Draft
11/4/85
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
NICKEL
NOTE: This draft contains only freshwater data. The saltwater data
will be incorporated later. The freshwater CCC is likely
to change when the saltwater data are incorporated.
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
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NOTICES
This document has been reviewed by the Criteria and Standards Division,
Office of Water Regulations and Standards, U.S. Environmental Protection
Agency, and approved for publication.
Mention of trade names or commerciil products does apt constitute
endorsement or recommendation for use.
This document is available to the public through the 'National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
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ACKNOWLEDGMENTS
Loren J. Larson
Judy L. Crane
(freshwater authors)
University of Wisconsin-Superior
Superior, Wisconsin
Jeff Hyland
(saltwater author)
Environmental Research Laboratory
Narragansett, Rhode Island
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluth. Minnesota
David J. Hansen
(saltwater coordinator)
Environmental Research Laboratory
Narragansett, Rhode Island
Clerical Support:
Terry L. Highland
Shelley A. Heintz
IV
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CONTENTS
Foreword iii
Acknowledgments iv
Tables vi
Introduction ,
Acute Toxicity to Aquatic Animals
Chronic Toxicity to Aquatic Animals
Bioaccumulation .
Other Data
Unused Data
Summary
National Criteria ,
References
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TABLES
1. Acute Toxicity of Nickel to Aquatic Animals
2. Chronic Toxicity of Nickel To Aquatic Animals
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios
4. Toxicity of Nickel to Aquatic Plants
5. Bioaccumulation of Nickel by Aquatic Organisms
6. Other Data on Effects of Nickel on Aquatic Organisms ....
VI
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Introduction*
Nickel is one of the most common of the heavy metals occurring in
surface waters. In a survey of 969 waters in the U.S., McCabe et al.
(1970) reported detectable (> 1 jJg/L) nickel concentrations in 78% of
samples taken. Although nickel can exist in oxidation states of -1, 0.
+1, +2, +3, and +4, under usual conditions in surface waters the divalent
cation greatly predominates, and is generally considered the most toxic.
Water chemistry parameters influencing oxidation state, toxicity and
availability of the total nickel pool include pH, hardness, and presence
of complexing and adsorbing agents such as humic acids.
Natural sources of ambient nickel concentrations in aquatic systems
include degradation of parent material within the immediate basin, inflow
of allochthonous particulate nickel and nickel dissolved in precipitation.
Cultural increases in nickel concentrations can be produced by industries,
such as electroplating and smelting, and by the burning of coal and other
fossil fuels. Fly ash can contain as much as 1,000 Mg/L (Swaine 1980).
Lake restoration projects have experimented with fly ash as a floe to
precipitate dissolved nutrients. No information is available on
toxicological significance of metals leaching from the fly ash. Studies-
reporting ambient nickel concentrations in surface waters include Forstner
(1984), Hutchinson et al. (1975), Trollope and Evans (1976), Mathis and
Cummings (1973) and Solbe (1973). Of 1577 samples taken, Kopp and Kroner
* An understanding of the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses"
(Stephan et al. 1985), hereafter referred to as the Guidelines, is necessary
in order to understand the following text, tables, and calculations.
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(1969) reported those containing nickel averaged 19 >Jg/L with the maximum
concentration of 130 tJg/L in the Cuyahoga River in Ohio.
Because of the variety of forms of nickel (Callahan et al. 1979:
Niragu 1980) and lack of definitive information about their relative
toxicities. no available analytical measurement is known to be ideal for
expressing aquatic life criteria for nickel. Previous aquatic life
criteria for nickel (U.S. EPA 1980) were expressed in terms of total
recoverable nickel (U.S. EPA 1983a), but this measurement is probably too
rigorous in some situations. Acid-soluble nickel (operationally defined
as the nickel that passes through a 0.45 pirn membrane filter'after the
sample is acidified to pH = 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 nickel to, and bioaccumulation of nickel by,
aquatic organisms. No test results were rejected just because it was
likely that they would have been substantially different if they had
been reported in terras of acid-soluble nickel. For example, results
reported in terms of dissolved nickel would not have been used if the
concentration of precipitated nickel was substantial.
2. On samples of ambient water, measurement of acid-soluble nickel
should measure all forms of nickel that are toxic to aquatic life or
can be readily converted to toxic forms under natural conditions. In
addition, This measurement should not measure several forms, such as
nickel that is occluded in minerals, clays, and sand or is strongly
sorbed to particulate matter, that are not toxic and are not likely
to become toxic under natural conditions. Although this measurement
(and raanv others) will measure soluble, complexed forms of nickel,
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such as the EDTA complex of nickel, that probably have low toxicities
to aquatic life, concentrations of these forms probably are negligible
in most ambient water.
3. Although water quality criteria apply to ambient water, the measurement
used to express criteria is likely to be used to measure nickel in aqueous
effluents. Measurement of acid-soluble nickel should be applicable to
effluents because it will measure precipitates, such as carbonate and
hydroxide precipitates of nickel, that might exist in an effluent and
dissolve when the effluent is diluted with receiving water. If. desired,
dilution of effluent with receiving water before measurement of
acid-soluble nickel might be used to determine whether the receiving water
can decrease the concentration of acid-soluble nickel because of sorption.
4. The acid-soluble measurement should be useful for most metals, thus
minimizing the number of samples and procedures that are necessary.
5. The acid-soluble measurement does not require filtration at the time
of collection, as does the dissolved measurement.
6. The only treatment required at the time of collection is preservation
by acidification to pH = 1.5 to 2.0, similar to that required for the
total recoverable measurement.
7. Durations of 10 minutes to 24 hours between acidification and filtration
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 = 4.9 (Weber and Stumm 1963).
9. Differences in pH within the range of 1.5 to 2.0 probably will not
affect the result sustantially.
10. The acid-soluble measurement does not require a digestion step, as does
the total recoverable measurement.
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11. After acidification and filtration of the sample to isolate the acid-
soluble nickel, the analysis can be performed using either atomic
absorption spectroscopy or ICP-atomic emission spectroscopy (U.S. EPA
1983a), as with the total recoverable measurement.
Thus, expressing aquatic life criteria for nickel in terms of the acid-
soluble measurement has both toxicological and practical advantages. On
the other hand, because no measurement is known to be ideal for expressing
aquatic life criteria for nickel or for measuring nickel in ambient water
or aqueous effluents, measurement of both acid-soluble nickel and total
recoverable nickel in ambient water or effluent or both might be useful.
For example, there might be cause for concern if total recoverable nickel
is much above an applicable limit, even though acid-soluble nickel is
below the limit.
Unless otherwise noted, all concentrations reported herein are expected
to be essentially equivalent to acid-soluble nickel concentrations. All
concentrations are expressed as nickel, not as the chemical tested. The
criteria presented herein supersede previous aquatic life water quality
criteria for nickel (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 no't 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 this
document was conducted in February, 1985; some newer information was also
used.
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Acute Toxicity to Aquatic Animals
Mechanisms of nickel toxicity are varied and complex (Mushak 1980),
and as with other heavy metals, significant effects occur at cell membranes
and membranous tissues, such as gills. In fish, hematological effects
such as hyperglycemia, hepatic gylcogenolysis, lymphopenia, and erythrocytosis
have been reported in association with nickel intoxication (Agrawal et
al. 1979; Chaudhry 1984; Gill and Pant 1981).
The data base used to derive freshwater criterion for nickel (Table 1)
contains LCSOs for 21 species representing 15 families and 6 classes.
These species perform a range of ecological functions and occupy a variety
of freshwater habitats.
Lind et al. (manuscript) conducted studies with Daphnia pulicaria and
fathead minnows, on the relationship of both hardness and TOC with LC50
(Table 6). With both organisms, hardness was the only significantly
correlated parameter. Nebeker et al. (1985) reported an increase in
toxicity to nickel in 3 month to 12 month old rainbow trout. Rehwoldt et
al. (1973) observed a decrease in toxicity with age when comparing embryo
to adult snails. One of the most sensitive vertebrate species is the
narrow-mouthed toad. In 7 day tests, embryo and larva ECSOs were 50 >Jg/L
(Table 5). Embryo and larva EC50 for the marbled salamander was 410-420
(jg/L in 8 day tests (Birge and Black 1980; Birge et al. 1978). Seven day
EC50 for the channel catfish was 710 ug/L (Birge and Black 1980; Birge et
al. 1981). LC50 at 48 hrs for this fish was 36,840 ,jg/L (Willford 1966).
Different species exhibit different sensitivities to nickel, and many
other factors might affect the results of tests of the toxicity of nickel
to aquatic organisms. Criteria can quantitatively take into account such
a factor, however, only if enough data are available to show that the
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factor similarly affects the results of tests with a variety of species.
Hardness is often thought of as having a major effect on the toxicity of
nickel, although the observed effect is probably due to one or more of a
number of usually interrelated ions, such as hydroxide, carbonate, calcium,
and magnesium. Hardness is used here as a surrogate for the ions which
affect the results of toxicity tests on nickel. 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 four species for
which acute values are available over a range of hardness such that the
highest hardness is at least three times the lowest and the highest is
also at least 100 mg/L higher than the lowest. The slopes for all four
species are between 0.69 and 1.19 (see end of Table 1) and are close to the
slope of 1.0 that is expected on the basis that nickel, calcium, magnesium,
and carbonate all have a charge of two. An F-test showed that, under the
assumption of equality of slopes, the probability of obtaining four slopes
as dissimilar as these is P = 0.18. This was interpreted as indicating
that it is not unreasonable to assume that the slopes for the four species
are the same.
The pooled slope of 0.8478 was used with the data in Table 1 to
normalize the acute values to a hardness of 50 mg/L, where possible and
to calculate Species Mean Acute Values at a hardness of 50 mg/L. Genus
Mean Acute Values (Table 3) were then calculated as geometric means of
the available freshwater Species Mean Acute Values. Of the eighteen
genera for which acute values are available, the most sensitive genus,
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Daphnia, was 29 times more sensitive than the most resistant, Fundulus.
The freshwater Final Acute Value of 1,576.4 pg/L was calculated at a
hardness of 50 mg/L from the Genus Mean Acute Values in Table 3 using the
procedure described in the Guidelines. Thus, the freshwater Criterion
Maximum Concentration (in |Jg/L) = e(0.8478[In(hardness)1+3.353)^
Chronic Toxicity to Aquatic Animals
Represented in the data base on chronic toxicity of nickel to aquatic
animals (Table 2) are a cladoceran, a caddisfly, and two species of fish.
Comparison of chronic values within a small range of hardness values (51-
54 mg/L), the caddisfly is the most tolerant of chronic levels of nickel
(chronic value = 128.4 jJg/L) , Daphnia magna is the least tolerant (chronic
value = 14.77). and chronic effects in early life-stage rainbow trout
were reported at the lowest concentration tested, 35 |Jg/L. In hard water,
(205 to 210 mg/L) the fathead minnow was more tolerant of chronic nickel
exposure than Daphnia magna by a factor of almost 1.5.
The direct influence of hardness on chronic toxicity of nickel was
investigated by Chapman et al. (manuscript). Using Daphnia magna in life
cycle tests, they observed a decrease in chronic toxicity to nickel with
increased water hardness. Least squares regression of ln[hardness] and
ln[chronic value] produces a slope of 2.32 (cqrrelation = 0.986). Acute
LCSOs from measured studies with E>. magna (Table 1) were regressed in a
similar manner. [Note: this regression is not equal to the regression
used in calculation of Species Mean Acute Values]. Geometric means of
hardness and LCSQs were used in 2 sets of data with closely comparable
hardnesses (51.1 and 51. mg/L, and 100. and 104. mg/L) to represent these
points. Slope of the resulting regression line was 0.97 (correlation =
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0.990). This would suggest that although hardness has a strong effect on
acute toxicity in D. magna, its influence on chronic toxicity is greater.
Final Acute-Chronic Ratio was calculated to be 32.03 by the geometric
mean of the five acute-chronic ratios (Table 2). Division of Final ,Acute
Value by the Final Acute-Chronic Ratio results in a Final Chronic Value
of 24.608 pg/L (hardness * 50 mg/L). Assuming equality of slopes in
regressions of acute and chronic toxicities, the Final Chronic Equation
for nickel is e(0.8478[ln(hardness)J-0.1135).
Toxicity j^o Aquatic Plantg
Data on the toxicity of nickel to aquatic plants are found in Table 4.
Nickel concentrations resulting in a 40-60% reduction in algal growth
range from 50 jJg/L for a green algae, Scenedesmus acuminatz, to 5,000 pg/L
for the green algae, Ankistrodesmus falcatus and Chlorococcum. Because
hardness is often unspecified, direct comparison of toxicity data on
Table 4 is not advised. Wang and Wood (1984) indicate that resistance to
nickel in plants is also pH dependent. General comparison of Table 4
data with chronic toxicity data (Table 2) suggests that nickel concentrations
high enough to produce chronic effects in aquatic animals will also have
deteriorative effects on algal populations.
Studies by Patrick et al. (1975) cite a decrease in diatom diversity
and a shift to green and blue-green algae as a community effect of nickel
exposure. Their findings are in agreement a field study by Spencer and
Greene (1981) where an increase in blue-green algae was observed. Using
EDTA to manipulate Ni+^ concentrations, Spencer and Nichols (1983) reported
algal growth to be inversely related to free divalent nickel and independent
of total nickel concentrations.
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Brown and Rattigan (1979) studied nickel toxicity in two higher
aquatic plants, duck weed and Elodea (Anacha_r_is_). Despite the presence
of a thick cuticle, which protects it from many chemical agents (e.g.,
herbicides), duck weed was much more susceptible to nickel than was
Elodea.
Bioaccumulation
Data on bioaccumulation of nickel by aquatic organisms are found in
Table 5. Data are available for an alga, a cladoceran, and two species
of fish. The lowest BCF/BAF, 0.8, is for the rainbow trout where only the
muscle tissue is analyzed. All other studies whe&& conducted, on whole
body samples and BCF/BAF1s range from 9.3 for the alga to 193 for the
cladoceran. Lind et al. (manuscript) observed a decrease in BCF/BAF with
increased water concentration of nickel in a fathead minnow for the same
duration. This* same trend is observed im 'studies -with Daphnia* magtta
(Hall 1982).
Hall (1982) discussed the uptake of various' tissues in DAphara.
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Other Data
Data on Table 6 suggest a high toxicity to nickel in the single-celled
organisms. Bringmann and Kuhn (1959a. b; 1977a; 1979; 1980a, b; 1981)
have reported concentrations resulting in incipient inhibition (defined
variously, such as a 3% change in growth) for algae, bacteria, and
protozoans. Although incipient inhibition of growth may at times be
statistically significant, its ecological significance is unknown. Babich
and Stotzky (1983) observed delayed effects after a 24 hr exposure.
Although citing the effects of nickel, algal, bacterial, and protozoan
data appearing in Table 6 are not directly comparable to other data.
Willford (1966) reported 48 hr LC50 in 6 species (3 families) of
fishes tested in the same water. Although fish differed in size, neither
this nor taxonomic differences produced a clear trend in relative toxicity.
Blaylock and Frank (1979) observed LC50s for a carp larva at 3 days and
10.5 days to be 8,460 and 750 >Jg/L, respectively.
Shaw and Brown (1971) tested the effect of nickel on laboratory
fertilization of rainbow trout eggs. They report no statistically
significant effect at 1000 jjg/L (hardness = 260-280), and also note a
stimulation in development after fertilization compared to controls.
Several studies have investigated associated effects of nickel intox-
ication. See et al. (1975) studied the effect on photoresponse in a planarian.
Whitley and Sikora (1970) and Brkovic-Popovic and Popovic (1977) studied
effects on respiration in tubificid worms. Influence of nickel on thermal
resistance in salmonids is examined by Becker and Wolford (1980). Effect
of complexing agents on nickel toxicity in a carp are studied by Muramoto
(1983). Smith-Sonneborm et al. (1983) studied the toxicity of ingested
nickel dust particles in Paramecium. Although they do not cite data,
10
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Anderson and Weber (1975) derive an expression relating body size to
toxicity in the guppy.
In a field study, Havas and Hutchinson (1982) worked with acidified
and control ponds. They suggest the presence of heavy metal stress
(including nickel), caused by increased mobilization of these materials,
in the resident aquatic invertebrates, with decreased pH.
Unused Data
Some data on the effects of nickel on aquatic organisms were not used
because the studies were conducted with species not resident in North
America (Baudouin and Scoppa 1974; Khangarot et al. 1982; Sexana and
Parashari 1983; Van Hoof and Nauwelaers 1984; Verma et al. 1981). Data
were also not used if nickel was a component of a mixture (Besser 1985;
Anderson 1983: Hutchinson and Sprague 1981; Markarian et al. 1980; Muska
1978; Stratton and Corke 1979b; Wong et al. 1978; Wong et al. 1982).
Babich and Stotzky (1985), Birge and Black (1980), Phillip and Russo
(1978), Rai et al. (1981), and U.S. EPA (1978) only present data that
have been published elsewhere. Studies reporting no data or data in an
unusable form for deriving criterion include Braginsky and Scheherban
(1978). Jones (1939). Muska and Weber (1977a. b) Scheherban (1977),
Whitton and Shehata (1982). Brown (1968) provided an inadequate description
of experimental procedures.
Results of some laboratory tests were not used because the tests were
conducted in distilled or deionized water without addition of appropriate
salts (e.g., Buikema et al. 1973, 1974; Jones 1935; Shaw and Grushkin
1957) or were conducted in chlorinated or "tap" water (e.g., Grande and
Andersen 1983). Dilution waters in studies by Stratton and Corke (1979a)
and Mann and Fyfe (1984) contained excessive amounts of EDTA.
11
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Bringmann and Kuhn (1982) cultured Daphnia magna in one water and
conducted tests in another. Tests conducted with too few test organisms
(e.g., Tarzwell and Henderson 1960; Applegate et al. 1957) were not used.
Results of laboratory bioconcentration tests were not used if steady-state
was not demonstrated (e.g., Stokes 1975; Gerhards and Weller 1977).
Summary
Acute values for twenty-one species in 18 genera range from 1.101
jjg/L for a cladoceran to 43,240 Mg/L for a fish. Twelve of these values
are for fish, and there appears to be no clear taxonomic or size relationship
correlating relative toxicity. Water hardness appears to be significantly
correlated to observed LC50 values.
Chronic toxicity to nickel occurs at a concentration as low as 14.8
[jg/L for Daphnia magna in soft water. Chronic value increases to 356.6
{jg/L for I), magna in hard water. Of all organisms tested, fathead minnows
are the most tolerant of chronic nickel intoxication with a value of
526.7 (Jg/L. Final acute-chronic ratio is 32.03.
Nickel appears to be quite toxic to freshwater algae, with concentrations
as low as 50 pg/L producing significant inhibition. Bioconcentration
factors for nickel range from 0.8 for fish muscle to 193 for a cladoceran.
with a median factor of 40.3.
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
12
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(in yg/L) of nickel does not exceed the numerical value given by
e(0.8478[ln(hardness)j-0.1135) more than once every three years on the
average and if the one-hour average concentration (in ug/L) does not
exceed the numerical value given by e(0.8478 [In(hardness)J+3.353)
more than once every three years on the average. For example, at hardnesses
of 50, 100, and 200 mg/L as CaCC>3 the four-day average concentrations of
nickel are 25, 42, and 80 Mg/L, respectively, and the one-hour average
concentrations are 788, 1418, and 2553 ug/L.
EPA believes that a measurement such as "acid-soluble" would provide a
more scientifically correct basis upon which to establish criteria for
metals. The criteria were developed on this basis. However, at this
time, no EPA approved methods for such a measurement are available to
implement the criteria through the regulatory programs of the Agency and
the States. The Agency is considering development and approval of methods
for a measurement such as "acid-soluble." Until available, however, EPA
recommends applying the criteria using the total recoverable method.
This has two impacts: (1) certain species of some metals cannot be
analyzed directly because the total recoverable method does not distinguish
between individual oxidation states, and (2) these criteria may be overLy
protective when based on the total recoverable method.
The allowed excursion frequency of three years is based on the Agency's
best scientific judgment of the average amount of time it will take an
aquatic ecosystem to recover from a pollution event in which exposure to
nickel exceeds the criterion. The resilience of ecosystems and their
ability to recover differ greatly, however, and site-specific criteria
may be established if adequate justification is provided.
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The use of criteria in designing waste treatment facilities requires
selection of an appropriate wasteload allocation model. Dynamic models
are preferred for the application of these criteria. Limited data or other
factors may make their use impractical, in which case one must rely on a
steady-state model. The Agency recommends interim use of 1Q10 for
Criterion Maximum Concentration (CMC) design flow and 7Q10 for the
Criterion Continuous Concentration (CCC) design flow in steady-state
models. These matters are discussed in more detail in the Techncial Support
Document for Water Quality-Based Toxics Control (U.S. EPA 1985) and the
Design Flow Manual (U.S. EPA 1986).
14
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Table 1. Acute Toxlctty of Nickel to Aquatic Animals
Spec 1 es
Worm,
Nals sp.
Snal 1 (embryo) ,
Amnlcola sp.
Snail (adult).
Amnlcola sp.
Cladoceran,
Daphnla maqna
Cladoceran,
Daphn la maqna
Cladoceran,
Daphnla magna
Cladoceran,
Daphn la maqna
Cladoceran,
Daphn la magna
Cladoceran,
Daphnla magna
Cladoceran,
D*phnla magna
Cladoceran,
Daphnla pul Icarla
Cladoceran,
Daphnla pul 1 carlo
Cladoceran,
Daphnla pullcarla
Method*
s.
s,
s,
s,
s.
s.
s,
s.
s,
s,
s,
s,
s,
M
M
M
U
U
M
M
M
M
M
M
M
M
Chemical
Nickel
chloride
Nickel
chloride
Nickel
nitrate
Nickel
chloride
Nickel
chloride
"Nickel
chloride
Nickel
chloride
Nickel
sulfate
Nickel
sul fate
Nickel
sul fate
Hardness LC50
(mg/L as or EC50
CaCOj) (Mg/L)»»
FRESHWATER SPECIES
50 14,100
50 1 1 ,400
50 14,300
<317
45.3 510
51.1 915
51 1,800
100 2,360
104 1 ,920
206 4,970
48 2,182
48 1,8)3
44 1 ,836
Adjusted
LC50 or EC50
(ug/L)*""
14,100
11,400
14,300
554.5
998.3
1,770
1,311
1,032
1,496
2,259
1,877
2,046
Species Mean
Acute Value
((iq/L)««"» Reference
14,100 Rehwoldt et at.
Rehwoldt et al .
12,770 Rehwoldt et al.
Anderson 1948
Bleslnger and
Chrlstensen 1972
Cat 1 et al. 1983
- Chapman et al .
Manuscript
Chapman et al .
Manuscript-
Chapman et al .
Manuscript
1,101 Chapman et al.
Manuscript
Llnd et al .
Manuscript
Llnd et al .
Manuscript
Llnd et al .
Manuscript
1973
1973
1973
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Table 1. (Continued)
Species
Cladoceran,
Daphnla pul Icarla
Amphlpod,
Gammarus sp.
Mayfly,
Ephemerel la subvarla
Damsel fly,
Unidentified sp.
Stonef ly ,
Acroneurla lycorlas
Caddlsf ly,
Unidentified sp.
American eel,
Anqul 1 la rostrata
American eel,
Angullla rostrata
Rainbow trout (2 mos),
Salmo galrdnerl
Rainbow trout (Juvenile),
Salmo galrdnerl
Rainbow trout (Juvenile),
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo qalrdnerl
Method*
S, M
S, M
S, U
S, M
S, U
S, M
S, M
S, M
F, M
F, M
F, M
F, M
F, M
F, M
Chemical
Nickel
sulfate
Nickel
sulfate
Nickel
sulfate
Nickel
nl trate
Nickel
nitrate
Nickel
sulfate
Nickel
sulfate
Nickel
sulfate
Nickel
sul fate
Nickel
sul fate
Hardness LC50
(mg/L as or EC50
CoCOj)
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Table 1. (continued)
Species Method*
Rainbow trout (juvenile), F, M
Salmo galrdnerl
Rainbow trout (juvenile), F, M
Salmo galrdnerl
Rainbow trout (juvenile), F, M
Salmo gafrdner I
Rainbow trout (3 mos), F, M
Salmo galrdner 1
Rainbow trout (3 mos), F, M
Salmo galrdnerl
Rainbow trout (12 mos), F, M
Salmo galrdner 1
Rainbow trout (12 mos), F, M
Salmo galrdnerl
Goldfish (1-2 g), S, U
Carasslus auratus
Common carp (<20 on), S, M
Cypr Inus carplo
Common carp, S, M
Cypr Inus carplo
Fathead minnow, F, M
Plmephales promelas
Fathead minnow, F, M
Plmephales promelas
Fathead minnow (Immature), S, U
Plmephales promelas
Fathead minnow ( Immature) , S, M
Plmephales promelas
Chemical
Nickel
sulfate
Nickel
sulfate
Nickel
sulfate
Nickel
chloride
Nickel
chloride
Nickel
chloride
Nickel
chloride
Nickel
chlor Ide
Nickel
nitrate
-
Nickel
sul fate
Nickel
sul fate
Nickel
chloride
Nickel
ch lor Ide
Hardness
(mg/L as
CaC05)
27-
39
27-
39
27-
39
27-
39
20
53
55
45
44
210
210
LC50
or EC50
(Mg/L)»*
15,900t
II.SOO1"
11,100t
10,000
10,900
8,900
8,100
9,820
lo.eoo1"
10,400
5,209
5,163
27,000
32,200
Adjusted
LC50 or EC50
(Mg/L)»"»
14,220
15,500
12,660
11,520
21,350
10,090
9,593
5,696
5,754
7,998
9,538
Species Mean
Acute Value
(wq/L)»«*» Reference
Anderson 1981
Anderson 1981
Anderson 1981
Nebeker et al .
Nebeker et al .
Nebeker et al .
13,390 Nebeker ef al.
21,350 Pickering and
Henderson 1966
Rehwoldt ot al.
1971
9,838 Rehwoldt et al .
1972
Llnd et al .
Manuscript
Llnd et al.
Manuscr 1 pt
Pickering 1974
Pickering 1974
1985
1985
1985
1985
-------
Table 1. (continued)
Species
Fathead minnow (Immature),
Plmephales promelas
Fathead minnow (Immature),
Plmephales promelas
Fathead minnow (1-2 g) ,
Plmephales promelas
Fathead minnow (1-2 g) ,
Plmephales promelas
Fathead minnow (1-2 g) ,
Plmephales promelas
Fathead minnow (1-2 g) ,
Plmephales promelas
Banded kllllflsh «20 cm),
Fundulus dlaphanus
Banded kllllflsh,
Fundulus dlaphanus
Guppy (6 mo) ,
Poecl 1 la retlculata
White perch «20 cm) ,
Morone amerlcana
White perch,
Morone amerlcana
Striped bass ( finger 1 Ing) ,
Morone saxatllls
Striped bass,
Morone saxatllls
Striped bass (63 day),
Morone saxatllls
Method*
F,
F,
s.
s.
s.
s,
s,
s,
s,
s,
s,
s,
s,
s,
M
M
U
U
U
U
M
M
U
M
M
M
M
U
Chemical
Nickel
chloride
Nickel
chloride
Nickel
chlor Ide
Nickel
chloride
Nickel
ch lor I'de
Nickel
chlor Ide
Nickel
nitrate
Nickel
chlor Ide
Nickel
nitrate
Nickel
nl trate
Nickel
chloride
Hardness
(mg/L as
CoC03)
210
210
20
20
360
360
53
55
20
53
55
53
55
40
LC50
or EC50
(pg/L)««
28
25
5
4
42
44
46
46
4
13
13
6
6
3
,000
,000
,180
,580
,400
,500
,200f
,100
,450
,600f
,700
,200f
,300
,900
Adjusted
LC50 or EC50
((ig/L>"»
9
7
11
9
7
8
43
42
9
12
12
5
5
4
,294
,405
,260
,960
,953
,347
,970
,520
,677
,940
,640
,901
,811
,712
Species Mean
Acute Value
(iiq/L)*11"" Reference
Pickering
Pickering
Pickering
Henderson
Pickering
Henderson
Pickering
Henderson
8,051 Pickering
Henderson
Rehwoldt
1971
43,240 Rehwoldt
1972
9,677 Pickering
Henderson
Rehwoldt
1971
12,790 Rehwoldt
1972
Rehwoldt
1971
Rehwoldt
1972
Palawskl
1974
1974
and
1966
and
1966
and
1966
and
1966
et al .
et al .
and
1966
et al .
et al .
et al .
et al .
et al .
-------
Table 1. (continued)
Species
Striped bass (63 day),
Morone saxatl 1 Is
Rock bass,
Amb 1 op 1 1 tes rupestr I s
Pumpklnseed (<20 cm).
Lepomls glbbosus
Pumpklnseed,
Lepomls glbbosus
Blueglll (1-2 g) ,
Lepomls macrochlrus
Blueglll (1-2 g) ,
Lepomls macrochlrus
Blueglll (1-2 g) ,
Lepomls macrochlrus
Method*
S, U
F, M
S, M
S, M
S, U
S, U
S, U
Chemical
Nickel
chloride
Nickel
sul fate
Nickel
nitrate
_
Nickel
chlor Ide
>,.„•„,
: :e
Nickel
chlor Ide
Hardness LC50 Adjusted
(mg/L as or EC50 LC50 or EC50
CaCOv) (|iq/L>M* (pq/L)"1"1
285 33,000 7,545
26 2,480 4,317
53 8,100f 7,710
55 8,000 7,379
20 5,180 11,260
20 5,360 11,660
360 39,600 7,428
Species Mean
Acute Value
(iig/L)»»"" Reference
5,909 Palawskl et al. 1985
4,317 Llnd et al .
Manuscr Ipt
Rehwoldt et al .
1971
7,542 Rehwoldt et al.
1972
Pickering and
Henderson 1966
Pickering and
Henderson 1966
9,917 Pickering and
Henderson 1966
* S = static, R = renewal, F = flow-through, M = measured, U = unmeasured.
** Results are expressed as nickel, not as the chemical.
*** Freshwater LC50s and ECSOs were adjusted to hardness = 50 mg/L using the pooled slope of 0.8478 (see text).
««»« freshwater Species Mean Acute Values are calculated at hardness = 50 mg/L.
' In river water.
-------
Table 1. (continued)
Results of Covarlonce Analysis of Freshwater Acute Toxlctty versus Hardness
Species
Daphnla magna
Fathead minnow
Striped bass
Bluegl II
All of above
n
6
10
4
3
23
Slope
1.1810
0.8294
1.0459
0.6978
0.8478
95Jf Confidence Limits Degrees of Freedom
0.3185,
0.6755,
0.7874,
0.5678,
0.6669
2.0434
0.9833
1.3045
0.8279
0.9999
4
8
2
1
18
P = 0.18 for equality of slopes.
-------
Table 2. Chronic Toxlclty of Nickel to Aquatic Animals
Species
Test*
Chemical
Hardness
(mg/L as
CaCOO
Limits
Chronic Value
(»ig/L)** Reference
FRESHWATER SPECIES
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Caddlsf ly,
CMstoronla magnlflca
Rainbow trout,
Salmo galrdnerl
Fathead minnow,
Plmep hales promelas
Fathead minnow,
Plmephales promelas
* LC = 1 Ife-cycle or
LC
LC
LC
LC
ELS
LC
ELS
partial llfjs-cycle
** Results are expressed as nickel, not
*** Unacceptable effects occurred at all
Nickel
chloride
Nickel
chl or Ide
Nickel
chloride
•Nickel
chloride
Nickel
chloride
Nickel
chloride
Nickel
sul fate
; ELS = early II
as the chemical.
51
105
205
54
53
210
-
fe-stage.
10.2-
21.4
101-
150
220-
578
66-
250
380-
730
108.9-
433.5
14.77 Chapman et al.
Manuscript
123.1 Chapman et al.
Manuscript
356.6 Chapman et al.
Manuscript
128.4 Nebeker et al. 1984
<35 Nebeker et al. 1985
526.7 Pickering 1974
217.3 Llnd et al.
Manuscript
concentrations tested.
Results of Regression Analysis
Species
Daphnla magna
n Slo
of Freshwater Chronic Toxlclty
pe 95)C Confidence Limits
3 2.29 0.6666,
4.4444
versus Hardness
Degrees of Freedom
1
-------
Table 2. (Continued)
Acute-Chronic Ratio
Species
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Oaphnla magna
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Hardness
(mg/L as
CaCOx)
51
104-
105
205-
206
210
44-
45
Acute Value
1,800
1,920
4,970
27,930*
s.ise"11
Chronic Value
(i>g/l)
14.7
123.1
356.6
526.7
217.3
Ratio
122.4
15.60
13.94
53.03
23.87
* Geometric mean of four values In Table 1.
** Geometric mean of two values In Table 1.
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
Rank*
18
17
16
15
14
13
12
It
10
9
8
7
6
Genus Mean
Acute Value
(iiq/L)
43,240
40,480
30,200
21 ,350
21,200
14,100
13,390
13,000
W12,770
12,180
9,838
9,677
8,693
Species
Banded kl 1 1 If 1st),
Fundulus dlaphanls
Stonef ly,
Acroneurla lycortas
Caddlsfly,
Unidentified sp.
Goldfish,
Carasslus auratus
Oomsetf ly,
Unidentified sp.
Worm,
Nals sp.
Rainbow trout,
Salmo galrdnerl
Amph Ipod,
Gammarus sp.
Snail,
Amnlcola sp.
Amer lean eel ,
Anqul 1 la rostrata
Common carp,
Cyprlnus carplo
Guppy,
Poecllla rettculata
White perch,
Morone amerlcana
Striped bass,
Species Mean
Acute Value
(Mq/L)"
43,240
40,480
30,200
21,350
21,200
14,100
13,390
13,000
12,770
12,180
9,838
9,677
12,790
5,909
Species Mean
Acute-Chronic
Ratio*"
Morone saxatlI Is
-------
Table 3. (Continued)
Rank*
5
4
3
2
1
Genus Mean
Acute Value
(gq/L)
8,648
8,051
4,637
4,317
1,499
Species
Blueglll,
Lepomls macrochlrus
Pumpklnseed,
Lepomls qlbbosus
Fathead minnow,
Plmephales promelas
Mayfly,
Ephemeral la subvarla
Rock bass,
Ambloplltes rupestrls
Cladoceran,
Oaphnla pul (car la
Cladoceran,
Daphn la maqna
Species Mean
Acute Value
dig/D**
9,917
7,542
8,051
4,637
4,317
2,042
1,101
Species Mean
Acute-Chronic
Ratl6««»
35.6
29.9
* Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
»» From fable 1.
*•* From table 2.
Fresh water
Final Acute Value » 1,576.4 ug/L (at a hardness of 50 mg/L)
Crl**rlon Maximum Concentration = (1,576.4 »q/\.Yfy/ 2 » 788.2 ug/%fct a
hardness of 50 mg/L)
Pooled Slope = 0.8478 (see Table 1)
In (Criterion Maximum Intercept) » In (788.2) - (slope x lnW))l
» 6.6698 - (0.8478 x 3.9120*..» 3.353
Criterion Maximum Equation = e<0.8478l In(hardness) I + 3.353)
£lnal Acute-Chronic Ratio » 32.03 (aee text)
FlnW*.Chronlc Value = (1,576.4 Mq/L) / 32.03 - 24.61 pg/L (at ha*»*ess of 50 mg/L)
FlnSl'Chronlc Equation = e'0*847^! In(hardness)l-0.1l35)
-------
Table 4. Toxic Ity of Nickel to Aquatic Plants
Species
Blue-green alga,
Anabaena flos- aquae
Blue-green alga,
Hlcrocystls aeruglnosa
Green alga,
Anklstrodesmus falcatus
Green alga,
Anklstrodesmus falcatus
Green alga,
Anklstrodesmus falcatus
var. aclcularls
Green alga,
Chlamydomonas eugametos
Green alga,
Chi ore! la vulqarls
Green alga,
Chlorococcum sp.
Green alga,
Haematococcus capensls
Green alga,
Pedlastrum tetras
Green alga,
Scenedesmus acumlnata
Chemical
Nickel
nitrate
Nickel
chloride
Nickel
chloride
Nickel
nitrate
Nickel
nitrate
Nickel nitrate or
Nickel sulfate
Nickel nitrate or
Nickel sulfate
Nickel
chloride
Nickel nitrate or
Nickel sulfate
Nickel
nitrate
Nickel nitrate or
Nickel sulfate
Hardness
(mg/L as Duration
CaCX»5>_ (days)
FRESHWATER SPECIES
14
8
10
14
14
47.5 12
47.5 12
10
47.5 12
14
47.5 12
Effect
84$ reduction
1 n growth
Incipient
Inhibition
45$ reduction
In growth
98$ reduction
In growth
42* reduction
In growth
91$ reduction
In growth
53$ reduction
In growth
52$ reduction
In growth
85)1 reduction
In growth
Increased
growth
54$ reduction
In growth
Result
(ug/L)«
600
5
5,000
100
100
700»»
300»»
5,000
300»»
100
50"
Reference
Spencer and Greene
1981
Brlnqmann and Kuhn
1978a,b
Devi Prasad and
Devi Prasad 1982
Spencer and Greene
1981
Spencer and Greene
1981
Hutch Inson 1973
Hutch Inson and
Stokes 1975
Hutch Inson 1973;
Hutch Inson and
Stokes 1975
Devi Prasad and
Devi Prasad 1982
Hutch Inson 1973;
Hutch Inson and
Stokes 1975
Spencer and Greene
1981
Hutch Inson 1973;
Hutch Inson and
-------
Table 4. (Continued)
Spectes
Green alga,
Scenedesmus acumlnata
Green alqa,
Scenedesmus dlmorphus
Green alqa,
Scenedesmus obllquus
Green alga,
Scenedesmus quadrlcauda
Green alqa,
Scenedesmus quadrlcauda
Alga (metal-tolerant strain),
Scenedesmus acutlformIs
Diatom,
Mavlcula pelllculosa
Duckweed,
Lemna minor
Chemical
Nickel nitrate or
Nickel sulfate
Macrophyte,
El odea (Anacharls) canadensls
Nickel
nitrate
Nickel
chloride
Nickel
chloride
Nickel
nitrate
Nickel
nitrate
Nickel
chIor Ide
Nickel
chloride
Hardness
(mg/L as
CaC03)
47.5
49.8
14.96
Duration
(days)
13
14
10
8
14
6
14
28
28
Effect
Reduced
growth
30? reduction
In growth
47? reduction
In growth
Incipient
Inhibition
EC50
EC50
Result
(pg/L)»
500
100
3,000
1,500
60% reduction 100
In growth
50? reduction 1,171»«
In growth
82? reduction 100
In growth
340
2,800
Reference
Stokes et a). 1973;
Hutchlnson and
Stokes 1975
Spencer and Greene
1981
Devi Prasad and
Devi Prasad 1982
Brlngmann and Kuhn
1977a; 1978a,b;
1979; 1980b
Spencer and Greene
1981
Stokes 1975
Fezy et al. 1979
Brown and Rattlgan
1979
Brown and Rattlgan
1979
* Results are expressed as nickel, not as the chemical.
** Estimated from graph.
-------
Table 5. Btoaccutnulaton of Nickel by Aquatic Organisms
Species
Chemical
Concentration
In Hater (pq/D*
Hardness
-------
Table 6. Other Data on Effects of Nickel on Aquatic Organisms
Species
Hardness
dng/L as
Chemical CaCOT)
Resu 1 t
Duration Effect (uq/D*
Reference
FRESHWATER SPECIES
Green alga,
Scenedesmus quadrlcauda
Green alga,
Scenedesmus quadrlcauda
Alga,
(mixed population)
Bacter 1 urn,
Aeromonas sobrla
Bacterium,
Bacl 1 lus brevls
Bacterium,
Bacl 1 lus cereus
Bacterium,
Escherlchla col 1
Bacterium,
Escherlchla col 1
Bacterium,
Pseudomonas putlda
Bacterium,
Serratla marcescens
Protozoan,
Entoslphon sulcatum
Protozoan,
Mlcroreqma heterostoma
Nickel
chloride
Nickel
ammon lum
sul fate
Nickel 87-
nltrate 99
Nickel 40
chloride
Nickel 40
chloride
Nickel 40
chloride
Nickel
chloride
Nickel
ammon lum
sul fate
Nickel
chlor Ide
Nickel 40
chloride
Nickel
chloride
Nickel
chloride
96 hrs Incipient 1,500
Inhibition
(river water)
96 hrs Incipient 900
Inhibition
(river water)
<53 days Decrease In 2-
dlatom diversity; 8.6
shift to qreen and
blue-qreen algae
24 hrs** Reduction In 5
abundance
24 hrs** Reduction In 5
abundance
24 hrs** Reduction In 5
abundance
Incipient 100
Inhibition
Incipient 100
Inhibition
16 hrs Incipient 2.5
Inhibition (3.0)
24 hrs** Reduction In 10
abundance
72 hrs Incipient 140
Inhibition
28 hrs Incipient 50
Inhibition
Brlngmann and Kuhn
1959a,b
Brlngmann and Kuhn
1959a,b
Patrick et al . 1975
Bablch and Stotzky
1983
Bablch and Stotzky
1983
Bablch and Stotzky
1983
Brlngmann and Kuhn
1959a
Brlngmann and Kuhn
1959a
Brlngmann and Kuhn
1977a; 1979; 1980b
Bablch and Stotzky
1983
Brlngmann 1978;
Brlngmann and Kuhn
1979; 1980b; 1981
Brlngmann and Kuhn
1959b
-------
Table 6. (Continued)
Species
Protozoan,
Mlcroreqma heterostoma
Protozoan,
Chi lomonas parameclum
Protozoan,
Uronema parduezl
Tubl field worm,
Tublfex tublfex
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla maqna
Cladoceran,
Daphnla maqna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla maqna
Cladoceran,
Daphnla pul Icarla
Cladoceran,
Daphnla pul Icarla
Cladoceran,
Daphnla pul Icarla
Hardness
(mg/L as
Chemical CnCOj)
Nickel
ammon lum
sul fate
Nickel
chloride
Nickel
chloride
Nickel 34.2
sulfate
Nickel
chloride
Nickel
ammon 1 urn
sul fate
Nickel 288
chloride
Nickel 45.3
Chloride
Nickel 45.3
chloride
Nickel 45.3
chlor Ide
Nickel 25
sutfate
Nickel 28
sul fate
Nickel 28
sul fate
Duration
28 hrs
48 hrs
20 hrs
48 hr
48 hrs
48 hrs
24 hrs
48 hrs
21 days
21 days
48 hrs
48 hrs
48 hrs
Effect
Incipient
Inhibition
Incipient
Inhibition
Incipient
Inhibition
LC50
EC50 (river
water)
EC50 (river
water)
EC50
(swimming)
EC50 ( Immobll-
zatlon) (fed)
EC50 (Immobll-
zatlon)
16? reproduc-
tive Impairment
LC50 (TOC =
39 mg/L)
LC50 (TOC =
15 mg/L)
LC50 (TOC =
13 mg/L)
Result
(ufl/L>*
70
820
42
8.70
7.00
6,000
6,000
11,000
1,120
130
30
2,171
1,140
1,034
Reference
Brlngmann and Kuhn
1959b
Brlngmann et al . 1980;
Brlngmann and Kuhn
1981
Brlngmann and Kuhn
1980a, 1981
Brkovlc-Popovlc and
Popov Ic 1977a
Brlngmann and Kuhn
I959a,b
Brlngmann and Kuhn
I959a,b
Brlngmann and Kuhn
1977b
Bleslnger and
Chrlstensen 1972
Bleslnger and
Chrlstensen 1972
Bleslnger and
Chrlstensen 1972
Llnd et al . Manuscript
Llnd et al . Manuscript
Llnd et al. Manuscript
-------
Table 6. (Continued)
Species
Cladoceran,
Daphnla put Icarla
Cl adoceran,
Oophnla pu 1 Icarla
Cladoceran,
Daphnla pul Icarla
Cladoceran,
Oaphnla pul Icarla
Cladoceran,
Daphnla pul lean la
Cladoceran,
Oaphnla pul Icarla
Cladoceran,
Dapnnla pullcarla
Cladoceran,
Daphnla pul Icarla
Cladoceran,
Oaphnla pul Icarla
Cladoceran,
Oaphnla pul Icarla
Mldqe,
Chlronomus sp.
Coho salmon (year line)),
Oncorhynchus klsutch
Rainbow trout (0.5-0,9 g) ,
Salmo qalrdnert
Rainbow trout (1 yr) ,
Salmo qalrdnerl
Chemical
Nickel
sul fata
Nickel
sul fate
Nickel
sul fata
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
chloride
Nickel
sul fate
Nickel
su 1 fate
Hardness
(mg/L as
CaCOT>
29
73
74
84
86
89
89
100
1 14
120
50
90
42
240
Duration
48 hrs
48 hrs
48 hrs
48 hrs
48 hrs
48 hrs
48 hrs
48 hrs
48 hrs
48 hrs
96 hrs
144 hrs
48 hrs
48 hrs
Effect
UC50 (TOC =
13 mg/L)
LC50 (TOC =
28 mq/L)
LC50 (TOC =
28 mq/L)
LC50 (TOC =
32 mq/L)
LC50 (TOC =
34 mq/L)
LC50 (TOC =
18 mq/L)
LC50 (TOC =
34 mq/L)
LC50 (TOC =
34 mq/L)
LC50 (TOC =
27 mg/L)
LC50 (TOC =
33 mq/L)
LC50
100$ survival
LC50
LC50
Result
(ug/L)«
697
3,414
2,325
3,014
3,316
2,042
2,717
3,757
3,156
3,607
8,600
5,000
35,730
32,000
Reference
Llnd et at. Manuscript
Llnd et al. Manuscript
Llnd et al. Manuscript
Llnd et al. Manuscript
Llnd et al. Manuscript
Llnd et al. Manuscript
Llnd et al. Manuscript
Llnd et al. Manuscript
Llnd et al. Manuscript
Llnd et al. Manuscript
Rehwoldt et al . 1973
Lorz et al . 1978
Wll Iford 1966
3rown and Dal ton 1970
-------
Table 6. (Continued)
Species
Rainbow trout
(embryo, 1 arva) ,
Salmo galrdnerl
Rainbow trout (embryo),
Salmo galrdnerl
Rainbow trout
(embryo, larva),
Salmo galrdnerl
Rainbow trout
(embryo, larva),
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout (adult),
Salmo galrdner 1
Rainbow trout (10 g),
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Brown trout (0.8-1.2 g) ,
Salmo trutta
Brook trout (0.4-0.6 g) ,
Salvellnus fontlnalls
Lake trout (2.5-3.2 g) ,
Salvellnus namaycush
Goldfish,
Carasslus auratus
Goldfish (embryo, larva),
Carasslus auratus
Chemical
Nickel
chloride
Nickel
chloride
Nickel
chlor Ide
Nickel
sulfate
Nickel
chlor Ide
Nickel
chl or Ide
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
chlor Ide
Nickel
chloride
Hardness
(mg/L as
CaCO,)
104
(92-110)
104
125
174
240
320
28.4
22.5
42
42
42
195
Duration
28 days
28 days
28 days
28 days
3.5 days
6 mos
20 mlns
48 hr
48 hrs
48 hrs
48 hrs
19-50 hrs
200-210 hrs
7 days
Effect
EC50 (death
and deform! ty)
LC50
EC50 (death
and deformity)
EC50 (death
and deformity)
Decreased gill
dl f f us Ion
Increase In
1 Iver proteoly-
tlc activity of
males
Avoidance
threshold
LC50
LC50
LC50
LC50
LT
IT
EC50 (death
and deformity)
Result
(pq/L)»
50
50
60
90
2,000
1,000
23.9
54,963
60,290
54,040
16,750
100,000
10,000
2,140
Reference
Blrge 1978; Blrge and
1980; Blrqe et at . 1978,
1980, 1981
Blrge et al . 1979
Blrge et al . 1981
Blrge et al . 1981
Hughes et al. 1979
Aril lo et al. 1982
Glattlna et al. 1982
Bornatowlcz 1983
Wll Iford 1966
Wll Iford 1966
Wll Iford 1966
Ellis 1937
Blrge 1978
-------
Table 6. (Continued)
Species
Goldfish (embryo, larva),
Carasslus auratus
Common carp (embryo),
Cyprlnus carplo
Common carp (larva),
Cyprlnus carplo
Common carp (embryo),
Cyprlnus carplo
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Channel catfish (1.2-1.5 g) ,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Guppy,
Poecl 1 la rotlculata
Guppy (184 mg) ,
Poec II 1 a ret 1 cu 1 ata
Chemical
Nickel
chloride
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sul fate
Nickel
sulfate
Nickel
sulfate
Nickel
su 1 fate
Nickel
sul fate
Nickel
chlor Ide
Nickel
sul fate
Nickel
chlor Ide
Hardness
(mg/L as
CaOH)
93-
105
128
128
360
28
29
77
86
89
91
42
93-
105
260
260
Duration
7 days
72 hrs
72 hrs
257 hrs
-
96 hrs
96 hrs
96 hrs
96 hrs
96 hrs
96 hrs
48 hrs
7 days
96 hrs
48 hrs
Effect
EC50 (death
and deformity)
LC50
LC50
EC50 (hatch)
LC50 (TOC =
14 mg/L)
LC50 (TOC =
12 mg/L)
LC50 (TOC =
32 mg/L)
LC50 (TOC =
15 mg/L)
LC50 (TOC =
33 mg/L)
LC50 (TOC =
30 mg/L)
LC50
EC50 (death
and deformity)
LC50 (high
sol Ids)
LC50
Result
(xg/L)«
2,780
6,100
8,460
750
22,000
2,923
2,916
12,356
5,383
17,678
8,617
36.840
710
34,900
37,000
Reference
Blrqe and Black 1980;
Blrge et al . 1981
Blaylock and Frank
1979
Blaylock and Frank
1979
Kapur and Yadov 1982
Llnd et al . Manuscript
Llnd et al . Manuscript
Llnd et al . Manuscript
Llnd et al. Manuscript
Llnd et al . Manuscript
Llnd et al . Manuscript
Wll Iford 1966
Blrge and Black 1980;
Blrge et al . 1981
Khangarot 1981
Khangarot et al . 1981
-------
Table 6. (Continued)
Species
Blueqlll (0.7-1.1 g),
Lepomts macrochlrus
Largemouth bass
(embryo, larva),
Mlcropterus salmoldes
Narrow-mouthed toad
(embryo, larva),
Gastrophryne carol Inensls
Narrow-mouthed toad
(embryo, larva),
Gastrophryne carol Inensls
Fowler's toad,
Bufo fowlerl
Marbled salamander
(embryo, larva),
Ambystoma opacum
Chemical
Nickel
sulfate
Nickel
chloride
Nickel
chloride
Nickel
chloride
Nickel
chloride
Nickel
chloride
Hardness
-------
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