Hardness
(mg/L as
CaCOj)
31
31
200
200
48
45
46
103
103
103
254-271
52-56
200
200
202
LC50
or EC50
84
75
440
490
114
121
88.5
210
310
120
390
18
320
310
170
Species Mean
Acute Value
(n9/U"** Reference
Mount & Stephen, 1969
Mount & Stephen, 1969
Geckler, et al . 1976
Geckler, et al . 1976
Lind, et al .
Manuscript
Llnd, et al.
Manuscript
Llnd, et al.
Manuscript
Blrge, et al . 1983
Blrge, et al . 1983
Birge, et al . 1983
115.5 Birge, et al. 1983
16.74 Andros & Carton, 1980
86.67 Geckler, et al. 1976
83.97 Geckler, et al. 1976
Brunqs, et al . 1973
38
-------
Table 1. (Continued)
Species
Brown bul (head,
Ictalurus nebulosus
Brown bul (head,
Ictalurus nebulosus
Banded kl III fish,
Fundulus dlaphanus
Banded kl III fish.
Fundulus dlaphanus
Mosqultoflsh (female),
Gambusla afflnls
Mosqultoflsh (female),
Gambusla afflnls
Guppy,
Poecl 1 la retlculata
Guppy,
Poecl Ma retlcuJata
Guppy,
Poecl 1 la retlculata
Guppy (6.5 mg) ,
Poecl lla retlculata
Guppy (63 mg; female),
Poecllla retlculata
Guppy (60 mq; male),
Poecllla retlculata
Guppy (340 mg; female),
Poecl H» retlcuJata
Guppy,
Poecllla retlculata
Guppy,
Poecl 1 la rotlculata
Method*
FT, M
FT, M
S, M
S, M
S, U
S, U
S, U
FT, M
FT, M
R, U
R, U
R. U
R, U
S, U
S, U
Chen leal
Copper
sul fate
Copper
sul fate
Copper
ni trate
Copper
nitrate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Hardness
(•g/L as
CaCOj)
202
200
53 »
55
27-41
27-41
20
87.5
67.2
144-188
144-188
144-188
144-188
230
240
LC50
or EC50
190
540
860
840
93
200
36
112
138
I60m
275m
210ttf
480m
1.250
764
Species Mean
Acute Value
(M<]/L)*** Reference
Brungs, et al. 1973
69.81 Geckler, et al . 1976
Rehwoldt, et al . 1971
790.6 Rehwoldt, et al . 1972
Joskl & Rege, 1980
196.1 Joskl 4 Rege. 1980
Chynoweth, et al. 1976
Black, 1974;
Chynoweth, et al. 1976
Black, 1974;
Chynoweth, et al. 1976
Deshmukh &
Mara the, 1980
Deshmukh &
Marathe, 1980
Deshmukh &
Marathe, 1980
Deshmukh &
Marathe, 1980
Khangarot, 1981
124.6 Khangarot, et dl .
19816
39
-------
Tab)* I. (Continued)
Specie*
White perch,
Moron* aowricana
White perch.
Morone amerlcana
Striped bass,
Morone saxatl I Is
Striped bass.
Morone saxatl Us
Striped bass,
Morone saxat Ills
Striped bass (larva),
Morone saxatl 1 Is
Striped bass < finger ling) ,
Morone saxat Ills
Stripped bass (larva),
Morone saxatl 1 1 s
Striped bass ( t 1 ngerllng) ,
Morone saxat Ills
Punpklnseed,
Lopomls glbbosus
Punpklnseed,
tepomls qlbbosus
Punpklnseed,
lepouls glbbosus
PuMpklnseed,
Lepomls glbbosus
Pumpklnseed,
Lepouls glbbosus
Method8
S, H
S, M
S, M
S, M
S, U
S. 0
s, u
s, u
s, u
S, M
S, M
FT, M
FT, M
FT, M
Che* leal
Copper
nl trate
Copper
nitrate
Copper
sul fate
Copper
chloride
Copper
chloride
Copper
sul fate
Copper
sul fate
Copper
nitrate
-
Copper
sul fate
Copper
sul fate
Copper
sul fate
Hardness
<=3/L as
CaCOjL
53
55
53
55
35
34.5
34.5
34.5
34.5
53
55
125
125
125
LC50 Species Mean
or ECSO Acats Vsias
UO./L)"" (tig/L)*** Reference
6,200
6,400 5,860
4,300ft
4,000™
620
50
50
25
30 ***•*
2,400ft
2,700ft
1,240
1,300
1,670
Rehwoldt, et al.
Rsh-oldt, et sU
Rehwoldt, et al .
1971
Rehwoldt. et al.
1972
Wei Iborn, 1969
Hughes, 1973
Hughes, 1973
Hughes, 1973
Hughes, 1973
Rehwoldt, et al .
1971
Rehwoldt, et al .
1972
1971
197!
Spear, 1977; Anderson
& Spear, I980b
Spear, 1977; Anderson
& Spear, I980b
Spear, 1977; Anderson
& Spear, 19BOb
40
-------
Tabl* 1. (Continued)
Species
Pumpklnseed,
Lepomls glbbosus
Pumpklnseed,
Lepomls qlbbosus
Pumpklnseed,
Lepomls qlbbosus
Pumpklnseed,
Lepomls glbbosus
Bluegl 1 1,
L epom 1 s macr och 1 rus
Bluagl II,
Lepomts macrochl rus
Bluegl II.
Lepomls macrochlrus
Bluegl I I,
Lepomls macrochlrus
Rlueglll,
Lepomls macrochlrus
Bluegl II,
Lepomis macrochlrus
Btueglll,
Lepomls macrochlrus
Bluegl It,
Lepomls macrochlrus
Blueqlll,
Lepomls macrochlrus
Bluegl 1 1,
Lepomls macrochlrus
Method1
FT,
FT,
FT,
FT,
s,
s,
s,
FT,
FT,
FT,
s,
s,
S,
S,
H
M
M
M
0
U
U
M
M
M
U
U
U
U
Chemical
Cooper
sol fate
Copper'
sul tate
Copper
sulfate
Copper
sul fate
Copper
sul tate
Copper
sul fate
Copper
sulfate
Copper
sulfate
Copper
sul tate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
chlor 1 de
Hardness
<«g/L as
CaCOjl
125
125
125
125
52
209
365
45
200
200
20
400
43
43
LC50 Spec las Moan
or EC50 Acute Value
(H9/L)" (Mg/L)"»
\ ,940
1 ,240
1 ,660
1,740 640.9
400
680
1 ,020
1,100
8,300
10,000
200
10 ,000
770
1,250
Reference
Spear, 1977; Anderson
& Spear, I980b
Spear, 1977; Anderson
& Spear, 1980b
Spear. 1977; Anderson
& Spear, I980b
Spear, 1977; Anderson
& Spear. 1980b
Inglls & Davis, 1972
Ing Us 4 Davis, 1972
Inglis & Oavls, 1972
Benolt. 1975
Geckler, et al. 1976
Geckler, et al. 1976
TarzMelI & Henderson,
1960
Tarzwell A Henderson.
1960
Academy of Natural
Sciences, 1960
Academy of Natural
Sciences, 1960;
Patrick, et al. 1968;
Cairns A Scheler, 1968
-------
Table 1. (Continued)
Species
Blueql II,
Leoomls macrochlrus
Blueglll,
L epo» Is macroch 1 r us
Bluegl 1 1,
Lepoals macrochlrus
Blueqlll,
Lepomls macrochlrus
Blueglll,
Leponls Macrochlrus
Rainbow darter,
Etheostoma caeruleum
Orangethroat darter,
Etheostoma spectabl le
Mozambique tl lapla,
Ti lapla mossMRblcB
Polychaete worm,
Phyllodoce Maculata
Polychaete worm,
Neanthes arenaceodentata
Polychaete worn,
Neanthes arenaceodentata
Polychaete worn,
Neanthes arenaceodentata
Polychaete worm,
Nereis dlverslcolor
Polychaete worm.
Nereis dlverslcolor
Method*
S, U
s, u
FT, M
FT, M
FT, M
FT, M
FT, M
S, U
S, U
FT, M
FT, M
FT, M
S, U
S, U
Hardness
<«g/L a*
Chewlcal CaCO^)
Copper 20
sulfate
Copper 360
sul fate
Copper 35
sul fata
Copper 40
chloride
Copper 26
chloride
Copper 200
sul fate
Copper 200
sul fate
Copper 1 1 5
sul fate
SALTWATER SPECIES
Copper
sul fate
Copper
nitrate
Copper
nl trate
Copper
nl trate
Copper
sul fate
Copper
sul fate
LC50
or EC50
UgA)"
660
10,200
2.400
1,000
1,000
320
850
1,500
120
77
200
222
200
445
Species Mean
Acute Value
dig/D"11 Reference
Pickering & Henderson,
1966
Pickering & Henderson,
1966
O'Hara, 1971
Thompson, et al .
1980
1,017 Cairns, et al . 1981
86.67 Gecklar, et al . 1976
230.2 Geckler, et al . 1976
684.3 Quresh 1 & Saksena,
1980
120 McLusky & Phi 1 lips,
1975
Pesch & Morgan, 1978
Pesch & Morgan, 1978
150.6 Pesch & Hoftaan, 1982
Jones, et al. 1976
Jones, et al . 1976
42
-------
Table 1. (Continued)
Species
Polychaete worm.
Nereis dtverslcolor
Polychaete worm.
Nereis diver si col or
Black aba lone,
Hallotls cracherodl 1
Red aba lone,
Hallotls rutescens
Red aba lone (larva),
Hallotls rufescens
Blue mussel (embryo),
Mytl lus edulls
Pacific oyster (embryo),
Crassostrea gigas
Pacific oyster (embryo),
Crassostrea gigas
Pacific oyster (adult),
Crassostrea glgas
Eastern oyster (embryo),
Crassostrea virgin lea
Eastern oyster (embryo),
Crassostrea virgin lea
Eastern oyster (embryo),
Crassostrea virqlnlca
Eastern oyster (embryo),
Crassostrea virqlnlca
Common rangla,
Rang) a cuneata
Common rang 1 a ,
Rangla cuneata
Method11
s,
s,
s,
s.
s,
s,
s,
s,
FT,
s,
s,
s,
S.
S.
s.
u
u
u
u
u
u
u
u
M
U
U
U
u
u
u
Chewlcal
Copper
sulfate
Copper
su If ate
Copper
sulfate
Copper
su 1 fate
Copper
sultate
Copper
sul fate
Copper
su 1 fate
Copper
sul fate
Copper
sulfate
Copper
chloride
Copper
chloride
Copper
ch 1 or 1 de
Copper
chloride
Hardness LC50
(•g/L as or EC50
CaCOjL (M9/L)"
480
410
50
65
114
5.8
5.3
11.5
560»»»»
128
15.1
18.7
18.3
8,000
7,400
Species Mean
Acute Value
(ug/L)"*" Reference
Jones, at al. 1976
363.8 Jones, et al. 1976
50 Martin, et al . 1977
Martin, et al . 1977
86.08 Martin, et al . 1977
5.8 Martin, et al . 1981
Martin, et al . 1981
Coqllanese & Martin,
1981
7.807 Okazaki , 1976
Calabrese, et al . 1973
Maclnnes A Calabrese,
1978
Maclnnes & Calabrese,
1978
28.52 Maclnnes i Calabrese,
1978
Olson & Harrel, 1973
7,694 Olson & Harrel, 1975
43
-------
Table 1. (Continued)
Species
Soft-shall clam,
Hya arenarla
Copepod ,
Pseudodl apt onus coronatus
Copapod,
Eurytemora af finis
Cop apod,
Acartla clausi
Cop apod ,
Acartla tonsa
Copapod,
Acartla tonsa
Copapod ,
Acartla tonsa
Mysld,
Hysldopsls bah fa
Mysld,
Hysldopsls blqelowl
American lobs tar (larva),
Honarus amerlcanus
American lobster (adult),
Homarus amerlcanus
Dungenass crab ( larva) ,
Cancer magi star
Grean crab (larva),
Carclnus maanas
Shaapshaad minnow,
Cyprlnodon variegatus
Method*
s,
s.
s,
s,
s,
s.
s,
FT,
FT,
s,
s,
s,
s.
s,
U
u
U
u
u
u
u
H
M
U
U
U
U
|]
Hardness
(•g/L as
Chenlcal C«CO3)
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
chloride
Copper
nitrate
Copper
nitrate
Copper
nitrate
Copper
sulfata
Copper
sul fate
Copper
sul fate
Copper
ni trate
LC50
or EC50
-------
Table 1. (Continued)
Species
Atlantic silverside (larva),
Menldla menldla
Atlantic silverside (larva).
Hen 1 d 1 a men 1 d 1 a
Atlantic silverside (larva),
Menldia menldla
Atlantic silverside (larva).
Men 1 d 1 a men 1 d 1 a
Atlantic silverside (larva),
Menldla menldla
Atlantic silverside (larva),
Menldla menldla
Atlantic silverside (larva),
Menldla menldla
Tidewater si Iverslde,
Menldla penlnsulae
Florida pompano,
Trachlnotus carol Inus
Florida pompano,
Trachlnotus carol Inus
Florida pompano,
Trachlnotus carol inus
Summer flounder
(early cleavage embryo),
Parallchthys dentatus
Summer flounder
(early cleavage embryo),
Method*
FT,
FT,
FT,
FT,
FT.
FT,
FT,
s.
S,
s,
s,
FT,
FT,
M
M
M
M
M
M
M
U
U
U
U
M
M
Chemical
Copper
ni trate
Copper
nitrate
Copper
ni trate
Copper
nitrate
Copper
nl trate
Copper
ni trate
Copper
ni trate
Copper
nitrate
Copper
sul fate
Copper
sul fate
Copper
sul fate
Copper
nitrate
Copper
nl trate
Hardness LC50
(«g/L as or EC50
CaCOji^ (Mg/L)»"
66.6
216.5
101. 8
97.6
155.9
197.6
190.9
140
360
380
510
16.3
11.9
Species Mean
Acute Value
dig/D"" Reference
Cardin, 1982
Card In, 1982
Cardin, 1982
Cardin, 1982
Cardin, 1982
Cardin, 1982
135.6 Cardin, 1982
140 Hansen, 1983
Blrdsong & Avavit,
1971
Blrdsong & Avavit,
1971
41 1.7 Blrdsong & Avavl t,
1971
Cardin, 1982
Cardin, 1982
Parallchthys dentatus
45
-------
Table 1. (Continued)
Species Method*
Summer flounder FT, H
(bias tula stage embryo),
Parallchthys dentatus
Winter flounder (embryo), FT, H
Pseudop 1 euronectes
amerlcanus
Winter flounder (embryo), FT, H
Pseudop 1 euronectes
amerlcanus
Winter flounder (embryo), FT, M
Pseudop 1 euronectes
amerlcanus
Winter flounder (embryo), FT, M
Pseudop 1 euronectes
amerlcanus
Winter flounder (embryo), FT, M
Pseudop 1 euronectes
amerlcanus
Winter flounder (embryo), FT. M
P seudop 1 euronectes
amerlcanus
Winter flounder (embryo), FT, M
P seudop 1 euronectes
amerlcanus
Winter flounder (embryo), FT, M
Pseudop 1 euronectes
amerlcanus
Winter flounder (embryo), FT, M
Pseudop 1 euronectes
Chemical
Copper
chloride
Copper
nitrate
Copper
nitrate
Copper
nitrate
Copper
nitrate
Copper
chloride
Copper
nl trate
Copper
chloride
Copper
nitrate
Copper
nitrate
Hardness LCSO Species Mean
(mg/L as or EC50 Acute Value
111. B"" 13.93 Cardln
77.5 - Cardln
167.3 - Cardln
52.7 - Cardln
158.0 - Cardln
173.7 - Cardln
271.0 - Cardln
132.8 - Cardln
148 .2 - Cardln
98.2 128.9 Cardln
nee
, 1982
, 1982
, 1982
, 1982
, 1982
, 1982
, 1982
, 1982
, 1982
, 1982
amerlcanus
46
-------
Table I. (Continued)
* S = static, FT = flow-through, R = renewal, U = unmeasured, M * measured.
** Results are expressed as copper, not as the chemical.
•** Freshwater Species Mean Acute Values are calculated at a hardness of 50 mg/L using the pooled slope.
**•" Not used In calculation of Species Mean Acute Value because data are available tor a more sensitive II fa stage.
»*•»* NO Species Mean Acute Value calculated because acute values are too divergent for this species.
' Not used In calculations (see text).
ft Not used In calculations because Rehwoldt, et al. (1971, 1972, 1973) obtained values that appear to be higher
than appropriate for a number of species (see text).
ttt not used In calculations because of wide range In hardness.
Results of Covarlance Analysis of Freshwater Acute Toxlclty versus Hardness
Species
Daphnla magna
Daphnla maqna except
value fron Dave (1984)
Daphnla pul Icarla
Chinook salmon
Cutthroat trout
Rainbow trout
Fathead minnow
Guppy
Bluegi 1 1
All of above
AH of above except
value from Dave (1984)
n
13
12
8
10
9
40
25
5
15
125
124
Slope
0.4666
1.0438
0.6952
0.6092
0.8766
0 .8889
1.1949
1 .3639
0.7776
0.9177*
0.9422n
95| Confidence Halts Degrees of Freedom
-0.5141,
0.2906,
0.4480,
0.3530,
0.2560,
0.6520,
1.0455,
0.6289,
0.2848,
0.7886,
0.8209,
1.4474
1.7970
0.9424
0.8654
1 .4972
1.1258
1.3444
2 .0990
1.2703
1 .0468
1.0635
11
10
6
8
7
38
23
3
13
116
It5
p=0.09 for equality of slopes.
P=0.ll for equality of slopes.
-------
Tab)* 2. Chronic Toxlclty of Copper to Aquatic Animals
Species
T«st"
Chemical
Hardness
(mg/L as Limits Chronic Value
CaC03) Uq/D"
Reterenc*
FRESHWATER SPECIES
Snail,
Campeloma decision
Snal 1 ,
Ptiysa Integra
Cladoceran,
Daphnla maqna
Cladoceran,
Oaphnla maqna
Cladoceran,
Daphnla maqna
Amph 1 pod ,
Gammarus pseudoHmnaeus
Caddistly,
Cllstornla magnifica
Chinook salmon,
Oncorhynchus tshawytscha
Rainbow trout.
Sal mo galrdneri
Brown trout,
Sal mo trutta
Brook trout,
Salvellnus tontlnalls
Brook trout,
Salvellnus tontlnalls
Brook trout,
Salvellnus tontlnalls
Lake trout,
Salvellnus namaycush
LC
LC
LC
LC
LC
LC
LC
ELS
ELS
ELS
LC
ELS
ELS
ELS
Copper
sultate
Copper
sultate
Copper
ch 1 or 1 da
Copper
chloride
Copper
chloride
Copper
su 1 fate
Copper
ch 1 or i de
Copper
chloride
Copper
sultate
Copper
sultate
Copper
sul fate
Copper
sultate
Copper
su 1 f dte
Copper
sul fate
35-55
35-55
51
104
211
45
26
23
45.4
45.4
45
45.4
37.5
45.4
8-14.8
8-14.8
11.4-16.3
20-43
7,2-12.6
4.6-8
8.3-13
11.4-31.7
22.0-43.2
9.5-17.4
22.3-43.5
3-5
22.0-42.3
10.88
10.88
13.63
29.33
9.525
6.066
10.39
<7.4
19.01
30.83
12.86
31.15
3.U73
30.51
Arthur & Leonard,
1970
Arthur & Leonard,
1970
Chapman, et al.
Manuscript
Chapman, et al.
Manuscr 1 pt
Chapman, et al .
Manuscript
Arthur 4 Leonard,
1970
Nebeker, et al . 1984
Chapman, 1975, 1982
McKIm, et al . 1978
McKIm, et al. 197tt
McKIm & Benolt, 1971
McKIm, et al. 1978
Sauter, et al . 1976
McKIm, et al . 1978
48
-------
Table 2. (Continued)
Species
Northern pike,
Esox lucius
Bluntnose minnow,
Plmephales notatus
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
White sucker,
Catostomus commersoni
Blueqll 1,
Lepomis macrochirus
Mysld,
Mysldopsls bah la
" LC = 1 1 f e cycle or
T«sf
ELS
LC
LC
LC
LC
ELS
ELS
LC
LC
partial life
** Results are expressed as copper,
"""Adverse effects occurred at all
Results of
Species
Hardness
(mg/L as Limits Chronic Value
Chemical CaCO^) (v9/L)" (|ig/L)" Reference
Copper 45.4 34.9-104.4 60.36 McKIm, et al. 1978
sul fate
Copper 194 4.3-16 8.798 Horning & Neihelsel,
sul fate 1979
Copper 198 14.5-33 21.87 Mount, 1968
su 1 fate
Copper 30 10.6-18.4 13.97 Mount & Stephan, 1969
sul fate
Copper 200 24-32 27.71 Pickering, et al.
sulfate 1977
45 13.1-26.2 18.53 Lind, et al .
Manuscript
Copper 45.4 12.9-33.8 20.88 McKIm, et at. 1978
sul fate
Copper 45 21-40 28.98 Benoit, 1975
su 1 fate
SALTWATER SPECIES
Copper - 38-77 54.09 Lussier, et al.
nitrate Manuscript
cycle; ELS = early life stage.
not as the chemical.
concentrations tested.
Regression Analysis of Freshwater Chronic Toxlclty versus Hardness
n Slope 95$ Confidence Limits Degrees of Freedom
Daphnla maqna 3 -0.2508 -10.03, 9.53 1
49
-------
Table 2. (Continued)
Acute-Chronic Ratios
Species
Snail,
Campeloma dec Is urn
Snail,
Physa Integra
Cladoceran,
Daphnla magna
Cladoceran,
Paphnla magna
Cladoceran,
Oaphnla magna
Amphipod,
Gammarus pseudol Imnaeus
Ch 1 nook sa 1 nwn ,
Oncorhynchus tshawytscha
Brook trout.
Salvellnus font! nails
Bluntnose minnow,
Plmephales notatus
Fathead minnow.
Plmephales promelas
Fathead minnow.
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
BlueglU,
Leponls macrochlrus
Mysld,
Hysldopsls bah I a
Hardness
(mg/L as
CaCO})
35-55
35-55
51-52
104-105
207-211
35-55
23-25
45
194
198-200
30-31
200
45-48
45
—
Acute Value Chronic Value
(wg/L)
1,700
39
26
30
69
20
33.1
100
231.9*
470
75
474.8**
106.9*"
1,100
181
(ng/L) Ratio
10.88 156.2
10.88 3.585
13.63 1.908
29.33 1.023
9.525 7.244
6.066 3.297
<7.4 >4.473
12.86 7.776
8.7<*8 26.36
21.87 21.49
13.97 5.369
27.71 17.13
18.53 5.769
28.98 37.96
54.09 3.346
* Geometric mean ot three values from Horning and Neihelsel (1979) In Table I.
** Geometric mean of two values from Pickering, et al. (1977) In Table 1.
••"Geometric mean ot three values trow Llnd, et al. (Manuscript) In Table 1.
50
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
ink*
41
40
39
38
37
36
35
34
33
32
31
30
Genus Mean
Acute Value
-------
Table 3. (Continued)
Rank*
29
28
27
26
25
24
23
22
21
20
19
18
t*>nus Mean Spiles Mean Species HMO
Acute Value Acute Value Acute-Chronic
(pg/L)" Species " Ratio
331.8 Striped shiner,
Notropis chrysocepha lus
242.7 Worm,
Lumbriculus varieqatus
196.1 Mosqul tof Ish,
Gambusla af finis
166.2 Snail,
Gonlobasls livescens
157.1 GoldUsh,
Carasslus auratus
156 .8 Common carp,
Cyprlnus carplo
141.2 Rainbow darter,
Ethaostoma caeruleun
Orangethroat darter,
Etheostoma spectabl Is
I35i0 Bryoioan,
Pectinate! la magnl t lea
133.0 Chi se (mouth,
Acrochel lus alutaceus
124.6 Guppy,
Poecllla retlculata
1 10.4 Brook trout,
Salvelinus tontlnalis
91.29 Bluntnose minnow,
Plmephales notatus
Fathead ml nnow,
331.8
242.7
196.1
166.2
157.1
156.8
86.67
230.2
135.0
133.0
124.6
HO. 4 7.776
72.16 26.36
115.5 I0.33"«
Plmephales promelas
-------
Table 3. (Continued)
Rank*
17
16
15
14
13
12
11
10
Genus Mean Species Mean
Acute Value Acute Value
(tigA)** Species (pg/L)**
90.00 Worm,
Nals sp.
88.54 Coho salmon,
Oncorhynchus klsutch
Sockeye salmon,
Oncorhynchus nerka
Chi nook salmon,
Oncorhynchus tshaxytscha
86.67 Blacknose dace,
Rhlnlchthys atratulus
85.97 Creek chub,
Semotllus atrontaculatus
82.11 Cutthroat trout,
Salmo clarki 1
Rainbow trout,
Salmo gairdneri
Atlantic salmon,
Salmo salar
78.55 Central stoneroller,
Campos toma jnomalum
76.92 Midge,
Chlroiiomus tentans
Midge,
Chironomus sp.
69 .8 1 Brown bo 1 1 head ,
90.00
70.25
233.8
42.26
86.67
83.97
66.26
42.50
196.6
78.55
197.2
30.00
69.81
Species Mean
Acute-Chronic
Ratio
>4.473
Ictalurus nebulosus
53
-------
Table 3. (Continued)
Rank*
9
8
7
6
5
4
3
2
1
Genus Mean Species Mean
Acute Value Acute Value
(uq/L>" Species (pa/D**
56.2) Snail,
Gyraulus circumstr latus
53.08 Worm,
Limnodrllus hottmelster!
39.35 Snail,
Physa heterostropha
Snail ,
Physa inteqra
37.05 Bryozoan,
Lophopodella carter)
37.05 Bryozoan,
Plomatella etnarglnata
25.22 Amphipod,
Gawmarus pseudol Imnaeus
Amphipod,
Gammarus put ex
18.77 Cladoceran,
Cerlodaphnla retlculata
17.08 Cladoceran,
Oaphnla magna
Cladoceran,
Daphnla pulex
Cladoceran,
Daphnla pullcarla
16.74 Northern squaw fish.
56.21
55.08
35.91
43.07
37.05
37.05
22.09
28.79
18.77
2). 17
25.42
9.263
16.74
Species Mean
Acute-Chronic
Ratio
-
3.585
3.297
2.4 I8""
-
Ptychochal lus Oregon en si s
-------
Table 3. (Continued)
Rank*
20
19
18
17
16
15
14
13
12
1 1
10
Genus Maan Species Mean
Acute Value Acute Value
<,»g/t)" Species
-------
Table 3. (Continued)
Rank*
9
8
7
6
5
4
i
2
1
Genus Mean Species Mean Species Mean
Acute Value Acute Value Acute-Chronic
(uQ/L)** Species (uo/L)«* Ratio
120 Polychaete worn,
Phyllodoce maculate
69.26 American lobster,
Homanus amerlcanus
65.60 Stack aba lone,
Ha II otis cracherodll
Red aba lone,
Haliotis rufuscens
49 Ounganess crab.
Cancer magi star
i9.97 Copepod,
Acartla clausl
Copepod,
Acartla tonsa
59 Soft- shell clam,
Mya arenarla
14.92 Pact fie oyster.
Crassostrea giqas
Eastern oyster,
Crassostrea virgin lea
13.93 Simmer flounder,
Paral Ictithys dentatus
5.8 Blue mussel ,
Hyti lus edulis
120
69 .28
50
dft.08
49
52
30.72
39
7.807
28.52
13.93
5.8
56
-------
Table 3. (Continued)
* Ranked tram most resistant to most sensitive based on Genus Mean Acute Value.
" Freshwater Genus Mean Acute Values and Species Mean Acute Values are at a hardness of 50 mg/L.
•** Geometric mean of tour values In Table 2.
••••Geometric mean ot three values In Table 2.
Fresh water
Final Acute Value = 18.46 pQ/L (at a hardness of 50 mg/L)
Criterion Maximum Concentration = (18.46 ug/L) / 2 = 9.230 Mq/L (at a hardness of 50 mg/L)
Pooled Slope = 0.9422 (see Table I)
In
-------
Table 4. Toxlclty ot Copper to Aquatic Plants
Spec 1 as
Alga,
Anabaana tlos-aqua
Alga,
Anabaana varlabllls
Alga,
Anabaena strain 7120
Alga,
Anacystls nldulans
Alga,
Anklstrodesmus braunl 1
Alga,
Ch lamydomonas sp.
Alga,
Chloral la pyrenoldosa
Alga,
Chloral la pyrenoldosa
Alga,
Chloral la reqularls
Alga,
Chlorella saccharophl la
Alga,
Chloral la sp.
Alga,
Chloral la vulgar Is
Alga,
Chloral la vulgarls
Alga.
Chlorella vulqaris
Effect
FRESHHATER SPECIES
75f growth
Inhibition
Growth
Inhibition
Lag In growth
Growth
inhibl ton
Growth reduction
Growth
reduction
Lag in growth
Growth
inhibition
Lag i n growth
96- hr EC50
Photosynthes! s
Inhibited
Growth
Inhibition
96- hr IC50
33-day EC50
(growth)
Result
(pg/L)
200
100
64
100
640
8.000
1
100
20
550
6.J
200
6?
ISO
Reference
Voung 4 Lisk. 1972
Young & LUk, 1972
Laube, et al . I960
Young A Llsk, 1972
Laube, et al . 1980
Calms, et al . 1978
Steeman- Nielsen &
W 1 urn-Andersen , 1970
Steeman-Nlelsan &
Kamp-Nlelsen, 1970
Sakaguchi , et al .
1977
Rachll n, et al .
1982
Gachtar, et al .
1973
Young A Llsk, 1972
Ferard, et al . 1983
Rosko & Rachli n,
1977
58
-------
Table 4. (Continued)
Spec! as
Alga,
Chi orel la vulgarls
Alga.
Chroococcus parts
Alga,
Cyclotella meneghlnlana
Alga,
Eudorlna call torn lea
Alga,
Scenedesmus acumtnaTus
Alga,
Scenedesmus quadrlcauda
Algae,
Mixed culture
Blue green algae.
Mixed culture
Diatom,
Navlcula Incerta
Diatom,
Nltzschla llnearls
Diatom,
Nltzschla pa lea
Duckweed,
Lemna minor
Macrophyte,
El odea canadensls
Effect
50J growth
reduction
Growth
reduction
Growth
reduction
Growth
Inhibition
40% growth
reduction
Growth
reduction
Sign! t leant
reduction In
photosynthesis
50J reduction In
photosynthesis
4-day EC50
5-day EC50
Complete growth
inhlbi tlon
7 -day EC50
50t reduction in
photosynthetlc Oo
Result
-------
Table 4. (Continued)
Specie*
Eurasian wateroil 1 foi 1 ,
Myr 1 ophy 1 1 UHI splcatum
Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrum caprlcornutum
Blue alga,
Mlcrocystls aeruglnosa
Green alga,
Scenedesmus quadrlcauda
Effect
32-day EC50
(root weight)
Growth
reduction
14-day EC50
(eel 1 volume)
Inclpi ant
Inhibition
1 ncl pient
Inhlbl tlon
Result
((.9/1)
250
50
85
30
1 ,100
Reference
Stanley, 1974
Bart left, «t al.
1974
Chrlstensen, et al . 1979
Brinqmann, 1975;
Bringmann & Kuhn,
1976, I978a,b
Brinqmann & Kuhn, 1977a,
I976a.b, 1979, I980b
Alga, giant kelp,
Macrocystls pyrltera
Alga,
Thai assIosIra aestevallls
Alga,
Thai assIosIra pseudonana
Alga,
Arophldtnlum carter!
Alga,
Ollsthodlscus luteus
Alga,
Skeletonema costatum
Alga,
Nltschla closterlum
Alqa,
Scrlppsiella (aeroense
SALTWATER SPECIES
96-hr EC50 100
(photosynthesIS
Inactlvatlon)
Reduced 19
chlorophylI a
72-hr EC50 5
(growth rate)
14-day EC50 <50
(growth rate)
14-day EC50 <50
(growth rate)
14-day EC50 50
(growth rate)
96-hr EC50 33
(growth rate)
5-day EC50 5
(growth rate)
Clendenning &
North, 1959
Holllbaugh, et al. I9SO
Erlckson, 1972
Erlckson, et al.
1970
Erlckson, et al.
1970
Erlckson, et al.
1970
ftosfco A ftachJin,
1975
Saltullah, 1978
60
-------
Table 4. (Continued)
Species
Alga.
Prorocentrum IB I cans
Alga,
GymnodInIum splendens
Red alga,
Champ I a parvula
Red alga,
Champ I a parvula
Red alga,
Champ I a parvula
Red alqa,
Champ Ia parvula
Alga,
ChioreI la stlgmatophora
Alqa,
Asterlonella Japonlca
Effect
Result
(ng/L)
5-day EC50 10
(growth ratia)
5-day EC50 20
(growth rate)
Reduced tetrasporo- 4.6
phyte growth
Reduced tetraspor- 13.3
angla production
Reduced female 4.7
growth
Stopped sexual 7.3
reproduction
21-day EC50 70
(cell volume)
72-hr EC50 12.7
(growth rate)
Refer Mice
Saifullah, 1976
Salfullah, 1978
Steele & Thursby,
1983
Steele A Thursby,
1983
Steele & Thursby,
1983
Steele & Thursby,
1983
Chr Istensen, et al,
1979
Fl sher & Jones,
1981
61
-------
Species
Table 5. BfoaccuMulatlon of Copper by Aquatic Organ!SMS
Tissue
Duration Bloconcvntratlon
(days) Factor Reference
Alqa,
Chlorella regular Is
Alga.
Chroococcus parts
Astatic clam.
Cor bleu la flunlnea
Cladoceran,
Daphnla inagna
Stonet ly,
Pteronarcys call torn lea
Fathead minnow (larva),
Plmephales promelas
Blueqll 1,
Lepoml s macrochlrus
Alqa,
Puna Hal la prlmolecta
Alga,
Ounaliella tertlolecta
Alga,
Chlamydomonas sp.
Alga,
Chlorel la sal Ina
Alga,
Stlchococcus baclllarls
Alqa,
FRESHWATER SPECIES
20 hrs
10 min up
Soft tissue 28
Whole body 7.
14
30
Muscle .660
SALTWATER SECIES
25
25
25
25
25
25
2,000
to 4 ,000
17.700-
22,600
471"
203
290
1.0
153"
168"
135"
74*
156"
273*
Sakaguchl , at
1977
Les & Walker ,
Graney , et al
Winner, I984a
Nehring, 1976
Llnd, et al.
Manuscript
Benolt, 1975
Rl ley & Roth,
Riley & Rotn,
Rl ley & Roth,
Rlley & Roth,
Rl ley & Hoth,
Rlley & Roth,
al.
1984
. 1983
1971
1971
1971
1971
.1971
1971
Heniselmls vlrescens
62
-------
Table 5. (Continued)
Species
Alga,
HenIsel«Is brunescens
Alga,
01Isthodlscus luteus
Alga,
AsterloneI la Jnponlca
Alga,
Phaeodactyluro trlcornutum
Alga,
Honochrysls lutherl
Alga,
Pseudopedlnel la pyrltormls
Alga,
Heteromastlx longlflllts
Alga,
Mlcromonas squamata
Alga,
Tetraselmls tetrathele
Polychaeta worm,
Phyllodoce maculata
Polychaata worm,
Neanthes arenaceodentata
Polycbaete worm,
Nereis dlverstcolor
Polychaete worm,
Ctrrlformta spirabranchla
Polychaete worm,
EudlstylI a Vancouveri
Blue mussel,
Mytl I us edulls
Tissue
Duration Bloconcentratlon
(days) Factor Reference
25
25
25
25
25
25
25
25
25
21
28
24
24
33
309 •
323*
138"
85»
6I7«
279*
265*
l,750»
2,550»
203»
250"
1,006
14
553* Riley & Roth, 1971
182* RI ley & Roth, 1971
Rlley & Roth, 1971
Rlley i Roth, 1971
Riley & Roth, 1971
Rlley & Roth, 1971
RI ley & Roth, 1971
Rlley & Roth, 1971
Rlley & Roth, 1971
McLusky & Phil lips,
1975
Pesch & Morgan, 1978
Jones, et al. 1976
Mllanovlch, et al.
1976
Young, et al. 1979
Phillips, 1976
90
63
-------
TabU 5. (Continued)
Species
Bay scallop,
Argopecten jrradians
Bay seal lop,
Argopecten Irradlans
Eastern oyster,
Crassostrea vlrglnlca
Eastern oyster,
Crassostrea vlrglnlca
Quahog clam,
Mercenarla mercenarla
Soft-shell clam,
Mya arenarla
Tissue
Duration
(days)
112
112
140
140
70
35
Bl oconcentratlon
Factor
3,310
4,160
28,200
20,700
88
3,300
Reference
Zarooglan & Johnson,
1983
Zaroogfan 1 Johnson,
1983
Shuster & Pringle,
1969
Shuster & Pringle,
1969
Shuster & Pringle,
1968
Shuster & Pringle,
1968
•Bloconcentratlon factor was converted from dry weight to wet weight basis.
64
-------
Table 6. Oth«r Data on Effects of Copper on Aquatic Organisms
Species
Green alga,
H-6-atococcus sp ,
Green alga,
Scenedesmus quadricauda
Green alga,
Scenedesmus auadrl cauda
Alga,
Cladophora qlomerata
Diatom,
Coreonel s placentula
Phytoptankton,
Mixed species
Perlphyton,
Mixed species
Bacteria,
Escherlchla coll
Bacteria,
Pseudomonas put! da
Protozoan,
Entoslphon sulcatum
Protozoan,
Mlcroregma heterostona
Protozoan ,
Chi lomonas parameclum
Protozoan,
Uronema parduezl
Protozoa,
Mixed species
Duration
96 hrs
96 hrs
45 mln
12 mos
12 mos
124 hrs
1 yr
16 hrs
72 hrs
28 hrs
46 hrs
20 hrs
/ days
Effect
FRESHWATER SPECIES
Inhibited
growth
inclpi ent
Inhibl tlon
EC50 Inhibition of
phosphorus uptake
Suppressed
growth
Suppressed
growth
Reduced rate of
primary production
Affected species
composition; reduced
product ivl ty
Incipient
Inhibition
1 nclplent
Inhibl tion
Incipl ent
Inhibition
Incipient
inhibition
Incipient
Inhibition
Incl pi ent
Inhibl tlon
Reduced coloniza-
tion rates
Rasuit
(Mg/D
50
150"
5.1
120
120
10
2.5
80
30
110
50
3,200
140
167
Reference
Pear (mutter & Bucnneim,
1983
Brlngmann i Kuhn, !959a,t>
Peterson, et al. 1984
Weber & McFarland, 1981
Weber & McFarland, 1981
Cote, 1983
Leland & Carter, 1984,
Manuscript
Brlngmann & Kuhn, 1959a
Brlngmann & Kuhn, 1976,
1977a, 1979. I980b
Bringmann, 1978;
Brlngmann & Kuhn, 1979,
1980b, 1981
Brlngmann & Kuhn, 1959b
Brlngmann, et al. 1980,
1981
Brlngmann i Kuhn, 1960a,
1981
Cairns, et al . 1981
65
-------
Table 6. (Continued)
Spec let
Protozoa,
Mixed species
Rotifer,
Karate) la sp.
Rotifer,
Phllodlna acutlcornls
Worm,
Aeolosoma head ley)
Snail,
Gonlobasls llvescens
Snail,
Mltrocrls sp.
Snail,
Lymnaea amarglnata
Asiatic clam (adult) ,
Cor bleu la man II ens Is
Asiatic clan (adult) ,
Corblcula man II ens Is
Asiatic clam (larva),
Corblcula manllensls
Cladoceran,
Daphnla amblgua
Cladoceran,
Duration Effect
15 days Reduced coloniza-
tion rates
24 hrs EC50
48 hrs LC50 ( 5 C)
(10 C)
(15 C)
(20 C)
(25 C)
48 hrs LC50 (5 C)
(10 C)
(15 C)
(20 C)
(25 C)
46 hrs LC50
48 hrs LC50 (5 C)
(10 C)
(15 C)
(20 C)
(25 C)
48 hrs LC50
96 hrs LC50
70 days ILC
24 hrs 53. If mortal 1 ty
72 hrs LC50 (fed)
Life cycle Reduced productivity
Result
((.g/L)
100
101
1.300
1,200
1,130
1,000
950
2,600
2,300
2,000
1,650
1,000
860
3,000
2,400
1,000
300
210
300
>2,600
<10
25
67.7
49
Reference
Bulkema, et al . 1983
Borgmann & Ralph,
1984
Cairns, et al . 1978
Cairns, et al. 1978
Cairns, et al. 1976
Cal rns, et at. 1978
Cairns, et al . 1976
Harrison, et al. I98t,
1984
Harrison, et al. 1981 ,
1984
Harrison, et al . 1981 ,
1984
Ml nner & Parrel 1 ,
1976
Ml nner & Parrel 1,
Daphnla ambiqua
1976
66
-------
Table 6. (Continued)
Spec I as
Cladoceran,
Oaphnla magna
Cladoceran,
Oaphnla magna
Cladoceran,
Dophnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Result
Duration Effect (Mg/L)
16 hrs EC50 (Immobiliza-
tion)
48 hrs EC50 (ted)
(immobl llzatlon)
21 days Reproductive
Impairment
48 hrs LC50 ( 5 C)
(10 C)
(15 C)
(25 C)
Life cycle Reduced number of
young produced
72 hrs LC50
72 hrs LC50 (fed)
Life cycle Reduced productivity
Life cycle Reduced productivity
Life cycle Reduced number of
young produced
29 hrs Median survival time
48 hrs EC50
58
38
60
22
90
70
40
7
10
56-75
86.5
88.8
85
81.5
81.4
85.3
49
28.2
10
12.7
100"
Reference
Anderson, 1944
Bleslnger &
Chrlstensen, 1972
Bleslnger &
Chrlstensen, 1972
Cairns, et al . 1978
Adema & DeGroot Van
Zljl, 1972
Oebelak, 1975
Ml nner & Parrel 1,
1976
Winner 4 Farrel 1 ,
1976
Winner, et al. 1977
Winner, et al . 1977
Andrew, et al . 1977
Brlngmann & Kuhn,
1959a,b
67
-------
T«bU 6. (Continued)
Species
C i adoceran ,
Dap'hnla magnn
Cladoceran (3-9 days),
Oaphnta magna
Cladoceran (adult),
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla parvula
Cladoceran,
Oaphnta parvula
Cladoceran,
Daphnla pulex
Cladoceran,
Daphnla pulex
Cladoceran,
Daphnla pule
Cladoceran,
Daphnla pulex
Duration
24 hrs
72 hrs
72 hrs
24 hrs
48 hrs
Life cycle
48 hrs
21 days
Life cycle
72 hrs
Lite cycle
72 hrs
Life cycle
48 hrs
100 mln
Result
Effect (,g/i)
LC50 80
LC50 (10 C)
(15 C)
(25 C)
(50 C)
LC50 (30 C)
BC50
(Immobilization)
EC50 (250 (M Trls)
EC50 (1,000 WM Trls)
Reduced longevity
LC50 (fed)
LC50 (fed)
Stopped reproduction
LC50 (fed)
Reduced productivity
LC50 (fed)
Reduced productivity
LC50 ( 5 C)
(10 C)
(15 C)
(25 C)
LC50 (15 day)
delayed mortal Ity
61
70
21
9.3
0.25
70
254
1,239
60
18.5
1.4
3.2
57
72
49
54
86
49
70
60
20
5.6
200
Reference
Brlngmann 4 Kuhn,
19776
Braglnskly & Shcherban,
1978
Bragmskly & Shcherban,
1978
Be'lavere & Gorbl, 1981
Borgmann * R-lph, 1983
Winner 1981
Dave, 1984
M Inner & Parrel 1 ,
1976
Winner i parrel 1 ,
1976
M Inner & Parrel 1,
1976
Winner & parrel 1 ,
1976
Cairns, et at. 1978
Abel, 1980
68
-------
Table 6. (Continued)
Species Duration
Cladoceran, 48 hrs
Daphnla puiex
Cladoceran, 77 hrs
Daphnla pulex
Cladoceran, 48 hrs
Daohnla oultcarla
Cladoceran, 48 hrs
SlDOcaphalus serrulatus
Copepods, 7 days
Acnnthocyc 1 ops and
Olacyclops sp.
Amphlpod, 48 hrs
Gammarus fasclatus
Amphlpod, 96 hrs
Gammarus lacustrts
Crayfish, 17 days
Orconectes rust Icus
Crayfish (adult), 1,358 hrs
Effect
LC50 (fed)
LC50 (fed)
LC50 (TOC-14 »g/L)
(TOC-13 ma/L)
(TOC-13 »g/L)
(TOC-28 nq/L)
(TOC-34 mg/L)
(TOC-34 mq/L)
(TX-32 mg/L)
(TOC-32 nig/L)
(TOC«12 i»g/L)
< TOC-13 mg/L)
(TOC-28 mg/L)
(TOC-25 mg/L)
(TOC-13 mg/L)
(TOC=21 mg/L)
(TOC-34 mg/L)
LC50 (TOC-11)
(TX-12.4)
-------
Table 6. (Conf.nuad)
RMUlt
Spacljis
Mayfly,
Cloeon dlpterum
Mayfly.
Ephenerella grand) s
Mayfly.
Ephenerella subvarla
Stonef ly,
Pteronarcys cal Horn lea
Caddlsf ly,
Hydropsyche bet ten 1
Midge,
Chlronomus ten tans
Midge,
Tany tarsus dlsslmllls
Midge,
Unidentified
Coho salmon,
Oncorhynchus kl sutch
Duration
72 hrs
14 days
48 hrs
14 days
14 days
20 days
10 days
32 «ks
96 hrs
Eff«ct
LC50 (10 C)
(15 C)
(25 C)
(30 C)
LC50
LC50
LC50
LC50
EC50
LC50
Emergence
Reduced sur'
when transf<
to seawatar
R«f*r«nc«
193 Braqlnskiy & Shcherban,
95.2 1978
53
4.8
Coho salmon,
Oncorhynchus klsutch
30 days LC50
180-200 Nehring, 1976
320 Warnick & Bel I, 1969
10,100- Nehrlng, 1976
13,900
32,000 Marnlck & Bel I, 1969
77.5 Nebeker, et al. 1984a
16.3 Anderson, et al . 1980
30 Hedtke, 1984
30 Lorz & McPherson,
1976
360 Holland, et al. 1960
70
-------
Table 6. (Continued)
Species Duration
Coho salmon, 72 hrs
Oncorhynchus kl sutch
Coho salmon, 96 hrs
Oncorhynchus kl sutch
Coho salmon, 100 days
Oncorhynchus kl sutch
Coho salmon, 168 hrs
Oncorhynchus kl sutch
Coho salmon, 168 hrs
Oncorhynchus kl sutch
Sockeye salmon, 24 hrs
Oncorhynchus nerka
Chinook salmon, 72 hrs
Oncorhynchus tshawytscha 5 days
Chinook salmon, 26 days
Oncorhynchus tshawytscha
Chinook salmon (alevln), 200 hrs
Oncorhynchus tshawytscha
Chinook salmon (swim-up), 200 hrs
Oncorhynchus tshawytscha
Chinook salmon (parr), 200 hrs
Oncorhynchus tshawytscha
Effect
LC50
LC50 (TOC=7.3)
Reduced growth
rate
LC50
LC50 (acclimated to
copper tor 2 wks)
Significant change
In cor tl coster lod
LC50
LC50
Reduced survival and
growth of sac fry
LC50
LCIO
LC50
LCIO
LC50
LCIO
Result
(Mg/D
280
370
190
480
440
460
480
560
780
510
520
480
286
70
275
325-440
64
190
178
21
20
15
19
14
30
17
Reference
Hoi land, et al . I960
Buckley, 1983
Buckley, et al . 1982
McCarter 1 Roch, 1983
McCarter 4 Roch, 1983
Donaldson 4 Dye, 1975
Hoi land, et al . 1960
Hazel & Mel th, 1970
Chapman, 1978
Chapman, 1978
Chapman, 1978
71
-------
Table 6. (Continued)
Result
Specie*
Chinook salwon (smolt),
Oncorhynchus tshawytscha
Rainbow trout.
Sal mo galrdnerl
DuratIon
Effect
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Sal mo gal rdner I
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Salnto galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout (alevln),
Salmo galrdnerl
Rainbow trout (swim-up),
SaImo galrdnarI
Rainbow trout (parr),
SoImo galrdnarI
Rainbow trout (smolt).
Sal mo gal rdner I
Rainbow trout (smolt),
Salmo galrdnerI
Rainbow trout (smolt),
Salmo galrdnerI
200 Urs
% hrs
2 hrs
7 days
21 days
10 days
7 days
200 hrs
200 hrs
200 hrs
200 hrs
96 hrs
>10 days
LC50
LCIO
LC50
Depressed
response
LC50
ol factory
Median period of
survl val
Depressed
rate and
feeding
growth
Median, period ot
survl vat
LC50
CCIO
LC50
LCIO
LC50
LCIO
LC50
LCIO
LC50
Threshold
LC50
26
16
17
9
15
8
21
7
Reference
Chapman, 1973
516" Howarth & Sprague,
309" 1976
I II"
8 Kara, et al. 1976
44 Lloyd, 1961
40 Grande, 1966
75 Lett, et al. 1976
44 Lloyd, 1961
26 Chapman, 1978
19
Chapman, 1978
Chapman, 1978
Chapman. 197B
14 days
LC50
102*" Fogels & Sprague.
94" 1977
870 Calamarl &Marchettl,
1975
72
-------
Table 6. (Continued)
Species
Rainbow trout (fry),
Salmo qalrdnerl
Rainbow trout (fry),
Salmo qalrdnerl
Rainbow trout (fry),
Saloo qalrdnerl
Rainbow trout ( fry),
Salmo qalrdnerl
Rainbow trout
(embryo, larva),
Salmo qalrdnarl
Rainbow trout
(embryo, larva),
SaliBQ galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout (fry),
Salmo qalrdnerl
Rainbow trout (fry),
Salmo qalrdnerI
Rainbow trout (fry),
Salmo qalrdnerl
Rainbow trout,
Sat mo qalrdnerl
Result
Duration
I hr
24 hrs
Effect
Avoidance
LC50 (5 C)
(15 C)
(50 C)
0.1
950
450
150
Reference
Folmar, 1976
Cairns, et al. 1978;
96 hrs
48 hrs
80 rain
96 hrs
IC50
LC50 (field)
28 days EC50 (death and
detorwl ty)
28 days EC 10 (death and
deformity)
Avoidance
threshold
LC50
24 hrs LC50
72 hrs LC50
>I5 days Threshold LC50
250-680 Lett, et al. 1976
70 Calamari &Marchettl,
1975
110 Blrge, et al. 1980,
Blrge & Black, 1979
16.5 Blrge, et al. I98J
74 Black & airge, 1980
250 Goettl, et al. 1972
140 Shaw & Brown, 1974
110
580
19
54
48
78
18
96
Brown, et al. 1974
Miller & McKay, 1980
73
-------
TabU 6. (Continued)
Species Duration
Rainbow trout, 48 hrs
Salmo qalrdnerl
Rainbow trout, 48 hrs
Sal»o galrdnerl
Rainbow trout, 48 hrs
Sal»o galrdnerl
Rainbow trout, 72 hrs
Salpo galrdnerl
Rainbow trout, 48 hrs
Salmo galrdnerl
Rainbow trout, 4 mos
Salmo galrdnerl
Rainbow trout, 96 hrs
SalMO galrdnerl
Rainbow trout, 96 hrs
Salmo galrdnerl
Rainbow trout, 144 hrs
Sal»o galrdnerl
Rainbow trout, 144 hrs
Salmo galrdnerl
Rainbow trout, 144 hrs
Salmo galrdnerl
Rainbow trout,
Satmo galrdnerl
Rainbow trout (embryo), 96 hrs
Salmo galrdnerl
Rainbow trout, 96 hrs
Sal mo qalrdnerl
Effect
Result
(pg/L) Reference
LC50
LC50
LC50
LC50
LC50
Biochemical and
enzyme levels
LC50
LC50
500
Brown, 1968
750 Brown & Da I ton, 1970
150 Cope, 1966
1,100 Lloyd, 1961
270 Herbert & Vandyke,
1964
30 Arl I lo, et al. 1984
185 BIMs, et al. 1981
160 Daoust, 1981
LC50 (various diets) 246-408 Dlxon & Hilton, 1981
Incipient lethal
level
Incipient lethal
level '(aceI (mated
at 131-194 Mg/L)
Avoi dance
LC50
274-381 Dlxon i Sprague, I981a
564-717 Dlxon & Sprague, 1981a
6.4 Glattina, et al. 1982
400 Giles & Klaverkamp,
1982
LC50 (various diets) 11.3- Marking, et al. 1984
23.9
74
-------
TabU 6. (Continued)
Species
Rainbow trout,
Sal no galrdnerl
Rainbow trout.
Sal mo qalrdnerl
Atlantic salmon.
Sal mo salar
Atlantic salmon.
Sal mo salar
Atlantic salmon,
Sal mo salar
Atlantic salmon,
Sal mo salar
Brown trout,
Sal mo trutta
Brook trout,
Salvellnus tontlnalls
Brook trout,
Salvellnus fontlnalis
Brook trout,
Salvellnus fontlnalls
Longtin dace,
Agrosla chrysogaster
Central stoneroller,
Campos toma anomalum
Goldfish,
Carasslus auratus
Goldfish (embryo, larva),
Carasslus auratus
Duration
85 days
85 days
7 days
7 days
21 days
27-38 hrs
21 days
24 hrs
21 days
357 days
96 hrs
96 hrs
24 hrs
7 days
Result
E f tact (jig/t)
Reduced growth 31
(continuous exposure)
Reduced growth (Inter- 16
ml ttent exposure)
Incipient lethal 48
level
Incipient lethal 32
leva!
Median survival 40
time
Median survival 50
time
Median survival 45
time
Significant change 9
1 n cough rate
Significant changes 23
In blood chemistry
Significant changes 17.4
In blood chemistry
LC50 860**
LC50 (high BOO) 1,400
LC50 (5 C) 2,700
(ISC) 2,900
(30 C) 1,510
EC50 (death and 5,200
da form! ty)
R«twenc*
Selm, et al. 1984
Seim, et at. 19d4
Sprague, 1964
Sprague & Ramsay,
1965
Grande, 1966
Zltko 4 Carson, 1976
Grande, 1966
Orummond, et al . 1973
McKIm, et al . 1970
McKIra, et al. 1970
Lewis, 1970
Geckler, et al . 1976
Cairns, et al . 1978;
Blrge, 1978; Blrge &
Black, 1979
75
-------
Table 6. (Continued)
Spectes
Common carp (embryo),
Cyprlnut carplo
Common carp,
Cyprlnui carpio
Common carp (embryo),
Cyprlnus carplo
Go I dan shiner,
Notemlgonus crysoleucas
Striped shiner,
Notropls chrysocephalus
Striped shiner,
Notropls chrysocephales
Bluntnose minnow,
Plaephales notatus
Bluntnose Minnow,
Plmepnales notatut
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales prontalns
Fathead minnow,
Plmephalas promelas
Fathead minnow,
Plmaphalea promalas
Duration
72 hrs
48 hrs
-
24 hrs
96 hrs
96 hrs
48 hrs
96 hrs
96 hrs
Life cycle
96 hrs
96 hrs
96 hrs
Effect
Prevented
hatching
LC50
EC50 (hatch)
LC50 (5 C)
(15 C)
(30 C)
LC50 (high BOO)
Decrease blood
osmo 1 ar 1 ty
LC50 (21 tests)
(high BOO)
LC50 (6 tests)
(high BOO)
LC50 (21 tests)
high BOD)
Chronic 1 Imlts
(high BOO)
LC50 (36 tests)
(high BOD)
LC50 (7 tests)
(high BOD)
LC50
Result
(utt/U
700
170
4,775
330
230
270
8,400
16,000
3,400
4,000
5,000
2.500
750-
21.000
1,100-
20.000
1,610-
21,000
66-
120
<650-
23,000
740-
13,000
231
Reference
HI Idobrand A Cusnman,
1978
Harrison A Rice, 1981
4,775 Kapur & Yadv, 1982
Cairns, et al. 1978;
Geckler, et al. 1976
Lewis A Lewis, 1971
Geckler, et al. 1976
Geckler, et al. 1976
Brungs, et al. 1976
Brungs, et al. 1976
Geckler, et al. 1976
Gec'itAr, •'.- al. 1976
Curtis, et al. 1979;
Curtis & ward, 1981
.'6
-------
Table 6. (Continued)
Species
Fathead minnow,
Plmephales prone las
Fathead minnow,
Plmephales promelas
Creek chub,
Semotl lus atromnculatus
Pearl dace,
Semotl lus margarlta
Brown but (head,
Ictalurus nebulosus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Flaqf Ish,
Jordanella florldae
Duration Effect
96 hrs LC50 (TOC 12 mg/L)
(TOG 13 mq/L)
(TOG 36 mg/L)
(TOC 28 mq/L)
(TOC 15 mq/L)
1 TOC 34 mq/L)
(TOG 30 mg/L)
(TOC JO mg/L)
96 hrs LC50 U.ish from
pond contaml nated
with heavy metals)
96 hrs LC50
(high 1300)
7 hrs Overturning and
death
96 hrs LC50
(high BOO)
94 hrs Decreased blood
osmolarlty
24 hrs LC50 (5 C)
(15 C)
(30 C>
Increased
alblnl SKI
10 days EC50 (death and
detorml ty)
14 days LC50
96 hrs LC50
10 days LC50
Result
(n9/LI
436
516
1,586
1 ,129
550
1,001
2,050
2,336
360
410
11,500
1,100
1,010-
279,000
11,000
2,500
3,700
2,600
3,100
0.5
6,620
1,200"
1,270""
680"
Reference
Llnd, et al .
Manuscript
Blrge, et al. 1983
Geckler. et al. 1976
Tsal, 1979
Geckler, et al. 1976
Lewis 1 Lewis, 1971
Cairns, et al. 1978;
Mesterman & Birge,
1970
Blrge & Slack, 1979
Rlchey and Roseboom,
19 7B
Fogels & Spraque,
1977
77
-------
TabU 6. (Continued)
Result
Specie*
Duration
Effect
Reference
Mosqultotlsh,
Gambusia afflnls
Guppy,
Poecl lla retlculata
Guppy,
Poecl lla retlculata
Rock bass,
Ambloplltes rupestrls
Bluegl II,
Lepoml s macrochirus
Bluegl 1 1,
Lepoml s macrochlrus
Bluegl 1 1,
Lepoml s macrochirus
eiueglll,
Lepoml s nacrochlrus
Bluegl II,
Lepoml s macrochirus
Bluegl II,
Lepoml s macrochirus
Bluegl II,
Lepomls macrocftirus
Blueglll.
Lepomls wacrochlrus
Bluegl II,
Lepomls macrochirus
Larqemouth bass
(embryo, larva),
Hlcropterus salmoldes
96 hrs
24 hrs
48 hrs
96 hrs
24-36 hrs
48 hrs
24 hrs
96 hrs
14 days
96 hrs
96 hrs
BO mln
96 hrs
b days
LCM) (high
turbldl ty)
LCt.0
LC50
LC50
(high TOC)
Altered oxygen
consumption rates
LC50
LC50 (5 C)
(15 C>
(30 C)
LC50
(high BOD)
LC50
LC50
LCt>0
Avoidance
threshold
Biochemical
changes
EC50 (death and
detormi ty)
75 ,000
1,250
2,500
1,432
300
2,800
2,590
2.500
3,820
16.000
17,000
2,500"
3.700«»
740
1,800
8,480
2,000
6,560
Mai len, et al. 1957
Hlnlcuccl, 1971
Khangarot, et al .
I98la
Llnd, et al .
Manuscript
O'Hara, 1971
Cope, 1966
Cairns, et al . 1978;
Geckler. at al. 1976
Rlchey & Roseboom,
1978
Trama. 1954
Turnbul I, et al. 1954
Black & Blrge, 1980
Heath, 1984
Blrqe, et al. 1978;
Birge & Black. 1979
78
-------
Table 6. (Continued)
Species Duration
Largemouth bass, 24 hrs
Mlcropterus salmoIdes
Rainbow darter, 96 hrs
Etheostoma caeruleum
johnny darter, 96 hrs
Etheostoma nlqrum
Orangethroat darter, 96 hrs
Etheostoma spectablle
Leopard frog 8 days
(embryo, larva),
Rana pi pi ens
Narrow-mouthed toad 7 days
(embryo, larva),
Gastrophryne carol Inensls
American toad, 80 mln
Bufo amerlcanus
Fowler's toad 7 mln
(embryo, larva),
Buto fowler I
Southern gray tree frog 7 ml n
(embryo, larva),
Hyla chrysoscells
Marbled salamander 8 days
(embryo, larva),
Ambystoma opacum
Effect
Affected oper-
cular rhythm
LC50
(high BOO)
LC50
(high BOD)
LC50
(high BOD)
EC50 (death and
defomil ty)
ECt>0 (death and
deform!ty)
Avoidance
threshold
EC50 (death and
deformity)
EC50 (death and
deformity)
EC50 (death and
deformity)
Result
(nq/l) Reference
48 Morgan, 1979
4,500
5,900
2,800
6.800
9,800
7,900
5,400
5,800
50
40
100
Geckler, et al. 1976
Geckler, et al. 1976
Geckler, et al. 1976
Btrge & Black, 1979
Blrge, 1978; Blrge A
Black, 1979
Black & Birge, 1980
26,960 Blrge & Black, 1979
40 Blrge & Black, 1979
770 Blrge, et al. 1978;
Blrge & Black, 1979
79
-------
TabU 6. (Continual
Resuit
Duration Effect
SALTWATER SPECIES
Natural phytoplonktoo
popu!at Ions
Natural phytop lanktoo
populations
Alga,
LaminarI a hyperborla
Hydro)d,
Campanularla flexuosa
Hydrold,
Campanularla flexuosa
Hydromedusa,
Phlalldlum sp.
Ctenophore,
Pleurobrachla pilaus
Ctenophore.
Mn ami ops Is mccrdayl
Rotifer,
Bracnlonus pllcatllls
Polychaete norm,
Phyllodoce maculata
Polychaete worm,
Neanthes arenaceodentata
Polychaete norm,
Neanthes arenaceodentata
Polychaete worm,
Neanthes arenaceodentata
Polychaete worm,
Neanthes arenaceodentata
5 days
4 days
28 days
11 days
-
24 hrs
24 hrs
24 hrs
24 hrs
9 days
28 days
28 days
7 days
10 days
Reduced
chlorophy 1 I a
Reduced blomass
Growth
Growth
Inhlbi
Enzyme
LC50
LC50
LCbO
LC50
LC50
LC50
LC50
LC50
LC50
decrease
rate
tion
Inhibition
19 Holllbaugh, et al.
!98Q
6,4 tto! Mbaugh. at a),
1980
50 Hopkins 4 Kaln, 1971
10-13 Stebblnq, 1976
1.43 Moore & Stebblng,
1976
36 Reeva, et al . 1976
33 Reeve, et al. 1976
1976
17-29 Reeve, et al . 1976
100 Reave, et al. 1976
80 HcLusky & Phil lips,
1975
44 Pesch & Morgan, 1978
100 Pesch & Morgan, 1978
137 Pesch & Hoffman, 1982
98 Pasch i Hoffman, 1982
80
-------
Table 6. (Continued)
Species
Polychaete worn,
Neanthes orenaceodentata
Polychaete worm.
Cirri torn la splrabranchia
Larval annelids.
Mixed species
Black abalone.
Ha 1 1 01 1 s cracherod 1 1
Red abalone,
Hal I otls rutescens
Channeled whelk.
Busy con canal Iculatuw
Mud snal I,
Nassarlus obsoletus
Blue mussel ,
My t II us edulf s
Bay seal lop,
Arqopecten Irradlans
Bay seal lop,
Arqopecten Irradians
Eastern oyster ( larva) ,
Crassostrea virgin lea
Common ranqia,
Rang I a cuneata
Clam,
Macoma Inquinata
Clam,
Macoma Inquinata
Quahoq clam (larva).
Duration
28 days
26 days
24 hrs
96 hrs
96 hrs
77 days
72 hrs
7 days
42 days
H9 days
12 days
96 hrs
30 days
30 ddys
8-lU days
Result
Effect (|ig/l)
LC50 56
LC50 40
LC50 89
Hlstopathologlcal >32
ql 1 1 abnormal i tl es
Hlstopatholoqlcal >32
gill abnormal 1 ties
LC50 470
Decrease In oxygen 100
consumption
LC50 200
EC50 (growth) 5.8
100* mortality 5
LC50 46
LC50 (
-------
Tab I* 6. (ContlniMd)
RMult
Specie*
Duration
Effect
Qua hog clam (larva),
Mercenarla marcenarla
Common Pacific llttleneck,
Protothaca stamlnea
Soft-shell clam,
Mya arenarla
Copepod,
Undlnula vulgar Is
Copepod ,
Euchaeta marina
Copepod ,
Metrldla pact flea
Copepod,
Labldocera scottl
Copepod ,
Acartla clausl
Copepod,
Acartla tonsa
Copepod,
Acartla tonsa
Copepod,
Tlsbe holothurlae
Copepod (naupllus),
Mixed species
Amphlpod,
Awpellsca abdlta
Euphausl Id,
Euphausla pad t lea
Grass shrimp,
Pa 1 aemonetes puqlo
Coon stripe shrimp.
77 days
17 days
7 days
24 hrs
24 hrs
24 hrs
24 hrs
48 hrs
6 days
24 hrs
48 hrs
24 hrs
7 days
24 hrs
96 hrs
30 days
LC50
LC50
LC50
LC50
LC50
IC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LCt>0
Reference
25 Shuster & PrIngle,
1968
39 Roesljadl, 1980
Elsler, 1977
192
90
Reeve, et al . 1976
188 Reave, et al. 1976
176 Reave, et al . 1976
132 Reeve, et al. 1976
34-82 Moraltou-
Apostolopoulou, 1978
9-73 Sosnowskl, et al.
1979
104-311 Reeve, et al. 1976
80 Moral tou-Apostolopoulou
& Verrlopoulos, 1982
90 Reeve, et al. 1976
Scott, et al. Manuscript
Pandalus danaa
14-30 Reave, et al . 1976
12.600 Curtis, et al. 1979;
Curtis 4 Ward, 1981
27.0 Crocellus, et at.
1982
82
-------
Table 6. (Continued)
Species
American lobster,
Homarus amerlcanus
Sea urchin,
Arbacla punctulata
Arrow worm,
Sagltta hlsplda
Atlantic menhaden,
Brevoortla tyrannus
Pacific herring (embryo),
Clupea harengus pallasl
Pacific herring (larva),
Clupea harengus pallasl
Atlantic cod (embryo),
Gadus morhua
Munmlcnog,
Fundulus heteroclltus
Mummlchog,
Fundulus heteroclltus
Atlantic si Iverslde,
Menldla menldla
Pinf ish,
Lagodon rhomboldes
Spot.
Lelostomus xanthurus
Atlantic croaker,
Ouratl on
13 days
24 hrs
14 days
6 days
48 hrs
14 days
21 days
96 hrs
96 hrs
14 days
14 days
14 days
Effect
LC50
58< decrease In
sperm root! 1 i ty
LC50
LC50
Incipient LC50
Incipient LC50
LC50
HI stopathologlcal
lesions
Enzyme Inhibition
HI stopatho logical
lesions
LC50
LC50
LC50
Result
(pq/L)
56
300
43-460
610
33
900
10
<500
600
<500
150
160
210
Reference
McLeese, 1974
Young & Nelson, 1974
Reeve, et al . 1976
Engel, et al . 1976
Rice & Harrl son,
1978
Rice & Harrison,
1978
Swedmark & Granmo,
1981
Gardner & La Roche,
1973
Jacklm, 1973
Gardner & LaRoche,
1973
Engel, et al . 1976
Engel, et al. 1976
Engel, et al . 1976
Mlcropogonlas undulatus
83
-------
Table 6. (Continued)
Result
Specie* Duration Effect (ng/L) Reference
Winter flounder, 14 days HI stopathologlcal 180 Baker, 1969
Pseudop I euronectes lesions
amerlcanus
* In river water.
••Dissolved copper; no other measurement reported.
84
-------
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