r/EFft
United States
Environmental Protection
Agency
Office of Water
Regulations and Standards
Criteria and Standards Division
Washington, DC 20460
EPA-440/5-87-003
February 1987
Water
Ambient
t
Water Quality
Criteria for
Zinc - 1987
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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
ZINC
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
US. Environmental Faction Agency
Reaion 5, Library (PL-12J) Roo.
77 West Jackson Boulevard, 12th HOOf
Chicago, 1L 60604-3590
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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 commercial products does not 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.
NTIS Number: PB 87 153581
L L
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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 water quality criteria that accurately reflect the latest
scientific knowledge on the kind and extent of all identifiable effects
on health and welfare that might be expected from the presence of pollutants
in any body of water, including ground water. This document is a revision
of proposed criteria based upon consideration of comments received from
other Federal agencies, State agencies, special interest groups, and
individual scientists. Criteria contained in this document replace
any previously published EPA aquatic life criteria for the same pollutant(s)
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.
Criteria presented in this document are such scientific assessments. If
water quality criteria associated with specific stream uses are adopted
by a State as water quality standards under section 303, they become
enforceable maximum acceptable pollutant concentrations in ambient waters
within that State. Water quality criteria adopted in State water quality
standards could have the same numerical values as criteria developed
under section 304. However, in many situations States might want to adjust
water quality criteria developed under section 304 to reflect local
environmental conditions and human exposure patterns before .incorporation
into water quality standards. It is not until their adoption as part of
State water quality standards that criteria become regulatory.
Guidelines to assist States 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.
William A. Whittington
Director
Office of Water Regulations and Standards
111
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ACKNOWLEDGMENTS
Loren J. Larson
Judy L. Crane
(freshwater authors)
University of Wisconsin-Superior
Superior, Wisconsin
Jeffrey L. Hyland
Jerry M. Heff
(saltwater authors)
Battelle New England Laboratory
Duxbury, Massachusetts
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
David J. Hansen
(saltwater coordinator)
Environmental Research Laboratory
Narragansett, Rhode Island
Clerical Support:
Shelley A. Heintz
Diane L. Spehar
Nancy J. Jordan
Terry L. Highland
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CONTENTS
Page
Foreword
Acknowledgments iv
Tables vi
Introduction 1
Acute Toxicity to Aquatic Animals 8
Chronic Toxicity to Aquatic Animals 12
Toxicity to Aquatic Plants 13
Bioaccumulation 14
Other Data 16
Unused Data 23
Summary 30
National Criteria 31
References 103
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TABLES
Page
1. Acute Toxicity of Zinc to Aquatic Animals 34
2. Chronic Toxicity of Zinc To Aquatic Animals . . 56
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
59
Ratios
4. Toxicity of Zinc to Aquatic Plants 67
5. Bioaccumulation of Zinc by Aquatic Organisms 71
6. Other Data on Effects of Zinc on Aquatic Organisms 74
VI
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Introduction*
Zinc is the fourth most widely used metal in the world (Cammarota
1980), and its major uses are for galvanizing steel, for producing
alloys, and as an ingredient in rubber and paints. Because zinc(II)
substitutes to some extent for magnesium in the silicate minerals of
igneous rocks, weathering of bedrock gives rise to zinc in surface water.
Zinc always has the oxidation state of +2 in aqueous solution. Zinc(II)
is amphoteric, dissolving in acids to form hydrated Zn(II) cations and in
_2
strong bases to form zincate anions, usually Zn(OH)^ . Complexes of
zinc with the common ligands of surface waters are soluble in neutral and
acidic solutions, so that zinc is readily transported in most natural
waters and is one of the most mobile of the heavy metals. Concentrations
of zinc in uncontaminated fresh water are typically in the range of 0.5 to
10 pg/L (Trefry.and Presley 1979), whereas concentrations in clean sea
water range from 0.002 to 0.1 pg/L and increase with depth (Salomons and
Forstner 1984; Wallace et al. 1983).
Zinc occurs in many forms in natural waters and aquatic sediments.
At pH = 6.0 in fresh water, the dominant forms of dissolved zinc are
the free ion (98%) and zinc sulfate (2%), whereas at pH = 9.0, the dominant
forms are the mono-hydroxide ion (78%), zinc carbonate (16%), and
the free ion (6%) (Turner et al. 1981). In sea water at pH = 8.1,
the dominant species of soluble zinc are zinc hydroxide (62%), the
free ion (17%), the mono-chloride ion (6.4%), and zinc carbonate (5.8%)
* 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, and the
response to public comment (U.S. EPA 1985a) is necessary in order to
understand the following text, tables, and calculations.
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(Zirino and Yamamoto 1972). At pH » 7.0, the percentage of dissolved
zinc present in sea water as the free ion increases to 50%. In the
presence of dissolved organic materials, particularly humic substances,
the major fraction of dissolved zinc is in the form of zine-organic
complexes (Lu and Chen 1977).
Zinc can be present in sediments in several forms, including preci-
pitated Zn(OH)2s precipitates with ferric and manganic oxyhydroxides,
insoluble organic complexes, insoluble sulfides, and residual forms
(Patrick et al. 1977). As sediments change from a reduced to an oxidized
state, more zinc is mobilized and released in a soluble form (Lu and Chen
1977). The bioavailability of different forms of zinc in sediment varies
substantially and is poorly understood (Luoma and Bryan 1979). Baccini
(1985), Krantzberg and Stokes (1985), and Salomons (1985) reported that
benthic organisms influenced the partitioning of zinc between sediment
and the water column. •
Most of the zinc introduced into the aquatic environment is parti-
tioned into sediment by sorption onto hydrous iron and manganese oxides,
clay minerals, and organic materials (Lu and Chen 1977; Luoma and Bryan
1981; Parker et al. 1982; Warren 1981). Precipitation of the sulfide is
an important control on the mobility of zinc in reducing environments,
and precipitation of the hydroxide, carbonate, and basic sulfate salts can
occur when zinc is present in high concentrations. Formation of complexes
with organic and inorganic ligands can increase the solubility of zinc
and might increase or decrease the tendency for zinc to be sorbed (Salomons
and Forstner 1984).
The tendency of zinc to be sorbed is affected not only by the form
of the zinc and the nature and concentration of Che sorbent but also by pH
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and salinity. In a study of heavy metal sorption by two oxides and two
soils, zinc was completely removed from solution when pH exceeded 7, but
little or no zinc was sorbed when pH was below 6. Addition of inorganic
complexing ligands enhanced sorption (Huang et al. 1977). Helz et al.
(1975) and Solomons (1980) found less sorption of zinc to particulate matter
and sediment as salinity increased. This phenomenon was exhibited by many
other metals as well and apparently is due to displacement of the sorbed
zinc ions by alkali and alkaline earth cations, which are abundant in
brackish and saline waters. An increase in pH can increase sorption of
zinc even if salinity increases (Millward and Moore 1982; Solomons 1980).
Watanabe et al. (1985) reported that sorption of zinc was also dependent
on the organic carbon content of river sediments.
Zinc is an essential micronutrient for all living organisms (Leland
and Kuwabara 1985). Because zinc is essential, aquatic organisms have
evolved efficient mechanisms for accumulation of zinc from water and
food. The concentration of zinc in tissues of aquatic organisms is far
in excess of that required for various metabolic functions (Wolfe 1970).
Much of the excess zinc is bound to raacromolecules or is present as
insoluble metal inclusions in tissues (Simkiss et al. 1982). Inducible
low molecular weight metal-binding proteins, metallothioneins, are thought
to function, in part, in the intracellular sequestration and regulation
of the essential metals zinc and copper (Kojima and Kogi 1978; Roesijadi 1981).
Above some theoretical maximum beneficial concentration of zinc in
water, there exists a range of zinc concentrations that is readily tolerated
through each organism's capacity to regulate the uptake, internal distribution,
and excretion of zinc (Weiner and Giesy 1979). This range undoubtedly
varies among individuals, species, and larger phylogenetic groups. In
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addition, this tolerated range probably varies with the range of zinc
concentrations to which various populations have been historically exposed
and acclimated. Thus, biological variability in tolerance of zinc
is probably the result of phylogenetic differences and historic exposure
patterns, both short-term and geologic in scale.
Paramount to the question of the toxicity of zinc are the physical and
chemical forms of zinc, the toxicity of each form, and the degree of
interconversion among the various forms. Presumably, all forms oi: zinc
that can be sorbed or bound by biological tissues are potentially toxic.
Most likely, zinc will not be sorbed or bound unless it is dissolved, but
some dissolution of zinc can reasonably be expected to occur in the
alimentary canal following ingestion of particulates containing undissolved
zinc. Thus, the toxicity of undissolved zinc to a particular species
probably depends on feeding habits.- Therefore, plants and most fish are
probably relatively unaffected by suspended zinc, but many invertebrates
and some fishes might be adversely affected by ingestion of sufficient
quantities of particulates containing zinc.
The toxicity of zinc, as well as other heavy metals, is apparently
influenced by a number of chemical factors including calcium, magnesium,
hardness, pH, and ionic strength. These factors appear to affect the
toxicity of zinc either by influencing the availability of zinc or by
inhibiting the sorption or binding of available zinc by biological tissues.
In fresh water zinc appears to be less toxic at high hardness for a
variety of reasons, such as:
1) The ions contributing to hardness, primarily calcium and magnesium,
are divalent and compete with zinc, which is also divalent, for
sites of uptake and binding in biological tissues.
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2) Harder waters have higher ionic strengths due to the greater quantity
of charged ions (primarily mono- and divalent cations and anions) in
solution, and these ions electrostatically inhibit the ability of
other ions, such as zinc, to approach the sorption or binding sites
of the organisms. Thus zinc ions have lower activity in harder
waters.
3) Generally, harder waters have higher alkalinities and higher pHs,
resulting in the formation of insoluble, and possible soluble, zinc
carbonate and hydroxide compounds that are not sorbed by many species.
Thus, hardness appears to be the single best water quality characteristic
to reflect the variation in zinc toxicity induced by differences in
general water chemistry.
Because of the variety of forms of zinc (Callahan et al. 1979; Hem
1972; Salomons and Forstner 1984) and lack of definitive information
about their relative toxicities, no available analytical measurement is
known to be ideal for expressing aquatic life criteria for zinc. Previous
aquatic life criteria for zinc (U.S. EPA 1980) were expressed in terms of
total recoverable zinc (U.S. EPA 1983a), but this measurement is probably
too rigorous in some situations. Acid-soluble zinc (operationally defined
as the zinc that passes through a 0.45 tjm 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 zinc to, and bioaccumulation of zinc 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 terms
of acid-soluble zinc. For example, results reported in terms of dissolved
5
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zinc would not have been used if the concentration of precipitated zinc
had been substantial.
2. On samples of ambient water, measurement of acid-soluble zinc will
probably measure all forms of ginc that are toxic to aquatic life or
can be readily converted to toxic forms under natural conditions. In
addition, this measurement probably will not measure several forms,
such as zinc 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 many others) will measure soluble complexed forms
of zinc, such as the EDTA complex of zinc, 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 zinc in
aqueous effluents. Measurement of acid-soluble zinc probably will
be applicable to effluents because it will measure precipitates, such
as carbonate and hydroxide precipitates of zinc, 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 zinc might be used to determine whether
the receiving water can decrease the concentration of acid-soluble
zinc because of sorption.
4. The acid-soluble measurement is probably 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.
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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
of most samples of ambient water 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 to 9 (Weber and Stumm 1963).
9. Differences in pH within the range of 1.5 to 2.0 probably will not
affect the result substantially.
10. The acid-soluble measurement does not require a digestion step, as
does the total recoverable measurement.
11. After acidification and filtration of the sample to isolate the acid-
soluble zinc, the analysis can be performed using either atomic absorption
spectrophotoraetric or ICP-atoraic emission spectrometric analysis (U.S.
EPA 1983a), as with the total recoverable measurement.
Thus, expressing aquatic life criteria for zinc 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 zinc or for measuring zinc in ambient water or
aqueous effluents, measurement of both acid-soluble zinc and total
recoverable zinc in ambient water or effluent or both might be useful.
For example, there might be cause for concern if total recoverable zinc
is much above an applicable limit, even though acid-soluble zinc is below
the limit.
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Unless otherwise noted, all concentrations reported herein from
toxieity and bioconcentration tests are expected to be essentially equivalent
to acid-soluble zinc concentrations. All concentrations are expressed as
zinc, not as the chemical tested. The criteria presented herein supersede
previous aquatic life water quality criteria for zinc (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 excursions (U.S. EPA 1985b). The latest comprehensive
literature search for information for this document was conducted in
July, 1986; some more recent information might have been included.
Acute Toxicity to Aquatic Animals
Available data, which are usable according to the Guidelines, on
the acute toxicity of zinc to aquatic animals are presented in Table 1.
Acute values for freshwater invertebrates ranged from 32 to 40,930 Mg/L
(Table 1), and those for fishes ranged from 66 to 40,900 pg/L, except for
two values that appeared high for the guppy. The two ranges are very
similar and very wide, probably due at least in part to hardness-related
factors.
Although many factors might affect the results of tests of the
toxicity of zinc to aquatic organisms (Sprague 1985), water quality
criteria can quantitatively take into account only factors for which
enough data are available to show that the factor similarly affects the
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results of tests with a variety of species. Hardness is often thought of
as having a major effect on the toxicity of zinc in fresh water, 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 (expressed as rag CaC03/L) is used here as a surrogate for the
ions that affect Che results of toxicity tests on zinc. 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 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 eight slopes are
between 0.56 and 1.65 (see end of Table 1) and most are close to the
slope of 1.0 that is expected on the basis that zinc, 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 eight
slopes as dissimilar as these is P = 0.77. This was interpreted as
indicating that it is reasonable to assume that the slopes for these
eight species are the same.
Where possible, the pooled slope of 0.8473 was used to adjust the
freshwater acute values in Table 1 to hardness = 50 mg/L. Species Mean
Acute Values were calculated as geometric means of the adjusted acute
values. Five of the seven most resistant species (Table 3) were tested
in a series of experiments reported by Rehwoldt et al. (1971,1972,1973)
using Hudson River water, and high acute values were obtained in two
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other tests whose results were placed in Table 6 because the organisms were
not identified to genus. It is not known whether the river water reduced
the toxicity of zinc or if the species were inherently resistant. Rehwoldt
et al. (1971,1972) also reported LCSOs of 6,700 and 6,800 pg/L for the
striped bass, Morone saxatilis. These were considerably higher than the
LCSOs reported by Hughes (1970,1973) and Palawski et al. (1985) for the
same species, although the values reported by Hughes were not used due to
inadequate acclimation of the test organisms.
Genus Mean Acute Values (GMAVs) at hardness - 50 mg/L (Table 3) were
then calculated as geometric means of the available freshwater Species
Mean Acute Values. The GMAV for Morone was based only on the SMAV for
the striped bass because of the probability that the LCSOs reported by
Rehwoldt et al. (1971,1972) were two high for both species in this genus.
Of the 35 genera for which acute values are available, the most sensitive
genus, Ceriodaphnia, is about 950 times more sensitive than the most
resistant genus, Argia. Acute values are available for more than one
species in each of seven genera and the range of Species Mean Acute
Values within each genus is less than a factor of 3.7. The freshwater
Final Acute Value for zinc at hardness = 50 mg/L was calculated to be
130.1 ug/L using the procedure described in the Guidelines and the Genus
Mean Acute Values in Table 3. This value is above the Species Mean Acute
Value for a cladoceran and for the striped bass, but the results for the
striped bass were not obtained in a flow-through test in which the
concentrations of test material were measured. Thus, the freshwater
/. /TN s (0.8473[ln(hardness)]+0.8604)
Criterion Maximum Concentration (in ug/L) « ex
Acute tests considered useful in the derivation of a saltwater
criterion for zinc have been conducted with 26 species of invertebrates
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and 7 species of fish (Table 1). The range of Species Mean Acute Values
for saltwater invertebrates extends from 195 ug/L for embryos of the
quahog clam, Mercenaria mercenaria, (Calabrese and Nelson 1974) to 320,400
jjg/L for adults of the clam Macoma balthica (Bryant et al. 1985). The
range of Species Mean Acute Values for fish is narrower, extending from
191.4 ug/L for larvae of the cabezon, Scorpaenichthys marmoratus, (Dinnel
et al. 1983) to 38,000 Mg/L for juvenile spot, Leiostomus xanthurus
(Hansen 1983). As a general rule, early life stages of saltwater inverte-
brates and fish are more sensitive to zinc than juveniles and adults.
Both temperature and salinity affect the results of acute tests on
zinc. The effect of temperature has been studied with four bivalve
molluscs and one amphipod, whereas the effect of salinity has been studied
with a worm, clam, amphipod, two isopods, and a fish (Table 1). In
general, the LC50 increases as salinity increases (presumably because
complexation by chloride increases) and as temperature decreases. However,
the LC50 for a species also seems to decrease as salinity and temperature
deviate from the optimum for the species.
Of the 28 genera for which saltwater Genus Mean Acute Values are
available (Table 3), the most sensitive genus, Scorpaenichthys is about
1,700 times more sensitive than the most resistant, Macoma. Clams are
both sensitive and resistant to zinc. Acute values are available for
more than one species in each of five genera and the range of Species
Mean Acute Values within each genus is less than a factor of 5.2. The
saltwater Final Acute Value for zinc was calculated to be 190.2 |Jg/L>
which is slightly lower than the acute value for the most sensitive
species .
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Chronic Toxicity to Aquatic Animals
Although most of the chronic toxicity tests conducted on zinc with
freshwater species were in soft water ranging in hardness from 25 to 52 mg/L,
Chapman et al. (Manuscript) studied the chronic toxicity of sine to Daphnia
nagna at hardnesses of 52, 104, and 211 mg/L (Table 2). They found that the
chronic toxicity of zinc decreased when hardness increased from 52 to 104
mg/L. When hardness was further increased to 211 mg/L, the toxicity of
zinc did not change. No other data are available concerning the relationship
between hardness and the chronic toxicity of zinc.
The chronic values for the two species of freshwater invertebrates
ranged from 46.73 to >5,243 pg/L, whereas those for six species of fish
ranged from 36.41 to 854.7 ug/L.
A life-cycle toxicity test has been conducted with the saltwater
mysid, Mysidopsis bahia (Lussier et al. 1985). Survival, days to first
brood, and young/female reproductive day were all affected at 231 pg/L,
but no effects were detected at 120 >Jg/L.
Acute-chronic ratios are available for six freshwater and one saltwater
species. The freshwater Species Mean Acute-Chronic Ratios range from
0.7027 to 41.20,'whereas the saltwater ratio is 2.997 (Table 3). Because
the Final Acute-Chronic Ratio is meant to apply to sensitive species,
which often have lower acute-chronic ratios than resistant species, it
was calculated as the geometric mean of the ratios for the freshwater
Daphnia magna. Chinook salmon, and rainbow trout and the saltwater mysid.
The resulting value of 2.208 is lower than all the other Species Mean
Acute-Chronic Ratios (Table 3). Division of the freshwater and saltwater
Final Acute Values by 2.208 results in freshwater and saltwater Final
Chronic Values of 58.92 >Jg/L (at hardness = 50 mg/L) and 86.14 pg/L,
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respectively. In spite of the data on the effect of hardness on the
chronic toxicity of zinc to Daphnia magna, the freshwater chronic slope
is assumed to be the same as the acute slope, resulting in a freshwater
Final Chronic Value - e(0.8473[la(h«dae..)]+0.7614)>
Toxicity to Aquatic Plants
Toxicity tests on zinc have been conducted with 20 species of freshwater
plants, which were affected by zinc concentrations ranging from 30 to
>200,000 pg/L (Table 4). Although tests have been conducted with several
vascular plants, both the highest and lowest values were obtained with
algae.
Few data are available concerning the effect of hardness on toxicity
to plants. One study with the diatom, Navicula seminulum, (Academy of
Natural Sciences 1960) tested zinc toxicity at two hardnesses. At
hardness = 58.46 rag/L, zinc was more toxic, on the average, than in tests
at hardness = 174 mg/L. However, there was overlap in EC50s between the
hardnesses tested. The toxicity of zinc to algae, might be related to the
concentration of phosphate or nitrate (Kuwabara 1985; Rao and Subraraanian
1982).
The toxicity of zinc to saltwater plants has been tested with 18
species of phytoplankton and 8 species of macroalgae (Tables 4 and 6).
The diatom, Schroederella schroederi^, was the most sensitive phytoplankter,
with a 48-hour EC50 of 19.01 >Jg/L. Other species affected at concentrations
less than the Final Chronic Value are Cricosphaera carterae, Isochrysis
gabana, Thalassiosira rotula, Glenodinium halli, and Gymnodinium splendens.
Macroalgae were affected at concentrations >IQQ pg/L. Therefore, although
data on most saltwater plants indicate that they will be protected by a
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saltwater criterion derived from data on animals, some phytoplankters
might be affected under certain environmental conditions.
Bioaccumulat ion
Six freshwater species were exposed to zinc and had tissue concentra-
tions measured after sufficient time to achieve steady-state (Table 5).
Bioconcentration factors (BCF) ranged from 51 for the Atlantic salmon
(Farmer et al. 1979) to 1,130 for a mayfly (Nehring 1976). A mean BCF of
100 was obtained in three tests with a clam (Graney et al. 1983) , and the
BCF of 106 for a stonefly was much lower than that for the mayfly. Both
the flagfish and the guppy had BCFs between 400 and 500. Atchinaon et al.
(1977), Mclntosh and Bishop (1976), and Murphy et al. (1978a,b) measured
the concentrations of zinc in several species of fish obtained from a
pond contaminated with zinc. Direct accumulation from water did not
appear to be a major route of uptake of zinc by two species of fish in a
lake (Klaverkamp et al. 1983). Gushing a'nd Rose (1970), Gushing and
Watson (1971), and Gushing et al. (1975) studied the uptake of zinc by
periphyton and fish in microcosms. Van der Werff (1984) found that humic
and fulvic acids reduced the uptake of zinc by an alga.
Bioaccumulation data for zinc are available for six species of saltwater
algae and seven species of saltwater animals (Table 5). Steady-state BCFs
derived from laboratory exposures of saltwater algae for periods of 0.5 to
140 days ranged from 75.5 for the brown macroalga, Laminaria digitata
(Haritonidis et al. 1983) to 10,768 for another brown raacroalga, Fucus
serratus (Young 1975). BCFs based on data derived from field collections
of macroalgae ranged from 1,027 to 2,029 for a third brown macroalga,
Fucus vesiculosus (Foster 1976; Foster and Bale 1975).
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BCFs derived from laboratory exposures of saltwater animals for
periods of 14 to 126 days range from 3.692 in the whole body of the
shrimp, Pandalus montagui (Ray et al. 1980) to 23,820 in the total
soft tissue of the eastern oyster, Crassostrea virginica (Shuster and
Pringle 1968).
For the mummichog, Fundulus heteroclitus, the BCF for both whole
body and scales decreased with increasing concentration in water between
210 and 7,880 Mg/L (Sauer and Watabe 1984). At all concentrations, the
scales had a higher BCF than the whole body. Sequestration of zinc in
scales, which is accompanied by a decrease in scale calcification (Sauer
and Watabe 1984), might be a mechanism of zinc storage or detoxification
in fish. O'Grady (1981) showed that sea trout, Salmo trutta, mobilized
zinc stored in its scales during the upstream spawning migration.
For both algae and animals, there is a definite trend toward an
inverse relationship between concentration in water and BCF. This is
best exemplified by the data in Table 5 for the brown macroalga, Laminaria
digitata (Bryan 1969) and the mummichog, Fundulus heteroclitus (Sauer
and Watabe 1984). Seip (1979) developed a mathematical model for the
accumulation of zinc and other metals by the brown macroalga, Ascophyllum
nodosum. The concentration of zinc in the alga was found Co be an approximately
linear function of the mean concentration of zinc in water up to about
100 Mg/L. Because the slope of the curve was less than 1, BCFs tended to
decrease with increasing concentration in water.
No U.S. FDA action level or other maximum acceptable concentration
in tissue is available for zinc, and, therefore, no Final Residue Value
can be calculated.
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Other Data
A wide variety of other data is presented in Table 6. In a test
on zinc phosphate, growth of a freshwater green alga was inhibited
during a 14-day exposure to 64 pg/L (Carton 1972). Growth of Scenedesmus
quadricauda was inhibited during exposure to 1,200 yg/L in river water
(Bringraann and Kuhn 1959a,b). The primary productivity of plankton was
reduced when exposed to 15 pg/L for 14 days (Marshall et al. 1983).
Several studies have been conducted on the effect of temperature on the
acute toxicity of zinc (Braginskiy and Shcherban 1978; Cairns et al. 1975a,
1978; Pickering and Henderson 1966; See et al. 1974; Smith and Heath 1979).
Except for the rainbow trout and golden shiners, the species were more
sensitive to zinc at higher temperatures. Snails were more sensitive to
thermal shock after exposure to zinc (Cairns at al. 1976).
Concentrations of dissolved oxygen down to 3.5 mg/L did not affect
the toxicity of zinc to the bluegill, but lower concentrations did
(Pickering 1968). Anderson (1973) and Anderson and Weber (1975) found that
the acute sensitivity of the guppy to zinc depended on the weight of the
fish. Sabodash (1974) studied the effects of zinc and calcium on survival
and growth of larval grass carp.
Most insects were more resistant to zinc than the other freshwater
species tested. Mayflies, damselflies, stoneflies, and caddisflies had LC50s
ranging from 1,330 to 58,100 pg/L (Table 6). One midge (Chironomous sp.) had
a 96-hr LC50 of 18,200 pg/L (Rehwoldt et al. 1973), whereas another (Tanytarsus
dissimilis) had a 10-day LC50 of 36.8 pg/L (Anderson et al. 1980). The
T- dissimilis value is very low compared to other values obtained with insects.
Although most LC50s for rainbow trout ranged from 2,000 to 5,000
pg/L, Carton (1972) obtained an LC50 of 90 Mg/L in a test on zinc phosphate.
16
-------
A 7-day EC50 of 10 ug/L was obtained with embryos and larva of the narrow-
mouthed toad (Birge 1978; Birge et al. 1979).
Cairns et al. (1975b) and Khangarot (1982) examined the effect of
feeding on the results of acute tests on zinc, whereas McLeay and Munro
(1979) and Sparks et al. (1972b) studied the effects of photoperiod and
shelters, respectively. Brafield and Mattiessen (1976), Hughes (1975), Hughes
and Tort (1985), and Thompson et al. (1983) studied the effect of zinc on
respiration of fishes. Allen et al. (1980) and Muramota (1978) found
that various chelating agents reduced the acute toxicity of zinc. Several
studies examined the use of fishes as biomonitoring organisms for zinc
(Cairns and Waller 1971; Cairns et al. 1973a; Sparks et al. 1972; Waller
and Cairns 1972).
Many studies have examined zinc as a dietary requirement for freshwater
plants (e.g., Vaughn et al. 1982) and fish (e.g., Barash et al. 1982;
Bell et al. 1984; Dabrowski et ai. 1981; Gatlina and Wilson 1983,1984;
Jeng and Sun 1981; Ketola 1979; Knox et al. 1982,1984; Ogino and Yang
1978,1979; Richardson et al. 1985; Rodgers 1982; Satoh et al. 1983a,b,c;
Takeda and Shimma 1977).
Armitage (1980), Armitage and Blackburn (1985), Austin and Munteanu
(1984), Carlson et al. (1986), Eichenberger (1981), Eichenberger et al.
(1981), Foster (1982a), Harding et al. (1981), Hughes (1985), Lang and
Lang-Dobler (1979), Maas (1978), Meyer (1978), Rice (1977), Roline and
Boehmke (1981), Ruthven and Cairns (1973), Say and Whitton (1983), Say
et al. (1977), Sheehan and Knight (1985), Shehata and Whitton (1981),
Solbe (1973), Swain and White (1985), Swift (1985), Wehr and Whitton
(1983b,c), Wentsel and Mclntosh (1977), Williams and Mount (1965), Yan
17
-------
et al. (1985), Yasuno et al. (1985), and Zanella (1982) investigated
relationships between the abundance and diversity of freshwater species
and the concentration of zinc in water and sediment.
The detoxification of zine was studied by Kito et al. (1982), Klaverkamp
et al. (1985), Ley et al. (1983), Marofante (1962), Pierson (1985a,b),
Roch and McCarter (1984a,b), and Takeda and Shimizu (1982).
Low concentrations of zinc stimulate the rate of growth of saltwater
microalgae. Concentrations equal to or less than 100 Mg/L stimulated growth
of Nitzchia longissima during exposures lasting one to five days (Subramanian
et al. 1980). Similarly, growth of Skeletonema costatum was both stimulated
by zinc concentrations equal to or lower than 200 Mg/I. during one to five
days of exposure (Subramanian et al. 1980) and reduced by 20% during
exposure for 10 to 14 days to 100 ^g/L zinc (Brack et al. 1976). Wikfors
and Ukeles (1982) reported a 6.7% increase in the growth of Phaeodactylum
tricornutum during exposure for 12 days to 4,800 Mg/L- Therefore the
difference between beneficial and detrimental concentrations of zinc to
phytoplankton might be small and dependent on the species and exposure.
Stroragren (1979) studied the effect of zinc on growth of five species
of saltwater macr'oalgae. Growth was reduced at 1,400, but not 100,
\igll for Ascophyllum nodosum, Fucus serratus, Fucus spiralis, and Pelvetia
canaliculata, and at 7,000, but not 3,500, ^g/L for Fucus vesiculosus.
Bryan (1969) reported reduced growth of Laminaria digitata during exposure
for 24 days to concentrations as low as 100 |Jg/L. A concentration
of 250 Mg/L reduced growth of sporophytes of Laminaria hyperboria, whereas
5,000 ug/L induced abnormal maturation of gametophytes of the same species
' (Hopkins and Kain 1971). Zinc concentrations as low as 8.8 >jg/L altered
lipid metabolism in Fucus serratus (Smith and Harwood 1984).
18
-------
Two ciliate protozoans exhibited markedly different sensitivities to
zinc. Growth of Cristigera sp. was reduced by exposure for four to five
hours to concentrations as low as 50.63 ug/L (Gray 1974; Gray and Ventilla
1973), but a concentration of 10,000 Mg/L only reduced the growth of
Euplotes vannus by 10% (Persoone and Uyttersprot 1975).
Bryan and Hummerstone (1973) compared the sensitivity of the
polychaete, Nereis diversicolor, from sediments heavily contaminated with
zinc and other metals to that of the same species from clean sediments at
three salinities (Tables 1 and 6). At all three salinities, worms from
the contaminated sediments were less than a factor of two more resistant
to zinc than those from clean sediments. Worms from the contaminated
sediments also had somewhat lower BCFs than worms from clean sediments
when exposed to zinc in the laboratory for 34 days. These results suggest
that acclimation or genetic adaptation of the worms to contaminated
sediments provided only a minor ability to regulate zinc more efficiently
than worms from uncontaminated sediments.
The polychaetes, Ophryotiocha diadema and Ctenodrilus serratus, were
exposed to zinc in partial life-cycle tests .that began with adults and
examined effects on survival and reproduction (Reish and Carr 1978).
Population size was reduced 500 |jg/L in both static tests but effects of
zinc were not detected at 100 }Jg/L.
A variety of responses were observed in mud snails, Nassarius obsoletus,
during exposure for 72 hr to progressively higher concentrations of zinc
(Maclnnes and Thurberg 1973). At 2,000 tJg/L, there was a depression of
oxygen consumption. Locomotor behavior was inhibited at 10,000 Mg/L,
and death ensued at 50,000 Mg/L- Similarly, shell deposition by adults
of the blue mussel, Mytilus edulis, was inhibited by 50% following exposure
19
-------
for two to six days to >60 Mg/L (Manley et al. 1984; Stroragren 1982).
The EC50 based on reduced byssal thread production was 1,800 ,Jg/L, whereas
the 7-day LC50 was 5,000 pg/L (Martin et al. 1975). The 72-hr EC50 for
development of mussel embryos to the veliger stage was between 96 and 314
Mg/L (Dinnel et al. 1983).
Different life stages and developmental processes of gametes, embryos,
and larvae of Pacific oysters have different sensitivities to zinc. The
ability of oyster sperm to fertilize eggs was depressed by 50% after
exposure for 60 min to 443.6 Mg/L (Dinnel et al. 1983). The 48-hr LC50
for embryos was 241.5 Mg/L (Brereton et al. 1973). Larvae developed
abnormally and grew more slowly than controls at zinc concentrations
between 125 and 500 Mg/L (Brereton et al. 1973), whereas-ECSOs for growth
of 6-day-old and 16-day old larvae exposed for four days were 80 and 95
Mg/L, respectively (Watling 1982). The 96-hr LC50 for 6-day and L6-day
larvae was in excess of 100 Mg/L, whereas that for 19-day larvae was between
30 and 35 Mg/L (Watling 1982). Significant delay of, and reduction in,
successful settlement was observed after 5 days in 125 Mg/L (Boyden et al. 1975)
and after 20 days in 10 to 20 Mg/L (Watling 1983). Juvenile oyster spat
had a 23-day LC50 of 75 Mg/L (Watling 1983).
Exposure to 176 Mg/L for 72 hr caused a 50% reduction in the rate of
calcium uptake by larvae of the clam, Mulinia lateralis, whereas a concen-
tration of 200 Mg/L caused 53% mortality among the clam larvae in the same
time period (Ho and Suboff 1982). The 8 to 10-day LC50 was 195.4 Mg/L
for larvae of the quahog clam, Mercenaria mercenaria and growth of survivors
was estimated to be reduced by 38.4% (Calabrese et al. 1977).
At concentrations as low as 250 Mg/L, z^nc caused significant delays
in molting and development rate of larvae of the grass shrimp, Palaemonetes
20
-------
pugio, particularly under stressful temperature-salinity regimes (McKenney
1979; McKenney and Neff 1979,1981). Concentrations of 25 to 50 Mg/L
were without effect on the development rate of larvae of the mud crab,
Rhithropanopeus harrisii (Benijts-Claus and Benijts 1975). However,
in the presence of lead at 25 to 50 ug/L, these concentrations of zinc
produced a significant delay in the rate of larval development of mud
crabs. Rate of limb regeneration by adults of the fiddler crab, Uca
pugilator, was inhibited at zinc concentrations of 1,000 (Weis 1980).
This inhibitory effect was amplified at low salinities.
Motility of the sperm of the sea urchins, Arbacia punctulata and
Strongylocentrotus purpuratus, was stimulated by brief exposure to zinc
concentrations at or below 1,634 and 654.8 ug/L, respectively (Timourian and
Watchmaker 1977; Young and Nelson 1974). At concentrations of 3,269 and
6,538 >Jg/L, respectively, sperm motility was inhibited. Reduction of the
ability of echinoderm sperm to fertilize eggs appeared to be more sensitive
than sperm motility to the toxic effects of zinc (Dinnel et al. 1983).
EC50s after one hour of exposure of sperm ranged from 28 to 382.8
Mg/L. In tests with the sand dollar, Dendraster excentricus, and two sea
urchins, Strongylocentrotus droebachiensis and S_. purpuratus, development
to the pluteus stage was less sensitive than fertilization. Waterman (1937)
found that 810 tJg/L inhibited gastrulation and that 2,314 ug/L was lethal to
embryos of Arbacia punctulata.
Somasundarum et al. (1984a,b,c,d;1985) identified several developmental
anomalies and histopathological lesions in developing embryos and larvae
of Atlantic herring, Clupea harengus, that were exposed to 50 to 12,000
nig/L. Zinc concentrations below 6,000 pg/L did not affect embryo
volume. Below 2,000 pg/L, zinc accelerated embryonic development, but
21
-------
6 000 ug/L inhibited development. At zinc concentrations as low as 50
Mg/k» there was a significant increase in the incidence of jaw and branchial
abnormalities. Concentrations above 500 pg/L increased the incidence of
vertebral abnormalities. Significant decreases in the size of the otic
capsules and eyes were observed at zinc concentrations higher than 2,000
and 6,000 Mg/L> respectively. Ultrastructural changes in brain cells and
somatic musculature were observed in herring larvae that were allowed to
develop for 14 days in sea water containing 50 to 12,000 pg/L.
In contrast to the toxic effects noted above, Weis et al. (1981)
found that exposure to 10,000 Mg/L ameliorated teratogenic effects on
Fundulus heteroclitus exposed to methyl mercury. Also, zinc concentra-
tions of 1,000 Mg/L or greater enhanced regeneration of the tail fin and
ameliorated effects of methyl mercury on fin regeneration in adult:
mummichogs (Weis and Weis 1980).
Exposure of adult mummichogs to 2,200 MgA- resulted in increased
activity of the hepatic enzyme aminolevulinic acid dehydrase (Jackira
1973), whereas exposure to 60,000 pg/L caused 30% mortality and
histopathological lesions in the oral epithelium of survivors (Eisler and
Gardner 1973). Calcification of the scales of juvenile mummichogs was
inhibited at 760 to 7,100 Mg/L (Sauer and Watabe 1984).
Crustaceans and fish are able to accumulate zinc from both water and
food. For adult green crabs, Carcinus maenas, the BCF for zinc from
water was 130 and the bioaccumulation factor (BAF) for zinc from water and
food was 210 (Renfro et al. 1975), but the BAF was not significantly higher.
However the BAF was statistically higher than the BCF with adult mosquito
fish, Gambusia affinis, and juvenile spot, Leiostomus xanthurus (Willis
and Sunda 1984). At 120 days, the BAF and BCF for uptake of zinc from
22
-------
water alone and water plus food by mosquito fish were 45 and 8, respectively.
The BAF and BCF for spot after a 28-day exposure were 28 and 3, respectively.
These results suggest that these fish obtain five to nine times more zinc
from food than from water. It must be recognized, however, that the relative
magnitude of the contribution from both sources to the concentration of zinc
in saltwater animals will depend on the relative concentrations of zinc
in the water and food. Eisler (1967) and Eisler and Gardner (1973) have
shown that BCFs for adult mummichogs, Fundulus heteroclitus, are inversely
related to the concentration of zinc in the water.
Unused Data
Some data on the e.ffects of zinc on aquatic organisms were not used
because the studies were conducted with species that are not resident in
North America (e.g., Abbasi and Soni 1986; Ahsanullah and Arnott 1978;
Baudoin and Scoppa 1974;. Bengtsson 1974a,b,c,d,e; Carter and Nicholas
1978; Chapman and Dunlop 1981; Dunlop and Chapman 1981; Greenwood and
Fielder 1983; Harrison 1969; Howell 1985; Jones and Wacker 1979; Jones et
al. 1984; Karbe et al. 1975; Khangarot 1981,1984; Khangarot et al. 1982,
1985; Kumar and Pant 1984; Lomte and Jackhar 1982; Lyon et al. 1983;
Martin et al. 1977; Mathur et al. 1981; McFeters et al. 1983; Mecham
and Holliman 1975; Millington and Walker 1983; Milner 1982; Murti and
Shukla 1984; Natarajan 1982; Nazarenko 1970; Pentreath 1973; Sartory and
Lloyd 1976; Sastry and Subhadra 1984; Saxena and Parashari 1983; Seiffer
and Schoof 1967; ShaffL 1979; Shehata and Whitton 1981; Shukla et al.
1983; Solbe and Flook 1975; Speranza et al. 1977; Srivastava et al. 1985;
Stary and Krantzer 1982; Subhadra and Sastry 1985; Thorp and Lake 1974;
Verma et al. 1984; Wagh et al. 1985; White and Rainbow 1982; Willis 1983)
23
-------
or because the test specices was not obtained in North America and was
not identified well enough to determine whether it is resident in North
America (e.g., Greichus et al. 1978; Jennett et al. 1981; Pommery et al. 1985;
Tishinova 1977). Results (e.g., Bagshaw et al. 1986; Brown and Ahsanullah
1971) of tests conducted with brine shrimp, Artemia sp., were not used
because these species are from a unique saltwater environment.
Babich and Stotzky (1985), Biddinger and Gloss (1984), Cairns (1957),
Campbell and Stokes (1985), Connolly (1985), Doudoroff and Katz (1953),
Duxbury (1985), Eisler (1981), Hartman (1980), Kaiser (1980), LeBlanc
(1984), Lim (1972), Lloyd (1965), Macek and Sleight (1977), Mancini
(1983), McKim (1977), Pagenkopf (1976), Patrick et al. (1968), Phillips
and Russo (1978), Polikarpov (1966), Rai et al. (1981b), Riordan (1976),
Skidmore (1964), Skidmore and Firth (1983), Slooff et al. (1986), Sprague
et al. (1964), Strufe (1964), Taylor et al. (1982), Thomson and MacPhee
(1985), Vernon (1954), Vytnazal (1985), Weatherley et al. (1980), and
Whitton (1970) only contain data that have been published elsewhere.
Results were not used if either the test procedures, test material,
or dilution water was not adequately described (e.g., Back 1983; Bates et
al. 1981; Baudin 1983a,b; Berg and Brazzell 1975; Biegert and Valkovic
1980; Birge and Just 1973,1975; Bradley and Sprague 1983; Brauwers 1982;
Brkovic-Popovic and Popovic 1977a,b; Brown 1968; Carpenter 1927; Coburn
and Friedman 1976; Danil'chenko 1977; Darnall et al. 1986; Dilling and*
Healy 1927; Fleming and Richards 1982; Hutchinson and Sprague 1985;
Ishizaka et al. 1966; Joraensostrorasks and McLaughlLn 1974; Knittel
1980; Labat et al. 1977; Miller et al. 1985; Muramoto 1980; Pavicic 1980;
Petry 1983; Rao and Saxena 1981; Sabodash 1974; See et al. 1974,1975;
24
-------
Sicko-Goad and Lazinsky 1981; Tokunago and Kishikawa 1982; Vinot and
Larpent 1984).
Data were not used if zinc was a component of an effluent (e.g.,
Bailey and Liu 1980; Cherry et al. 1979; Finlayson and Ashuchian 1979;
: " Frazier 1976; Grushko et al. 1980; Guthrie et al. 1977; Jay and Muncy
1979; Lewis 1986; Lu et al. 1975; Nagy-Toth and Barna 1983; Nehring and
Goettl 1974; Neufeld and Wallach 1984; Newman et al. 1985; O'Conner 1976;
Oladimeji and Wade 1984; Ozlmek 1985; Phillips and Gregory 1980; Rana and
Kumar 1975; Roesijadi et al. 1984; Saunders and Sprague 1967; Sprecht et
al. 1984; Wang 1982; Whitton et al. 1981; Wong and Tarn 1984a,b; Wood
1975), mixture (e.g., Baker and Boldigo 1984; Besser 1985; Biesinger et
al. 1974; Birge et al. 1978; Borgmann 1980; Brown et al. 1969; Cairns and
Scheier 1968; Cearley 1971; Chang et al. 1981; Christensen et al. 1985;
Cowgill et al. 1986; Danil'chenko and Strogahov 1975; Davies 1985; Davies
and Woodling 1980; Doudoroff 1956; Doudoroff et al. 1966; Eaton 1973;
Eisler 1977b; Finlayson and Verrue 1980; Giesy et al. 1980; Hedtke and
Puglisi 1980; Henry and Atchison 1979a,b; Hutchinson and Czyrska 1972;
Hutchinson and Sprague 1983; Lubinski and Sparks 1981; Markarian et al.
1980; Marking and Bills 1985; McLeese and Ray 1984; Muller and Payer
1980; Muska 1977; Patrick and Loutit 1976,1978; Pope 1981; Roch and McCarter
1984c,1986; Roch et al. 1985,1986; Rodgers and Beamish 1983; Sprague 1965;
Stromegcen 1980; Vymazal 1984; Wong et al. 1982a,b,1984b), or a sediment
(e.g., Arruda et al. 1983; Broberg 1984; Bryan et al. 1983; Dean 1974;
Krantzberg 1983; Laskowski-Hoke and Prater 1984; Lewis and Mclntosh 1984,
1986; Luoma and Jenne 1977; Malueg 1984; McMurtry 1984; Munawar et al.
1985; Oakden et al. 1984; Ray et al. 1981; Seelye et al. 1982; Wentsel
et al. 1977; Wong and Kwan 1981; Wong and Tarn 1984; Wong et al. 1984a).
25
-------
Data were not used if the organisms were exposed to zinc by injection
or gavage or in food (e.g., Barash et al. 1982; Baudin 1985; Bell et al.
1984; Cancalon 1982; Cowgill et al. 1985; Dallinger and Wieser 1984;
Dixon and Compher 1977; Gatlin and Wilson 1983,1984; Hibiya and Oguri
1961; Jeng and Sun 1981; Knox et al. 1984; Lyon et al. 1984; Mansouri-
Aliabadi and Sharp 1985; Marafonte 1976; Ogino and Yang 1978,1979; Patrick
and Loutit 1978; Richardson et al. 1985; Saiki and Mori 1955; Satoh et
al. 1983a,b; Smith-Sonneborn et al. 1983; Suzuki and Ebihara 1984; Suzuki
and Kawamura 1984; Suzuki et al. 1983,1984; Takeda and Shiraraa 1977;
Vaughan et al. 1982; Windotn et al. 1982; Young 1975).
Adragna and Privitera (1978,1979), Akberali and Earnshaw (1982),
Anderson et al. (1978), Babich et al. (1985,1986a,b), Brown (1976), Burton
and Peterson (1979), Genini and Turner (1983), Crespo (1984), Crist et
ai. (1-981), Doyle et al. (1981),-Everaarts et al. (1979), Fleming et al.
(1982), George (1983), Killer and Perlmutter (1971K Hiltibran (1971),
Kodama et al. (1982a), Nemosok et al. (1984), Rachlin and Perlmutter
(1969), Sirover and Loeb (1976), and Watson and Beamish (1981) only
exposed enzymes, excised or homogenized tissue, or cell cultures.
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., Affleet 1952; Carter and Cameron 1973; Eddy and Fraser 1982;
Matthiessen and Brafield 1973; McDonald et al. 1980; Porter and Hakanson
1976; Stary and Kratzer 1982; Stary et al. 1983; Taylor 1978; Vijayamadhavan
and Iwai 1975; Wang 1959) or were conducted in chlorinated or "tap" water
(e.g., Goodman 1951; Grande 1966; Haider and Wunder 1983; Hughes and
Adeney 1977; Jones 1935,1938,1939; Matthiessen and Brafield 1977; Rahel
26
-------
1981; Shcherban 1977; Skidmore 1970; Skidmore and Tovell 1972). Dilution
water was at too low a pH in tests by Michnowicz and Weaks (1984), whereas
temperature fluctuated too much in the test reported by Mills (1976b).
Allan et al. (1980), Bates et al. (1983), Buikema et al. (1974a,b,
1977), Cairns and Dickson (1970), Fayed and Abd-El-Shafy (1985), Kuwabara
(1985), Mills (1976a,b), Petersen (1982), Rainbow et al. (1980), Ruthven
and Cairns (1973), Say and Whitton (1977), Sullivan et al. (1973), and Zitko
et al. (1973) used dilution water that contained too high a concentration of
chelating agent or other organic matter. Mukhopadhyay and Konar (1984) used
a phosphate buffer, which might have detoxified zinc, although their LC50s
for two invertebrate species were quite low after adjustment for hardness.
Benson and Birge (1985), Berglind and Dave (1984), and Birge et al.
(1983) cultured or acclimated organisms in one water and conducted tests
in another. Hughes (1970,1973) did not acclimate organisms for a long enough
time. Tests conducted with too few test organisms (e.g., Applegate et
al. 1957; Gardner 1975; McLeese 1976; Sprague 1964a; Tishinova 1977)
were not used. High control mortalities occurred in tests reported by
Cairns and Scheier (1964) and Havas and Hutchinson (1982). The water
quality varied too much during tests conducted by Cairns et al. (1981),
Nehring and Goettl (1974), and Thompson et al. (1980). Toxicity tests
conducted without controls were not used (e.g., Graham et al. 1986).
The 96-hr values reported by Buikema^et al. (1974a,b) were subject to
error because of possible reproductive interactions (Buikema et al.
1977). The test organisms were possibly stressed by disease or parasites
during tests reported by Boyce and Yamada (1977), Guth et al. (1977), and
Sakanari et al. (1984). Hublou et al. (1954) conducted tests on zinc
leached from galvanized trays. Anudu (1983), Bradley et al. (1985a,b),
27
-------
Cairns (1972), Cairns et al. (1973a,b), DeFilippis and Pallaghy (1976),
Duncan and Klaverkamp (1980), Foster (1982b), LeBlanc (1982), and Wang
(1986b) conducted studies of acclimation to zinc or used organisms that
had been exposed or were resistant to zinc.
Biochemical and histological studies were not used (e.g., Anderson
and Sparks 1978; Canalon 1982; Cenini and Turner 1979; Eddy and Talbot 1985;
Kearns and Atchison 1979; Kodama et al. 1982a,b; Nemcsok et al. 1984;
Rachlin et al. 1985; Sailer et al. 1980; Schmitt et al. 1984; Taban et
al. 1982; Thomas et al. 1985; Vijayamadhauan and Iwai 1975; Watson and
Beamish 1980; Watson and McKoewn 1976; Yaraamoto et al. 1977).
Results of chronic tests were not used if the concentration of test
material was not measured (e.g., Winner and Gauss 1986) or if the test
solutions were only renewed once a week (e.g., Crandall and Goodnight
1962,1963). Data on toxicity or accumulation or both from microcosm or
model ecosystem studies were not used if the concentration of zinc in
water decreased with time (e.g., Bachman 1963; Davis and Negilski 1972).
Results of laboratory bioconcentration tests were not used Lf the test
was not flow-through or renewal (e.g., Dean 1974; Evtushenko et al. 1984;
Fayed et al. 1983; Hughes and Flos 1978; Joyner 1961; Joyner and Eisler 1961;
Lyngby et al. 1982; Skipnes et al. 1975; Sklar 1980; Slater 1961; Young
1977) or if the concentration of zinc in the test solution was not adequately
measured (e.g., Mellinger 1972; Munda 1979,1984; Phillips 1976,1977).
«
Hardy and Raber (1985) did not measure the concentration of zinc in tissues.
Van Hoof and Van San (1981) found high concentrations of zinc in their
control fish. Harvey (1974) studied depuration, but not uptake, of zinc
by a freshwater clam, and Ferguson and Bubela (1974) studied uptake by
homogenized algal suspensions. The concentration of zinc fluctuated too
much' in the tests reported by Kormondy (1965) and O'Grady and Obdullah (1985).
28
-------
Reports of the concentrations of zinc in wild aquatic organisms
(e.g., Abdullah et al. 1976; Abo-Rady 1979,1983; Adams et al. 1980,1981;
Amemiya and Nakayama 1984; Anderson 1977; Anderson et al. 1978; Arnac and
Lassus 1985; Badsha and Goldspink 1982; Bailey and Stokes 1985; Barber
and Trefry 1981; Bonn and Fallis 1978; Bosserman 1985; Bradley and Morris
; ' 1986; Brezina and Arnold 1977; Brooks et al. 1976; Brown 1977; Brown and
" . Chlow 1977; Burrows and Whitton 1983; Burton and Peterson 1979; Bussey et
al. 1976; Caines et al. 1985; Chapman 1985; Chassard and Balvay 1978;
Coughtrey and Martin 1977; Cover and Wilhm 1982; Cowx 1982; Dallinger
and Kautzky 1985; EIFAC 1977; Elder and Mattraw 1984; Elliott et al.
1981; Elwood et al. 1976; Estabrook et al. 1985; Felat and Melzer 1978;
Fletcher and King 1978; Fletcher et al. 1975; Franzin and McFarlane 1980;
Frazier 1975; Friant and Koerner 1981; Friant and Sherman 1980; Gale et
al. 1973a,b; Giesy and Weiner 1977; Greichus et al. 1978; Guillizzoni
1980; Hakanson 1984; Harding and Whitton 1978; Hei-t and Klusek 1985; Holm
1980; Howard and Brown 1983; Huggett et al. 1973; Jeng and Lo 1974;
Johannessan et al. 1983; Jones et al. 1985; Kleinert et al. 1974;
Kole et al. 1978; Korda et al. 1977; Lee et al. 1984; Lewis 1980; Lobel
and Wright 1983; Lord et al. 1977; Lowe et al. 1985; Lucas and Edgington
1970; Lundholm and Andersson 1985; Maas 1978; McFarlane and Franzin 1978;
McHardy and George 1985; Moreau et al. 1983; Morrison et al. 1985; Nabrzyski
1975; Nabrzyski and Gajewski 1978; Namminga and Wilhm 1977; Ney and
- Martin 1985; Ney et al. 1982; Norris and Lake 1984; O'Grady 1981; Paul
and Filial 1983; Pennington et al. 1982; Percy and Borland 1985; Peverly
1985; Rabe et al. 1977; Ranta et al. 1978; Ray and White 1979; Rehwoldt
et al. 1976; Romberg and Refro 1973; Salanki et al. 1982; Saltes and
Bailey 1984; Seagle and Ehlraann 1974; Shearer 1984; Shimma et al. 1984;
29
-------
Shuman et al. 1977; Simpson 1979; Stary et al, 1982; Stokes et .al,, 1985;
Strufe 1964; Teherani et al. 1979; Tessier et al» 1984; lisa and Strange
1981; Tsui and McCart 1981; Uthe and Bligh 1971; Van Coillie and Rousseau
1974; Van Loon and Beamish 1977; Villarreal-Trevin© et al. 1986; Vinikour
et al. 1980; Wachs 1982; Walker et al. 1975; Wehr and Whitton 1983a,b;
Wehr et al. 1983; Whitton et al. 1981,1982; Wiener and Giesy 1979:; Winger
and Andreasen 1985; Wissmar et al. 1982; Young and Blevins 1981, Zadory
1984) were not used to calculate bioaccumulation factors because eiither
the number of measurements of the concentration in water was too
small or the range of the measured concentrations in water was too large.
Summary
Acute toxicity values are available for 43 species of freshwater
animals and data for eight species indicate chat acute toxicity decreases
as hardness increases. When adjusted to a hardness of 50 mg/L, sensitivities
range from 50.70 ^ig/L for Ceriodaphnia reticulata to 88,960 Mg/L for a
damselfly. Additional data indicate that toxicity increases as temperature
increases. Chronic toxicity data are available for nine freshwater
species. Chronic values for two invertebrates ranged from 46.73 Mg/L for
Daphnia magga to >5,243 Mg/L for the caddisfly, Clistoronia magnifica.
Chronic values for seven fish species ranged from 36.41 rig/L for the flagfish,
Jordanella floridae, to 854.7 (jg/L for the brook trout, Salvelinus fontinalis.
Acute-chronic ratios ranged from 0.2614 to 41.20, but the ratios for the
sensitive species were all less than 7.3.
The sensitivity range of freshwater plants to zinc is greater than
that for animals. Growth of the alga, Selenastrum capricornutum, was
inhibited by 30 Mg/L. On the other hand, with several other species of
30
-------
green algae, 4-day ECSOs exceeded 200,000 Mg/L- Zinc was found to bioaccumulate
in freshwater animal tissues from 51 to 1,130 times the concentration
present in the water.
Acceptable acute toxicity values for zinc are available for 33
species of saltwater animals including 26 invertebrates and 7 fish.
. LCSOs range from 191.5 MgA- for cabezon, Scorpaenichthys marmoratus to
320,400 |Jg/L for adults of another clam, Macoma balthica. Early life
A
stages of saltwater invertebrates and fishes are generally more sensitive
to zinc than juveniles and adults. Temperature has variable and inconsistent
effects on the sensitivity of saltwater invetebrates to zinc. The sensitivity
of saltwater animals to zinc decreases with increasing salinity, but the
magnitude of the effect is species-specific.
A life-cycle test with the mysid, Mysidopsia bahia, found unacceptable
effects at 120 Mg/L» but not at 231 >Jg/L, and the acute-chronic ratio was
2.997. Seven species of saltwater plants were affected at concentrations
ranging from 19 to 10,100 tJg/L. Bioaccumulation data for zinc are available
for seven species of saltwater algae and five species of saltwater animals.
Steady-state zinc bioconcentration factors for the twelve species range
from 3.692 to 23,820.
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 jJg/L) of zinc does not exceed the numerical value given by
31
-------
(0.8473[In(hardness)]+0.7614) more than once every three years on the
e
average and if the one-hour average concentration (in iJg/L) does not
... . (0.8473[ln(hardness)]+0.8604) OT.a
exceed the numerical value given by e more
than once every three years on the average. For example, at hardnesses
of 50, 100, and 200 mg/L as CaC03 the four-day average concentrations of
zinc are 59, 110, and 190 Mg/L, respectively, and the one-hour average
concentrations are 65, 120, and 210 pg/L. If the striped bass is as
sensitive as some data indicate, it will not be protected by this criterion.
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, saltwater aquatic organisms and their uses
should not be affected unacceptably if the four-day average concentration of
zinc does not exceed 86 ^g/L more than once every three years on the
average and if the one-hour average concentration does not exceed 95 \ig/l>
more than once every three years on the average.
"Acid-soluble" is probably the best measurement at present for
expressing criteria for metals and the criteria for zinc were developed
on this basis. However, at this time, no EPA approved method for such a
measurement is available to implement criteria for metals through the
regulatory programs of the Agency and the States. The Agency is
considering development and approval of a method for a measurement such
as "acid-soluble." Until one is approved, however, EPA recommends applying
criteria for metals using the total recoverable method. This has two
impacts: (1) certain species of some metals cannot be measured because
the total recoverable method cannot distinguish between individual oxidation
32
-------
states, and (2) in some cases these criteria might be overly protective
when based on the total recoverable method.
Three years is the Agency's best scientific judgment of the average
amount of time aquatic ecosystems should be provided between excursions
(U.S. EPA 1985b). The resiliencies of ecosystems and their abilities to
recover differ greatly, however, and site-specific allowed excursion
frequencies may be established if adequate justification is provided.
Use of criteria for developing water quality-based permit limits and
for designing waste treatment facilities requires selection of an
appropriate wasteload allocation model. Dynamic models are preferred for
the application of these criteria (U.S. EPA 1985b). Limited data or
other considerations might make their use impractical, in .which case one
must rely on a. steady-state model (U.S. EPA 1986).
33
-------
Table 1. Acute Toxic I ty of Zinc to Aquatic AnlMls
Species Method* Che»lcal
Worm, S, U Zinc chloride
Lumbrlculus varlegatus
Tublflcld worm, S, U Zinc sulfate
Llmnodrllus hoffmelstarl
Worm, S, M
Nals sp.
Snail (embryo), S, M
Amnlcola sp.
Snail (adult), S, M
Amnlcola sp.
Snail (adult), S, U Zinc sulfata
He) Isoma campanulatum
Snail (adult), S, U Zinc sulfate
Hel Isoma campanulatum
Snail (adult), S, U Zinc sulfate
Hal Isoma campanulatum
Snail (adult), S, U Zinc sulfate
Hal 1 soma campanulatum
Snail (adult), F, M Zinc chloride
Physa gyrlna
Snail, S, U Zinc chloride
Physa heterostropha
Hardness
(•g/L as
CaCOO
LC50
or EC50
Adjusted Species Mean
LC50 or EC50 Acute Value
Reference
FRESHWATER SPECIES
30
100
50
50
50
20
(12.8'C)
20
(22.8 *C)
100
(12.8 *C)
100
(22.8 *C)
36
45
(20 *C)
6,300
>2,274
18,400f
20,200f
14,000f
870
1,270
3,030
1,270
1,274
1,800
9,712 9,712
>1,264 >1,264
18,400 18,400
20,200
14,000 16,820
1,891
2,760
1,684
705.9 1,578
1,683 1,683
1,968
Bailey and Liu 1980
Murtz and Bridges
1961
RehMoldt et al . 1973
Rehwoldt et al . 1973
RehMoldt et al . 1973
Wurtz 1962
Wurtz 1962
Wurtz 1962
Wurtz 1962
Nebekar et al . 1986
Cairns and Scheler
1958 b; Academy of Na
C*» lAn/*ne f Q^vA
-------
TabU 1. (Continued)
Ul
Species
Snail,
Physa heterostropha
Sna 1 1 ,
Physa heterostropha
Snail,
Physa heterostropha
Snail (adult).
Physa heterostropha
Snail (adult).
Physa heterostropha
Sna 1 1 ( young) ,
Physa heterostropha
Snail (young).
Physa heterostropha
Snail (young),
Physa heterostropha
Snail (young),
Physa heterostropha
Snail (young),
Physa heterostropha
Snail (young),
Physa heterostropha
Asiatic clam (10-21 mm),
Method*
^^^M«BM*H
S, U
S, U
s, u
s, u
s, u
s, u
s, u
s, u
s, u
s, u
s, u
S. M
Chemical
Zinc chlor Ida
Zinc chloride
Zinc chloride
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfata
Zinc sul fata
Hardness
(•g/L as
CaCO.)
45
(30*C)
170
(20*C)
170
(30*C)
20
100
•
20
(10.6*C)
20
(12.8*Ci
20
(32.2°C)
100
(10.6'C)
100
(12.8*C)
100
(32.2*C)
64
LC50 Adjusted Species Mean
or EC50 LC50 or EC50 Acute Value
(iig/t)** 1
1,000
6,200
7,100
1,110
3,160
303
434
350
434
1,390
1,110
6,040"*
[»fl/D*** (pa/L)****
1,093
2,198
2,517
2,413
1,756
658.6
943.3
760.8
241.2
772.6
'
617.0 1.0B8
4,900 4,900
Reference
Cairns and Scheler
1958b; Academy of
Natural Sciences 1960
Cairns and Scheler
1958b; Academy of
Natural Sciences
1960
Cairns and Scheler
1958b; Academy of
Natural Sciences
1960
Wurtz and Bridges
1961 ; Wurtz 1962
Wurtz and Bridges
1961; Wurtz 1962
Wurtz 1962
Wurtz 1962
Wurtz 1962
Wurtz 1962
Wurtz 1962
Wurtz 1962
Cherry et al . 1980;
t**A**~*- A4- •! 1 QUA
Corblcula flumlnea
Rodgers et al. 1980
-------
Table 1. (Continued)
Species
Cladoceran <<24 hr) ,
Cerlodaphnla dubla
Cladoceran,
Cerlodaphnla retlculata
Cl adoceran.
Cerlodaphnla retlculata
Cl adoceran ,
Cerlodaphnla retlculata
Cl adocaran.
Oaphnla magna
Cladoceran,
Daphnla magna
Cladoceran ,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cl adoceran,
Daphnla reagna
Cl adoceran.
Daphnla magna
Cl adoceran,
Daphnla magna
Cladoceran,
Daphnla pulex
Cladoceran,
Daphnla pulex
Method*
R, M
S, U
S, U
S, M
S, U
S, U
S, M
S, U
S, M
S, M
S, M
F, M
S, M
S, U
Chemical
Zinc chlor Ida
Zinc chloride
Zinc chloride
Zinc chloride
Zinc chloride
Zinc sul fate
Zinc chloride
Zinc chloride
Zinc chloride
Zinc chloride
Zinc sul fate
Hardness
(•g/L as
52
45
45
45
-
45.3
.
45
45
t J *
54
105
196
130
45
45
*t J
IC50
or EC50
«,g/L)"
180
76
41
32
<71.95
100
280
68
334
525
655
798.9
500
107
Adjusted Species Me**
LC50 or EC50 Acute Value
(•oA)*** C»pA.»*"**
174.1 174.1
83.10
44.82
34.99 50.70
-
108.7
306.1
74.35
312.9
280.0
205.8
355.5 355.5
546.7
117.0 252.9
Reference
Carlson at al . 1986
Mount and Norberg
1984
Carlson and Roush
1985
Carlson and Roush
1985
Anderson 1948
Bleslnger and
Christ en sen 1972
Cairns et al . 1978
Mount and Norberg
1984
Chapman at al «
Manuscript
Chapman at al , •
Manuscript
Chapman et al »
Manuscript
Attar and Maty 1982
Cairns et at . 1978
Mount and Norberg
1984
-------
Table 1. (Continued)
Species
1 so pod (3-7 mm) ,
Asel lus blcrenata
1 so pod.
Asel lus communls
1 so pod,
Asel lus communls
1 so pod (3-7 mm) ,
Llrceus alabamae
Am phi pod ,
Cranqonyx pseudoqracl 1 1 s
Am phi pod.
Gammarus sp.
Damsel fl y.
Argla sp.
Bryozoan,
Pectlnatella maqnifica
Bryozoan,
Lophopodella carter 1
Bryozoan,
Plumatella emarqlnata
Method* Che* leal
MWHBWMB^^ ^•^"•"••^^•^••™
F, M Zinc sul fate
S, U Zinc sul fate
S, U Zinc sul fate
F, M Zinc sul fate
R, U Zinc sul fate
S, M
S, U Zinc sul fate
S, U
S, U
S, U
Hardness
img/L as
CaCOm)
220
20
100
152
50
50
20
190-
220
190-
220
190-
220
LC50
or EC50
20,110n
12,734
8,755
8,375ft
19,800
8,100f
40,930
4,310
w
5,630
5,300
«•• f -~-~ ••—
Adjusted
LC5O or EC50
5,731
27,680
4,866
3,265
19,800
8,100
88,960
1,307
1,707
1,607
Species Mean
Acute Value
(.„/!.)••••
5,731
-
11,610
3,265
19,800
8,100
88,960
1,307
1,707
1,607
Reference
Bosnak and Morgan
1981
Wurtz and Bridges
1961
Wurtz and Bridges
1961
Bosnak and Morgan
1981
Martin and Holdlch
1986
RehMoldt et al. 1973
Wurtz and Bridges
1961
Pardue and Wood 1980
Pardue and Wood 1980
Pardue and Wood 1980
-------
Table 1. (Continued)
Method-
_E2Ł
American eel , S, M
Angul 1 la rostrata
American eel, S, M
Anqull la rostrata
Coho salmon (yearling), R, M
Oncorhynchus klsutch
Coho salmon, F, M
Oncorhynchus klsutch
Sockeye salmon (parr), F, M
Oncorhynchus nerka
Chinook salmon (alevln), F, M
Oncorhynchus tshawytscha
Chinook salmon (juvenile), F, M
oo Oncorhynchus tshawytscha
Chinook salmon F, M
(swim-up alev In) ,
Oncorhynchus tshawytscha
Chinook salmon (parr), F, M
Oncorhynchus tshawytscha
Chinook salmon (smolt), F, M
Oncorhynchus tshawytscha
Cutthroat trout R» M
( finger 1 Ing),
Salmo clarkl
Rainbow trout (juvenile), F, M
Salmo qalrdneri
Rainbow trout (juvenile), F, M
S a 1 mo qalrdneri
Rainbow trout (30.5 g) , F, M
S a Imo qalrdneri
Rainbow trout (22.6 g) , F, M
Salmo qalrdneri
Che* leal
Zinc nitrate
Zinc chloride
Zinc chloride
Zinc chloride
Zinc chloride
Zinc sul fate
Zinc chloride
Zinc chloride
Zinc chloride
Zinc sul fate
Zinc sul fate
Zinc sul fate
Zinc sul fate
Zinc sul fata
Hardness
(•g/L as
CaCOjl
55
53
94
25
22
23
21
23
23
23
-
330
25
30
30
LC50
or EC50
14,500*
14,600f
4,600
905
749
>661ftt
84
97
463
701
90*
7,210
430
430
810
Adjusted Species Mean
LC50 or EC50 Acute Value
13,380
13,900 13,630
2,694
1,628 1.628
1,502 1,502
'
175.2
187.3
894.0
1,354 446.4
• "
1,457
773.6
662.9
1 , 249
Reference
Rehwoldt et al . 1972
Rehwoldt et al . 1973
Lorz and McPherson
1976,1977
Chapman and Stevens
1978
Chapman 1975,1978a
Chapman 1975J978b
Flnlayson and Verrue
1982
Chapman 1975J978b
Chapman 1975,1978b
Chapman 1975,t978b
Rabe and Sapping ton
1970
Slnley et al . 1974
Sjnley et a! , 1974
Goettl et al . 1974
Goettl et al . 1974
-------
TabU 1. (Continued)
Species
Rainbow trout (29.7 g) ,
Salmo galrdnerl
Rainbow trout (18.3 o>
Rainbow trout (2.0 g) ,
S a 1 mo galrdnerl
Rainbow trout (34.6 g),
Salmo galrdnerl
Rainbow trout (4.9 g).
S a 1 mo galrdnerl
Rainbow trout (52.1 g).
S a 1 mo galrdnerl
Rainbow trout (15.4 g) ,
S a 1 mo qalrdnerl
Rainbow trout (72 g) ,
Salmo galrdnerl
Rainbow trout (juvenile).
Salmo galrdnerl
Rainbow trout (alevln).
Salmo galrdnerl
Rainbow trout
(swim-up alev In) ,
Salmo galrdnerl
Ra Inbow trout ( parr) ,
Salmo galrdnerl
Rainbow trout (smolt),
Salmo galrdnerl
Rainbow trout (adult male).
Method*
F,
F.
F,
F,
F,
F,
F,
F,
R,
F,
F,
F,
F,
F,
M
M
H
M
M
M
M
M
U
M
M
M
M
M
Chwlcal
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
chloride
chloride
chloride
chloride
chl orlde
Hardness
(•g/L as
CaCOO
30
317
312
23
22
30
314
102
5
23
23
23
23
83
UC50 Adjusted Species Meen
or ECM LC50 or BC50 Acute Value
(ng/L)** (»qA.)***
410 632.1
4 S70
-------
Table 1. (Continued)
Species
Rainbow trout (juvenile),
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo qalrdnerl
Rainbow trout (Juvenile),
Salmo galrdnerl
Ra 1 nbow tro ut ( j uv en 1 1 e) ,
Salmo galrdnerl
Rainbow trout (juvenile),
Salmo galrdnerl
Rainbow trout (Juvenile),
Salmo galrdnerl
Rainbow trout ( f Ingerl Ing),
Salmo galrdnerl
Ra Inbow trout ( fry) ,
Salmo galrdnerl
Atlantic salmon (parr),
Salmo salar
Brook trout (Juvenile),
Salvel Inus fontlnal Is
Brook trout (juvenile),
Salvel Inus fontlnal Is
Brook trout (Juvenile),
Salvel Inus fontlnal Is
Brook trout (juvenile),
Salvel Inus fontlnal Is
Brook trout (juvenile).
Method*
F, M
F, M
F, M
FM
t n
F, M
F, M
S, M
F, M
F, M
F, M
F, M
F, M
F, M
F, M
Chemical
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sul fate
Zinc sulfate
Zinc chloride
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Hardness
(mg/L as
46.8
47.0
44.4
178
179
170
14
9.2
(pH=7.0)
14
46.8
47.0
44.4
178
179
LC50
or ECSO
(»g/L)**
370
517
756
2,510
2,960
1,910
560
66
740
1,550
2,120
2,420
6,140
6,980
Adjusted Species Mean
LC50 or ECSO Acute Value
(»q/L)*** (.flA)****
391.3
544.8
836.0
855.9
1,005
677.2
1,647
277.0 689.3
2,176 2,176
1,639
2,234
2,676
2,094
2,369
SalvelInus fontlnalIs
Reference
Hoicombe and Andrew
1978
Hoi combe and Andrew
1978
Hoi combe and Andrew
1978
Hoicombe and Andrew
1978
Hoicombe and Andrew
1978
HoIcombe and Andrew
1978
Spry and Mood 1984
Cuslmano et al . 1986
Carson and Carson 1972
Ho I combe and Andrew
1978
Hoi combe and Andrew
1978
Ho I com be and Andrew
1978
Ho I com be and. Andrew
1978
Ho I con be and Andrew
1978
-------
Table 1. (Continued)
Species
Brook trout (juvenile).
Salvel Inus fontlnalls
Longfln dace (juvenile).
Aqosla chrysogaster
Goldfish,
Car ass (us auratus
Goldfish (1-2 g).
Carasslus auratus
Common carp «20 cm).
Cyprlnus carplo
Common carp,
Cyprlnus carplo
Common car p ( 2 . 1 g) ,
Cyprlnus carplo
Golden shiner.
Notemlqonus crysoleucas
Fathead minnow (embryo).
P Imephales promelas
Fathead minnow (embryo),
P Imephales promelas
Fathead minnow (fry).
P Imephales promelas
Fathead minnow (1-2 g) ,
Method*
F,
R,
S,
S,
s.
s.
R,
S.
F.
F.
F,
s.
M
M
U
U
M
M
U
U
M
M
M
U
Che* leal
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
sul fate
sul fate
sul fate
sul fate
n 1 tr ate
-
sul fate
sul fate
sul fate
sul fate
sul fate
su 1 fa te
Hardness
(wg/L as
CaCO}>
170
217
50
20
53
55
19
50
174-
198
174-
198
174-
198
20
LC50
or EC50
(»o./L)**
4,980
790f
7,500
6,440
7,800"*
7,800f
3,120
6.000
1,820
1,850
870
2,550
Adjusted Species Mean
LCSO or EC50 Acute Value
(»g/L)*** (ji^/L)****
1,766 2,100
227.8 227.8
7,500
14,000 10,250
7,424
7,194
7,083 7,233
6,000 6,000
599.0
608.9
286.3
5,543
PImephales promelas
Reference
HoIcombe and Andrew
1978
Lewis 1978
Cairns et al. 1969
Pickering and Henderson
1966
Rehwoldt et al . 1971
Rehwoldt et al . 1972
Khangarot et al . 1983
Cairns et al. 1969
Pickering and Vigor
1965
Pickering and Vigor
1965
Pickering and Vigor
1965
Pickering and Henderson
1966
-------
Table 1. (Continued)
M
Species
Fathead minnow (1-2
P Imephales promejas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
P Imephales promelas
Fathead minnow (1-2
Method*
g»
g).
g).
g).
g>.
g).
g).
g),
g).
g).
g>.
s.
s.
s.
s.
F,
F,
F,
F,
F,
F,
F,
U
U
U
U
M
M
M
M
M
M
M
Chemical
_
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
sul fate
Hardness
(«g/L as
CaCOj)
20
(15"C)
20
(25'C>
20
(25*C)
360
(25*C)
63
54
97
103
212
208
54
LC50
or EC5O
(Mg/L)**
2,330
770
(780)
960
33,400
1 2, 500
13,800
18,500
25,000
29,000
35,500
13,700
Adjusted
LC5O or EC50
<»9/
5,
1,
2,
6.
10,
12,
10,
!)»•»
064
674
087
271
280
930
550
13,550
8,
10,
12,
528
610
840
Species Mean
Acute Value
(pg/L)**** Reference
Pickering and
1966
Pickering and
1966
Pickering and
1966
Pickering and
1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Henderson
Henderson
Henderson
Henderson
PImephales promelas
-------
Table 1. (Continued)
Species
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (1-2 g) ,
P 1 mepha 1 es prome I as
Fathead minnow (1-2 g) ,
P Imephales prome las
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (1-2 g) ,
P Imephales promelas
Fathead minnow (44.6 mm) ,
Method*
F.
F,
F,
F.
F,
F,
F,
F,
F,
F,
F,
s.
M
M
M
M
M
M
M
M
M
M
M
U
Chenlcal
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
sul
sul
sul
sul
sul
sul
sul
sul
sul
sul
sul
sul
fate
fate
fate
fate
fate
fate
fate
fate
fate
fate
fate
fate
Hardness
(•g/L as
CaC03)
63
100
99
186
195
54
49
98
102
193
216
166
LC50
or ECSO
Adjusted
LC50 or EC50
***
6
12
12
19
13
4
5
a
9
8
15
7
,200
,500
,500
,000
,600
,700
,100
,100
,900
,200
,500
,630
5.
6.
7,
6,
4,
4,
5.
4.
5.
2.
097
948
007
242
293
403
188
580
411
611
4,486
2.
760
Species Mean
Acute Value
(»g/L>**** Reference
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Mount 1966
Rachlln am
PImephales promelas
Par Im utter 1968
-------
GO
r-
!
. *
* 1
Ł •-
m
O)
CD
in
_•
I
•o
3
1
us
3 '
* i
1 *
k a
ss -
&* c5
Carlson
3
in
2
•o
$.
1 1
in
2
i
»•
1
§
1
o
s
ro*
3
m
CM
in
8
in
_ _ vO
in
o
10*
s a
o
IO
s
CO
CM
CM
O
O
o
8
o
«
(M
§
O
o
S
8 2
— >O
o> in
10 m
IS
(3V
8
CM
Hardness
(•g/L as
aCOO
8
CM
8
8
(N
8
CM
O
esi
CM
! «
P
^~
Ł
"3
in
8
0
(0
•^
"3
in
o
c
-2
2
3
in
0
^_
Ł
3
in
o
c
^
>^
"3
in
0
0
^
(0
•^
"3
in
|
Ł
(0
•^
"3
in
U
c
0
*
€
u
c
0
2
fc
u
u
c
0
2
c3
u
u
c
«
•O
U
c
0)
T3
I.
o
u
c
^
i
^^
«
I
TS
N 'o
,8
|k
— in
E _0
•o 15
e Ł
0 CL
Ł 9
4- e
10 —
U.Q.
rr\ in
I (3
CM —
— in
E 0
•»_
0 O
Ł F
•t- E
10 —
U-CL
I
CM
E
*'.
U.Q.
M
O
e
H'.
|
B '
Fathead
Fathead
5 in
10
ikj
Ł«•
E 0
Fathe
P Imep
C *
S (0
X O
o *-
c a
c
1 S
•3 (O
fi J=
10 —
u. a.
CM «
V ^
X O
1^1
he
Fat
P mep
r fc
I J
in ^T —
0 0
c — Ł
I. — O
isi
t 3^
O -i+-
z^ a.
in
in
0
o
Ł1
in „ —
0 o
C — Ł
V. —
0 -
2«-Q.
X
§
1. O
3 B
in o
0 in
44
-------
TabU 1. (Continued)
Hardness
(•g/L as
Species Method* Chenlcal CaCO?)
Banded kllllflsh «20 cm), S, M Zinc nitrate 53
Fundulus dlaphanus
Banded kllllflsh, S, M - 55
Fundulus dlaghanus
Flagflsh (juvenile), F, M Zinc sul fate 44
Jordanella florldae
Guppy (6 mo), S, U Zinc sul fate 20
Poecllla retlculata
Guppy, S, U Zinc sul fate 120
Poecll la retlculata
Guppy ( fry) , S, M Zinc sul fate 30
Poecllla retlculata
Guppy (adult male), S, M Zinc sul fate 30
.*: Poecll la retlculata
Guppy (adult female), S, M Zinc sul fate 30
Poecllla retlculata
Guppy (adult male) , S, U Zinc sulfate 118
Poecllla retlculata
Guppy (adult female), S, U Zinc sulfate 118
Poecllla retlculata
Southern platyflsh S, U Zinc sulfate 166
(20.8 mm),
Xlphophorus maculatus
White perch «20 cm), S, M Zinc nitrate 53
Morone amerlcana
White perch, S, M - 55
Morone amerlcana
Striped bass ( finger 1 Inq) , S, M Zinc nitrate 53
LC30 Adjusted
or ECSO LC50 or ECSO
19.1001" 18,180
I9,200f 17,710
1,500 1,672
1,270 2,760
30,000 14,290
1,740 2,682
5,050 7,785
6,400 9,866
300,000tftt
278,000tm
12,000 4,341
14,300f 13,610
14,400f 13,280
6,70oMttt .
Acute Value
(pg/L)**** Reference
Rehwoldt et al . 1971
17,940 Rehwoldt et al . 1972
1,672 Spehar 1976a,b
Pickering and Henderson
1966
Cairns et al . 1969
Pier son 1981
PI arson 1981
Plerson 1981
Sehgal and Sax en a
1 9oo
6,053 $8&8a' *** Saxena
4,341 Rachl In and Perl mutter
1968
Rehwoldt et al . 1971
13,450ttttf Rehwoldt et al . 1972
Rehwoldt et al . 1971
Morone saxatlI Is
-------
TabU 1. (Continued*
3P**'**
Striped bass,
Morone saxat Ills
Striped bass (63 d) ,
Morone saxat 1 1 Is
Striped bass (63 d) ,
Morone saxat Ills
Pumpklnseed (<20 cm).
Lepomls qlbbosus
Pumpkin seed ,
Lepomls qlbbosus
Blueqlll (3.5-3.9 g) ,
Lepomls macrochlrus
Blueglll (3.5-3.9 g) ,
Lepomls macrochlrus
Blueglll (3.5-3.9 g),
Lepomls macrochlrus
Blueglll (3.5-3.9 g) ,
Lepomls macrochlrus
Blueglll (2.5-3.9 g) ,
l.epomls macrochlrus
Blueglll (0.96 g).
Lepomls macrochlrus
Biueglll (2.80 g) ,
Lepomls macrochlrus
Hardness
(«g/L as
Uff-HshH* nh^alcal C0CQ»J
- S«i
S, M - 3D
S, U Zinc chloride 40
S, U Zinc chloride 285
S, M Zinc nitrate 53
c u - 55
S, M ~ -'-'
S. U Zinc chloride ^45^
S, U Zinc chloride ^45^
S. U Zinc chloride 170
' (18*0
S U Zinc chlor Ide 170
(30*C>
S, U Zinc chlor Ide 45
F, M Zinc chloride 45
F, M Zinc chlor Ide 45
LC50 Adjusted Species MMM
or EC50 LCSO or BCSO Acute Value
t«a/Ll»* (BaA.)*** (•fl/LI**11* Reference
6 aoot,tttt - - Rehwoldt et al .
' 1972
120 145.0 - Palawskl et al . 1985
430 98.40 119.4 Pal awskl et al . 1985
20,000* 19,040 - Rehwoldt et al . 1971
20,100* 18,540 18,790 Rehwoldt et al . 1972
. 7nn 4 592 - Cairns and Scheler
4,200 4.3« 195^ 1968. AcadaBy Qf
Natural Sciences 1960
, 500 3 827 - Cairns and Scheler
3,500 J,«*' 1957j Academy Qf Natural
Sciences 1960
,9 QOO 4 574 - Cairns and Scheler
12,900 4,3/4 J957; Acad
-------
Table 1. (Continued}
Species
Blueglll (54.26 g) ,
Lepomls macrochirus
Blueglll (1-2 g).
Lepomls macrochirus
Blueglll (1-2 g).
Lepomls macrochirus
Blueglll (1-2 g) ,
Lepomls macrochirus
Blueqlll (1-2 g).
Lepomls macrochirus
Blueglll (1-2 g).
L epom 1 s macroch 1 rus
Slueglll (1-2 g).
Lepomls macrochirus
Blueglll ,
Lepomls macrochirus
Blueglll,
Lepomls macrochirus
Mozambique tllapla (18 g) ,
Method*
F, M
S, U
S, U
S, U
S, U
S, U
S, U
F, M
F, M
S, U
Chemical
Zinc chlor Ide
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc sulfate
Zinc chloride
Zinc sulfate
Zinc sul fate
Zinc sulfate
Zinc chloride
Hardness
(•g/L as
CaCO?>
45
20
(15*C)
20
(25*C)
20
(25*C)
20
(25"C>
20
(25*C)
360
(25*C)
46
46
115
LC50 Adjusted Species Mean
or EC50 LC50 or EC50 Acute Value
3,314
6,440
5,460
4,850
5,820
5,370
40,900
9,900
12,100
1,600tf
3,623
14,000
11,870
1 0, 540
12,650
1 1 ,670
7,679
10,620
12^990 5,937
790.0 790.0
Tllapla mossamblca
Reference
Cairns and Scheler
1959
Pickering and Henderson
1966
Pickering and Henderson
1966
Pickering and Henderson
1966
Pickering and Henderson
1966
Pickering and Henderson
1966
Pickering and Henderson
1966
Cairns et al . 1971
Cairns et al . 1971
790.0 Qureshl and Saksena
1980
-------
Table 1. (Continued)
Species
Polychaete worm (juvenile),
Neanthes arenaceodentata
Polychaete worm (adult),
Neanthes areanceodentata
Polychaete worm (adult),
Nereis divers I col or
Polychaete worm (adult),
Nereis diversicol or
Polychaete worm (adult),
Nereis dlverslcolor
Polychaete worm (adult),
Nereis vlrens
Polychaete worm (adult),
Ophryotrocha dladema
Polychaete worm (adult),
Ctenodrllus serratus
Polychaete worm (larva),
Cap I tell a capltata
Polychaete worm (adult),
Cap I tell a capltata
Mud snalI (adult),
Nassarlus obsoletus
Blue mussel,
Mytil us edulls planulatus
Blue mussel,
Mytllus edulIs planulatus
Blue mussel ,
ptanulatus
Method*
Salinity
Cheat cat . (g/kg)
LC50
or EC50
Species Moan
Acute Value
(M9/L>«**
Reference
SALTWATER SPECIES
S, U
S, U
R, U
R. U
R, U
S. U
s. u
S. U
S, U
S, U
S, U
R, M
F. M
F, M
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
• Zinc
Zinc
Zinc
sul fate
su 1 f ate
sul fate 0.35
sul fate 3.5
sul fate 17.5
ch 1 or 1 de 20
sul fate
sul fate
su 1 f ate
sul fate
chloride 20
chloride 34
(21 °C)
chloride
cHlorlde
900
1,800
1.500
11,000
55,000
8,100
1,400
7,100
1.700
3,500
50,000
2,500
3,600
4,300
-
1,273
-
-
9,682
8,100
1,400
7,100
-
2,439
50,000
-
-
3,934
Relsh et al. 1976
Relsh et al. 1976
Bryan and Hummerstone
1973
Bryan and Hummers tone
1973
Bryan and Hummerstone
1973
Elsler and Hennekey
1977
Relsh and Carr 1978
Relsh and Carr 1978
Relsh et al. 1976
Relsh et al . 1976
Elsler and Hennekey
1977
Ahsanul lah 1976
Ahsanu! !ah 1976
Ahsanul lah 1976
ua'c)
-------
Table 1. (Continued)
Species
Pac 1 f 1 c oyster ( embryo) ,
Crassostrea qlqas
Pacific oyster (embryo),
Crassostrea qlqas
Eastern oyster (embryo).
Crassostrea virgin lea
Eastern oyster (embryo),
Crassostrea virgin lea
Eastern oyster (embryo),
Crassostrea virgin lea
Eastern oyster (embryo).
Crassostrea vlrglnlca
Clam (adult) ,
Macoma balthlca
Clam (adult).
Macoma balthlca
Clam (adult),
Macoma balthlca
Clan (adult) ,
Macoma balthlca
Clan (adult) ,
Macoma balthlca
Clam (adult) ,
Macoma balthlca
Clam (adult) ,
UAS~ssma K»l+hlf»Jk
Met1""!*
s.
s,
s,
s.
s.
s.
s.
s,
s.
s.
s.
s.
s.
M
M
U
U
U
U
U
u
u
u
u
u
u
Chemical •
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
chloride
chloride
chloride
chloride
chloride
chloride
sulfate
sul fate
sul fate
sul fate
sul fate
sul fate
sulfate
Salinity
(a/kg)
30
25
26
26
(25 C)
26
1 XA •/"* \
13U L.I
1.5
(5"C)
25
(5*C)
35
1 C •("» \
(5 C)
15
(10*C)
25
(10-C)
35
(10'C)
15
(15'C)
LC50 Species Nean
or EC50 Acute Value
~~ Ma* " *.««.<»«• •* _ ,* ^ — ^—— _.
263.5*«»*»
206.5
310
205.7
324.5
229.6
140,000
700.000
750,000
210,000
900.000
950.000
60,000
|»g/Ll""" Kerei wn.m
Nelson 1972
233.3 Olnnel et al ,
Calabrese et
Maclnnes and
1978
Maclnnes and
1978
262.5 Maclnnes and
1978
Bryant et al
Bryant et al
Bryant et al
Bryant et al
Bryant et al
Bryant et al
Bryant et al
, 1983
al. 1973
Calabrese
Cal abrese
Calabrese
. 1985
. 1985
. 1985
. 1985
. 1985
. 1985
. 1985
-------
Table 1. (Continued)
Species
Clam (adult),
Macoma balthlca
Clam (adult),
Macoma balthlca
Quahog clam (embryo),
MercenarI a mercenarI a
Soft-shelI clam (adult),
Mya arenarla
Soft-shell clam (adult),
Mya arenarla
Squid (larva),
Loll go opalescens
Copepod (adult),
Eurytemora afflnls
Copepod (adult),
Acartla clausl
Copepod (adult),
Acartla tonsa
Copepod (adult),
Nltocra splnlpes
Mysld (juvenile),
Mysldopsls bahI a
Mysld (juvenile),
Mysldopsls bah I a
Mysld (juvenile),
Mysldopsls bahla
Method*
s.
s.
s,
s.
s.
s.
s.
s,
s.
s.
s.
s.
F.
u
u
u
u
u
M
U
U
U
u
M
M
M
Chemical
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
sul fate
sul fate
chloride
ch 1 or 1 de
chloride
chloride
chloride
chloride
ch 1 or 1 de
chloride
ch 1 or 1 de
ch 1 or 1 de
chloride
Salinity
»*
180,000
250,000
195
7,700
5,200
>1,920
4,074
1,507
294.2
1,450
520.8
547.2
499
Species Mean
Acute Value
(Mfl/L)*** Refere*
Bryant
320,400 Bryant
ce
et al. 1985
et al. 1985
195 Calabrese and Nets*
1974
Elsler
1977
and Henneke]
6,328 Elsler 1977a
>1,920 Dlnnel
4,074 Lussier
1985
1,507 Lussier
1985
294.2 Lussier
1985
et al. 1983
and Card In
and Card In
and Card In
1,450 Bengtsson 1978
Lussier
1985
Lussier
1985
499 Lussier
and Gentlli
and Gent HI
et al. 198!
-------
Table 1. (Continued)
Species
Method"
Mysld (juvenile) ,
s.
H
Che* leal
Zinc
chloride
Salinity
(g/kg)
30
LC50
or EC50
(»g/L)*»
591.3
Specie* NMMI
Acute Value
<»Q/L)M»
591 .3
Mysldopsls blgelowl
Am phi pod
Coroph 1 urn
Am phi pod
Coroph 1 urn
Am phi pod
Coroph (urn
Am phi pod
Corophlum
Am phi pod
Corophlum
Am phi pod
Corophlum
Am phi pod
Corophlum
Am phi pod
(adult).
volutator
(adult).
vo 1 utator
(adult).
volutator
(adult).
volutator
(adult),
vo 1 utator
(adult),
volutator
(adult),
vo 1 utator
(adult).
s.
s.
S.
s.
S.
S.
s,
s,
U
U
U
U
U
U
U
U
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
sul
sul
sul
sul
sul
sul
,
sul
sul
fata
fate
fate
fate
fate
fate
fate
fate
Corophlum volutator
Am phi pod
Corophlum
Am phi pod
(adult),
volutator
(adult).
S,
s.
U
U
Zinc
Zinc
sul
sul
fate
fate
Corophlum volutator
Am phi pod
(adult) ,
s,
U
Zinc
sul
fate
Coroph 1 urn volutator
Am ph I pod
Coroph 1 urn
(adult).
vo 1 utator
s.
U
Zinc
sul
fate
5
(5*C)
10
(5*C)
15
(5*C)
25
(5*C)
35
(5*0
5
(10»C)
10
(10'C)
15
(10 *C)
25
(10 'O
35
(10 *C)
5
(15*C)
10
(15*C)
1.
4,
6,
12,
16.
>128,
1.
8,
11.
15,
1.
3.
000
600
500
000
000
ooomt
600
500
000
000
100
200
-
-
-
-
-
'_
-
-
-
-
-
-
Reference
Lussler and Gentile
1985
Bryant et al. 1965
Bryant et al. 1985
Bryant et al. 1985
Bryant et al. 1985
Bryant et al. 1985
Bryant et al. 1985
Bryant et al. 1985
Bryant et al . 1985
Bryant et al. 1985
Bryant et al. 1985
Bryant et al. 1985
Bryant et al. 1985
-------
Table 1. (Continued)
Species
Amphlpod (adult),
Corophlum volutator
Amphlpod (adult),
Corophlum volutator
Amphlpod (adult),
Corophlum volutator
Lobster (adult),
Homarus amerlcanus
Lobster (larva),
Homarus amerlcanus
Lobster ( larva),
Homarus amerlcanus
Lobster (larva),
<~n Homarus amerlcanus
Lobster (larva),
Homarus amerlcanus
Hermit crab (adult),
Pagurus long I carpus
Dung en ass crab ( larva) ,
Cancer maglster
Green crab ( larva) ,
Carclnus maenas
Starfish (adult),
Aster I as forbeslI
Mummlchog (adult),
Fundulus heteroclItus
Munmlchoq (adult) ,
Fundulus heteroclItus
Method*
s.
s.
s,
F,
s,
s.
s.
s.
s.
s.
s.
s,
s.
s,
u
u
u
u
u
u
u
u
u
H
u
u
u
u
Che* leal
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
Zinc
sul fate
sul fate
sul fate
sul fate
chloride
chloride
chloride
chloride
chloride
chloride
sul fate
chloride
chloride
chloride
Salinity
Cg/kg)
15
25
(15*C)
35
(15*C)
-
30
30
30
30
20
30
-
20
6.1
24
LC50
or EC50
3,400
4,400
3,600
48,000**
575
574.5
362.5
175
400
586.1
1,000
39,000
17,500
31,500
Specie* Mean
Acute Value
(*g/L)*** Reference
Bryant et al
Bryant et al
4,683 Bryant et al
Hay a et al .
Johnson 1985
Johnson 1985
Johnson 1985
380.5 Johnson 1985
400 Elsler and H
1977
586.1 Olnnel et al
1,000 Connor 1972
39,000 Elsler and H
1977
Dorfman 1977
Dorfman 1977
. 1985
. 1985
. 1985
1983
en n eke
. 1983
enneke
-------
Table I. (Continued)
Species
Mummlchog (adult),
Fundulus heterclltus
Mummlchog (adult),
Fundulus heteroclltus
Mummlchog (adult),
Fundulus heterclltus
Mummlchog (larva),
Fundulus heteroclltus
Atlantic sllverslde
(2-wk larva),
Men Id la men Id la
Atlantic sllverslde
(newly hatched larva),
Men Id la men Id la
Atlantic sllverslde
(newly hatched larva),
Men Id la menldla
Atlantic sllverslde
(newly hatched larva),
Men Id la menldla
Atlantic sllverslde
(newly hatched larva),
Menldla menldla
Tidewater sllverslde
(juven lie),
Menldla penlnsulae
Striped bass (63 day),
Morone saxatIlls
Spot ( juven lie) ,
Leiostomus xantnurus
Method*
s. u
s, u
s, u
s. u
s, u
s, u
s, u
s, u
s, u
Salinity
Chemical (g/kg)
Zinc sulfate 6.0
Zinc sulfate 22.9
Zinc chloride 20
Zinc chloride 30
Zinc chloride 31.2
Zinc chloride 30
Zinc chloride 30.2
Zinc chloride 30
Zinc chloride 30
LC50
or EC50
(ng/L)"
32,000
27,500
60,000
6(3,040
4,960
4,170
3,703
3,060
2,728
Species Mean
Acute Value
(»q/L)**" Reference
Dorfman 1977
Oorfman 1977
Elsler and H
1977
36,630 Card In 1985
Card In 1965
Card In 1985
Card In 1985
Card In 1985
3,640 Card In 1985
S, U
Zinc sulfate
Zinc chloride
Zinc sulfate
20
I
25
5,600
430
38,000
5,600
430
38,000
Han sen 1983
Palawskl et al .
1985
Hansen 1983-
-------
TabI* 1. (Continued)
Cabezon ( larva) ,
Scorpaenlchthys marmoratus
Winter flounder (larva),
Pseudopleuronectes amerlcanus
Winter flounder (larva),
P seudop 1 euronectes amer 1 can us
Method*
S. M
S, U
S. U
« S = static; R = renewal; F = flow-through
** Results are expressed as zinc, not as the
«»» Freshwater LC50s and EC50s were adjusted
ChealcaL
Zinc chloride
Zinc chloride
Zinc ch.or.de
; M - measured
chemical .
to hardness =
Sellnlty
27
30
30
; U = measured.
50 mg/L using the
LC50 Species NMH
or EC50 Acute Value
191.4 191.4
18,207
4.922 9,467
pooled slope of 0.8195 (see text).
»c +Ka hjtrrlna^c -
Reference
Dlnnel et al . ,983
Card In 1985
Card In 1985
When the hardness Is
a range, the geometric mean of the I
*«»» Freshwater Species Maan Acute Values were calculated at hardness = 50 mg/L.
»»»»« Calculated by problt analysis of the authors' data.
* In river water or stream water.
tf Average of values calculated using two different methods.
tft Value not used in calculation of slope or Species Mean Acute Value because this was . "greater than" value and a number of other
values are available for this species.
tttt value not ^ ,„ ca.cu.atlon of slope or Spec.es Mean Acute Value because va.ue appeared to be high In comparison with other values
available for this species.
ttm Not used In calculation of Genus Maan Acute Value (see text).
t« Va,ue not used In calculation of Spec.es Mean Acute Value because data are callable for a more sensitive life stage.
-------
Table 1. (Continued)
Results of Covarlance Analysis of Freslwater Acute Toxicltv versus Hardness
Ul
Ul
Species
n
Physa heterostropjia 12
Daphn la magna
Ra Inbow trout
Brook trout
Fathead minnow
Guppy
Striped bass
Bl ueq 1 1 1
Al 1 of above
7
25
6
36
5
2
16
109
Slope Standard Deviation
0
1
0
0
0
1
.9296
.2549
.8755
.8179
.8310
.6441
0
0
0
0
0
0
.2590
.4026
.1152
.1243
.2217
.4432
951 Confidence LI* Its
0.3521,
0
0
0
0
0
.2206,
.6370,
.4731,
.3802,
.2323,
1
2
1
1
1
.5071
.2892
.1140
.1627
.2818
3.0559
0.6500 -* -* , -*
0
0
.5603
.8473««
0
0
.1461
.0866
0.2467,
0
.6754,
0
1
.8739
.0192
Degrees of Freedom
10
5
23
4
34
3
0
14
100
* Standard deviation and confidence limits cannot be calculated because degrees of freedom =• 0.
•» P = 0.77 for equality of slopes.
-------
Table 2. Chronic ToxicIty of Zinc to Aquatic Anlaals
Hardness
(MQ/L as Limits
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran ,
Daphnla magna
Caddlsfly,
C 1 1 storon 1 a maqn 1 f 1 ca
Sockeye salmon,
Oncorhynchus nerka
Chinook salmon,
Oncorhynchus tshawytscha
Rainbow trout.
Salmo galrdner j
Rainbow trout.
S a 1 mo qalrdner 1
Brook trout.
Salvel Inus fontlnal Is
Fathead minnow.
Plmephales promelas
Flag fish.
Jordanella florldae
Guppy,
Pnacllla retlculata
Test*
LC
LC
LC
LC
LC
ELS
ELS
ELS
ELS
LC
LC
LC
LC
Chemical
Zinc
chloride
Zinc
chlor Ide
Zinc
chlor Ide
Zinc
chlor Ide
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
sul fate
Zinc
chlor Ide
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
CaCO,)
FRESHWATER
45
52
104
211
31
32-37
25
26
25
45.9
46
.44
30
(uq/L)««
SPECIES
<140.3t
97-190
43-52
42-52
>5,243ft
>242n
270-510
140-547
444-819
534-1,368
78-145
26-51
<173f
Chronic Value
(iiq/L)
<140.3
135.8
47.29
46.73
>5,243
>242
371.1
276.7
603.0
854.7
106.3
36.41
<173
Reference
Bleslnger et al .
f QQ4L
I9OO
Chapman et al .
Manuscript
Chapman et al „
Manuscript
Chapman et al •
Manuscript
Nebeker et al .
1984
Chapman 1978a
Chapman 1975
Slnley at al . t974
Cairns at al «, 1982
Hoi combe at al . 1979
Benoit and Hoi com be
1 070
1 7/O
Spenar S976asb
PI arson 1981
-------
TabU 2. (Continued)
Spaclas
Mysld.
Mysldopsls bahla
Tast* ChaMlcal
LC Zinc
chlor Ide
Hardness
tmg/L as Halts Chronic Valu*
SALTWATER SPECIES
30m 120-231 166.5
Rafaraaca
Lussler at al .
1985
* LC = life-cycle or partial life-cycle; ELS = early life-stage.
** Results are based on measured concentrations of zinc.
* Unacceptable effects occurred at all concentrations tested.
tt
The highest concentration tasted did not cause unacceptable effects.
ttf salinity (g/kg), not hardness.
-------
Table 2. (Continued)
Acute-Chronic Ratio
Hardness
Species
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Sockeye salmon.
Onchohynchus nerka
Chinook salmon
Oncorhynchus tshawytsgha
Rainbow trout.
S a 1 mo qalrdner 1
Brook trout.
Salvellnus fontlnal Is
Fathead minnow.
Plmephales promelas
F 1 aq f 1 sh ,
Jordanel la f lor Idas
Mysld,
Mysldopsls bah la
(•g/L as Acute Veloe
CaCOx) (MQ/L)
52-54 ^334
104-105 525
196-211 655
32-37 1,470
23-25 97-701*
25-26 430
45.9 1,996**
46 600
44 1 , 500
30*** 499
Chronic Value
(»g/L)
135.8
47.29
46.73
>242
371.1
276.7
854.7
106.3
36.41
166.5
Ratio
2.459
11.10
14.02
<6.074
0.2614
1 .889
1.554
2.335
5.644
41.20
2.997
* Range of values given In Chapman (1975,1978a> for Juveniles.
*» Geometric mean of three values In Table I from Ho I combe and Andrew
»*» Salinity (g/kg).
(1978).
-------
Table 3. Ranked Genus NMM Acute Values tilth Species NMW Acute-Chronic Ratios
Rank*
«B^HW^M»
35
34
33
32
31
30
Ol
VO
29
28
27
26
Genus Mean
Acute Value
t.g/L)*"
88,960
19,800
18,400
17,940
16,820
13,630
10,560
10,250
9,712
8,157
Species
FRESHWATER SPECIES
Dam set fly,
Argia sp.
Am phi pod,
Crangonyx pseudogracl 1 Is
Worm,
Nal^ sp.
Banded kill Iflsh,
Fundulus dlaphanu^
Snail ,
Amnlcola sp.
American eel ,
Angull la rostrata
Pumpkin seed ,
Lepomls glbbosus
Bluegll 1,
Lepomls macrochlrus
Goldfish,
Carasslus auratus
Worm,
Lumbrlculus varlegatus
Iso pod,
A sell us blcrenata
1 so pod ,
Species Mean
Acute Value
(nfl/L)*"*
88.960
19,800
18,400
17,940
16,820
13,630
18,790
5,937
10,250
9,712
5,731
11,610
Species Mean
Acute-Chronic
Ratio****
-
-
-
-
-
-
AselI us communls
-------
Table 5. (Continued)
Rank*
••^•WMW
25
24
23
22
21
20
19
18
17
16
15
14
Genus Nean
Acute Value
**
8,100
7,233
6,580
6,053
6,000
5,228
4,900
4,341
3.830
3,265
2,100
1,707
Species
Amphlpod,
Gammarus sp.
Common carp,
Cyprlnus carplo
Northern squawflsh,
Ptychochellus oreqonens Is
Guppy,
Poecll la retlculata
Golden shiner,
Notemlqonus crysoleucas
White sucker,
Catostomus commersonl
Asiatic clam,
Cor bleu la flumlnea
Southern platyflsh,
Xlphophorus maculatus
Fathead minnow,
P 1 mepha 1 es prome 1 as
1 so pod,
Llrceus alabamae
Brook trout ,
Salvellnus tontlnalls
Bryozoan ,
Lophopodella carter 1
Species Mean
Acute Value
8,100
7,233
6,580
6,053
6,000
5,228
4,900
4,341
3,830
3,265
2,100
1,707
Species Nean
Acute-Chroelc
-
~
-
-
5.644
2.335
-------
TabU 3. (Continued)
Rank*
13
12
11
10
9
8
7
6
5
Genus Mean
Acut* Valua
(*gA)** Species
1,672 Flaqflsh,
Jordanella florldae
1,607 Bryozoan,
P 1 umate 1 1 a rostrata
1,578 Snail,
Hellsoma campanulatum
1,353 Snail,
Physa gyrlna
Snail ,
Physa heterostropha
1,307 Bryozoan,
Pectlnetella magnified
>1,264 Tublflcld worm,
Llmnodrllus hof froelsterl
1,225 Rainbow trout,
Salmo galrdnerl
Atlantic salmon,
Salmo salar
1,030 Co ho salmon,
Oncorhynchus klsutch
Sockeye salmon, -
Oncorhynchus nerka
Chinook salmon,
Oncorhynchus tshawytscha
790.0 Mozambique tllapla.
Species Keen Species Mean
Acute Value Acute-Chronic
*** Ratio****
1,672 41.20
1,607
1,578
1 ,683
1,088
1,307
>1,264
689.3 1.554
2, 176
1 ,628
1,502 <6.074
446.4 0.7027f
790.0
Tllapla mossamblca
-------
Table 3. (Continued)
Rank*
4
3
2
1
Genus Mean
Acute Value
299.8
227.8
119.4
93.95
Species
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla pulex
Longfln dace,
Agosla chrysogaster
Striped bass,
Morone saxatllls
Cladoceran ,
Cerlodaphnla dubla
Cladoceran,
Species Mean
Acute Value
Ufl/L)***
355.5
252.9
227.8
119.4
174.1
50.70
Species Neaa
Acute-ChroM Ic
Ratio****
7.260tf
-
-
-
Cerlodaphnla retlculata
N>
-------
TabU 3. (ContlniMd)
Rank*
28
27
26
25
24
23
22
21
20
19
Genus M»an
Acute Value
<»S/L)**
320,400
50,000
39,000
38,000
36,630
9,467
7,100
6,328
4,683
4,515
Species Maan
Acute Value
Species <.a/L>*«
SALTWATER SPECIES
Clam,
Macoma balthlca
Mud snail,
Nassarlus obsoletus
Starfish,
Asterlas forbesll
Spot,
Lelostomus xanthurus
Mummlchog,
Fundulus heteroci Itus
Winter flounder,
P seudop 1 euronectes amerlcanus
Polychaete worm,
Ctenodr 1 1 us worm
Soft-shel 1 clam,
Mya arenarla
Am phi pod,
Corophlum volutator
Atlantic sllverslde.
Men Id la men Id la
Tidewater sllverslde.
320,400
50,000
39,000
38,000
36,630
9,467
7,100
6,328
4,683
3,640
5,600
Species Maan
Acute-Chronic
-
Men Id la penlnsulae
-------
Table 3. (Continued)
Rank*
^MBMBBVi^BV
18
17
16
15
14
13
12
11
10
9
8
6enus Man
Acute Value
<«q/L)** Species
8,856 Polychaete worm.
Nereis divers Icolor
Polychaete worm.
Nereis vlrens
4,074 Copepod,
Eurytemora afflnls
3,934 Blue mussel ,
Mytllus edulls
2,439 Polychaete worm,
Capltel la capitate
>1,920 Squid,
Lol 1 go opalescens
1,450 Copepod,
Nltocra splnlpes
1,400 Polychaete worm,
Ophryotrocha dladema
1,273 Polychaete worm
Neanthes arenaceodentata
1,000 Green crab,
Carclnus maenus
665.9 Copepod,
Acartla clausl
Copepod,
Acartla tonsa
586.1 Oungeness crab.
Specie* Mean Species Mean
Acute Value Acute-Chronic
(»g/L>*** Ratio****
9,682
8,100
4,074
3,934
2,439
>1,920
1,450
1,400
1,273
1,000
1,507
294.2
586.1
_
Cancer mag I star
-------
TabU 3. (Continued)
Genus Mean
Acute Value
Ul
6
5
4
3
2
t
543.2
430
400
380.5
247.5
195
191.4
Spec Us
Mysld.
Mysldopsls bah Ia
Mysld,
Mysldoopsls blgelowl
Striped bass,
Morone saxatlI Is
Hermit crab,
Pagurus long I carpus
Lobster,
Homarus amerlcanus
Pacific oyster,
Crassostrea glgas
Eastern oyster,
Crassostrea virgin lea
Qua hog clam,
Mercenarla mercenarla
Cabezon,
Scorpaenlchthys marreoratus
Spacles New*
Acute Value
(i.g/1.)***
499
591.3
430
400
380.5
233.3
262.5
195
191.4
Sp«cles Mean
Acute-CliroNlc
Ratio"***
2.997
* Ranked fron most resistant to most sensitive based on Genus Mean Acute Value.
Inclusion of "greater than" values does not necessarily Imply a true ranking,
but does allow use of all genera for which useful data are available so that
the Final Acute Value Is not unnecesarlly lowered.
** Freshwater Genus Mean Acute Values are at hardness » 50 mg/L.
*** From Table 1; freshwater values are at hardness • 50 mg/L.
»»»» From Table 2.
* Geometric mean of range given In Table 2.
** Geometric mean of three values In Table 2.
-------
Table 3. {Continued)
Fresh water
Final Acute Value = 130.1 pg/L (at hardness = 50 mg/L)
Criterion Maximum Concentration = (130.1 pg/L) / 2 = 65.05 pg/L (at hardness = 50 mg/L)
Pooled Slope = 0.8473 (see Table 1)
ln(Crlterlon Maximum Intercept) - ln(65.05) - (slope x ln(50)l
* 4.175 - (0.8473 x 3.9120) =• 0.8604
Criterion Maximum Concentration = e«>.8473Un(hardness) 1*0.8604)
Final Acute-Chronic Ratio = 2.208 (sea text)
Final Chronic Value = (130.1 pg/L) / 2.208 = 58.92 pg/L (at hardness = 50 mg/L)
Assumed Chronic Slope = 0.8473 (see taxt)
ln(Flnal Chronic Intercept) = ln<58.92) - Islope x ln(50)l
= 4.076 - (0.8473 x 3.9120) = 0.7614
Final Chronic Value = e10'8473' '"'hardness) '^^614)
Salt water
Final Acute Value = 190.2 pg/L
CrSterlon Maximum Concentration = (190.2 pg/L) /2 = 95,10 pg/L
Final Acute-Chronic Ratio = 2.208 (saa text)
Final Chronic Value = (190.2 [JQ/D / 2.208 = 86.14 pg/L
-------
Table 4. ToxicIty of Zinc to Aquatic Plants
Hardness
Species
Blue- green alqa,
Chroococcus par Is
Green alga,
Chlaraydomonas varlabllls
Green alga,
Chlamydomonas sp.
Green alqa,
Chloral la pyrenoldosa
Green alga,
Chlorel la saccharophl la
Green alga,
Chlorel la sal Ina
Green alga,
Chlorel la vulgarls
Green alga,
Chlorel la vulgarls
Green alga,
Chlorel la vulgarls
Green alga,
Scenedesmus quadr Icauda
Green alga,
Scenedesmus quadr Icauda
Green alga,
Selenastrum caprlcornututn
Green alga,
Selenastrum capr Icornutucn
Chemical
(•g/L as Duration Concentration
CaCOi) (days) Effect (*9/L)*
FRESHWATER SPECIES
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
chloride
Zinc
sul fate
Zinc
sul fate
Zinc
chloride
Zinc
chlor Ide
Zinc
sul fate
Zinc
sul fate
Zinc
chloride
Zinc
chloride
10
6
68 10
4
4
4
4
15
33
68 5
4
7
14
Reduced growth
3 Of reduction In
division rate
Reduced growth
LC50
EC50
LC50
EC 50
(growth)
EC50
(growth)
EC50
(cell division)
Reduced growth
LC50
>400
503
15,000
>200,000
7,100
>200,000
2,400
11,990-
23,980
5,100
20,000
>200.000
Incipient growth 30
Inhibition
EC95 40.4
(growth)
Reference
Las and Walker 1984
Bates et al. 1983
Cairns et al. 1978
Wong et al . 1979
Rachlln et al . 1982
Wong et al . 1979
Rachl In and Farran
1974
Ral et al. 1981 a
Rosko and Rachl In
1977
Cairns et al. 1978
Wong et al . 1979
Bartleft et al. 1974
Greene et al . 1975
-------
Table 4. (Continued)
Species
Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrum caprlcornutum
Diatom,
Cyclotella meneqhinlana
Diatom,
Navlcula Incerta
Diatom,
Navlcula semlnulum
Diatom,
Navlcula semlnulum
Diatom,
Navlcula semlnulum
Diatom,
Navlcula semlnulum
Diatom,
Navlcula semlnulum
Diatom,
Navlcuia semlnulum
Diatom,
Nltzschla_ 11 near Is
Duckweed,
Lemma qlbba
Duckweed,
Lemna minor
Chemical
Zinc
chloride
Zinc
sul fate
Zinc
chloride
Zinc
chloride
Zinc
sul fate
Zinc
sulfate
Duckweed,
Lemna minor
Hardness
(•g/L as
CaCOj)
-
68
-
58
(22 °C)
58
(28 *C)
58
(30 *C)
174
(22 *C)
174
(28 *C>
174
(30 *C)
294.6
-
-
-
Duration Concentration
fdavs) Effect («fl/L»*
14 EC95
(growth)
14-21 EC50
( blomass)
5 Reduced
growth
4 EC50
5 EC50
(growth)
5 EC50
(growth)
5 EC50
(growth)
5 EC50
(growth)
5 EC50
(growth)
5 EC50
(growth)
5 LC50
70 Did not re-
duce bl amass
28 EC50
(tissue damage
and death)
4 EC50
(growth)
68
50.9
20,000
10,000
4,290
1,590
1,320
4,050
2,310
3,220
4,300
654
67,700
10,000
Reference
Greene at al . 1975
Turbak at al . 1986
Cairns at al . 1978
Rachlln at al. 1983
Academy of Natural
Sciences 1960
Academy of Natural
Sciences 1960
Academy of Natural
Sciences I960
Academy of Natural
Sciences 1960
Academy of Natural
Sciences 1960
Academy of Natural
Sciences 1960
Patrick at al . 1968
Van der Werff and
Pruyt 1982
Brown and Rattlgen .
1979
Wang 1986 a
-------
Table 4. (Continued)
Specie* Chealcal
Duckweed, Zinc
Splrodela polyrhlza sulfate
Macrophyte, Zinc
Callltrlche plataycarpa sulfate
Eurasian waterm II fol I,
MyrlophyIlum splcatum
Macrophyte, Zinc
El odea canadensls sulfate
Macrophyte, Zinc
Elodea nuttallll sulfate
Diatom, Zinc
Navlcula Incerta chloride
Diatom, Zinc
Nltzschla cIosterlum sulfate
Diatom, Zinc
Nltzschla cIosterturn sulfate
Diatom, Zinc
Schroederella schroedarl sulfate
Dlnoflagellate. Zinc
Gymnodlnlum splendens sulfate
Dlnoflagellate. Zinc
Procentrum ml cans sulfate
Hardness
(•g/L M
CaCO,)
-
-
-
—
-
SALTWATER
-
-
-
32*«»
32»»»
32»«»
Duration
(days)
70
73
32
28
73
SPECIES
4
4
4
4
4
4
Concentration
Effect (PoA)»
Did not re- 654
duce blomass
Did not re- 654
duce blomass
EC50 21,600
(root weight)
EC50 22,500
(tissue damage
and death)
Did not re- 654
duce blomass
EC50 10,100
(growth)
EC 50 271
(growth)
EC50«» 360
(growth)
EC50 19.01f
(growth)
EC50 3,716f
(growth)
EC50 319.1f
(growth)
Refer ance
Van der Werff and
Pruyt 1982
Van der Werff and
Pruyt 1982
Stanley 1974
Brown and Rattlgan
1979
Van der Werff and
Pruyt 1982
Rachlln et al . 1983
Rosko and Rachl In
1975
Rosko and Rachl In
J975
Kayser 1977
Kayser 1977
Kayser 1977
-------
Table 4. {Continued)
Species Che* leal
Coccol Ithophor Id, Zinc
Crlcosphaera carterae sul fate
Giant kelp (young fronds),
Macrocvstls pyrlfera
Hardness
{«g/L as Duration Concentration
CaCOj) (do»») Effect (»g/L>*
• 4 EC50 76.69»»
(growth)
4 EC50 10,000
(photo syn-
thetic rate)
Reference
StlllweN IS
ClendennSng
North 1959
>77
and
* Ooncentratlon of zinc, not the chemical
** With chelatlng agent.
*** Salinity (g/kg), not hardness.
* Calculated from author's data.
-------
Table 5. BloaccuMulatloH off Zinc by Aquatic Organ I
Spec Us Chamlcal
Asiatic clam. Zinc
(1-3 yr), sulfate
Corblcula flumlnea
Asiatic clam. Zinc
(1-3 yr), sulfate
Corblcula flumlnea
Asiatic clam, Zinc
(1-3 yr) , sulfate
Corblcula flumlnea
Mayfly, Zinc
Ephemeral la 9rand Is suIfate
Stonefly, Zinc
Pteronarcys callfornlca sulfate
Atlantic salmon, Zinc
Salmo salar sulfate
Flag fish, Zinc
Jordanella florldae sulfate
Guppy, Zinc
Poecllla retlculata sulfate
Guppy, Zinc
PoeclI la retlculata sulfate
Guppy, Zinc
PoeclI la retlculata sulfate
Hardness
Concentration («g/L as Duration
In water (»q/L)« CaCCM (days! Tissue
FRESHWATER SPECIES
218 58.3 28
433 58.3 28
835 58.3 28
30-70 14
30-70 14
12-24 .. 80
139 45 100
173 30 134
328 30 134
607 30 134
Soft
tlssua
Soft
tissue
Soft
tissue
Whole
body
Whole
body
Whole
body
Whole
body
Whole
body
Whole
body
Whole
body
BCF or
BAF*" Reference
126.2*»* Graney et al. 1963
71.6*»» Graney et al. 1983
102.2»*» Graney et al. 1983
1,130 Nehrlng 1976
106 Nehrlng 1976
51 Farmer et al . 1979
417.3««" Spehar et al . 1978
477.8
534.9
492.8
965.5
466.3
512.4
Pier son 1981
Plerson 1981
Plerson 1981
-------
IBUIV *• %v*»*ii ••••••——-
Species
Concentration
s»h._i«»i In water (iiQ/L)*
Salinity Duration
Co/ka)
-------
Table 5. (Continued)
OJ
Species
Barnacle (adult) ,
Balanus balanoldes
Shrimp (adult).
Pandalus montagu 1
Mummlchog (Juvenile),
Fundulus heteroclltus
Mummlchog (juvenile),
Fundulus heteroclltus
Mummlchog (juvenile),
Fundulus heteroclltus
Mummlchog (juvenile),
Fundulus heteroclltus
Mummlchog (juvenile),
Fundulus heteroclltus
Mummlchog (juvenile).
Fundulus heteroclltus
Che* leal
—
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chlor Ide
Zinc
chloride
Zinc
chloride
Zinc
chloride
Concentration
In water (»q/L>*
to Ł
IB.O
ŁC
O J
210
210
O 1 f\
810
810
7,880
7,880
Salinity Duration
(days)
30
14
56
56
56
56
56
56
Tissue
Soft
tissue
Whole
body
Scales
Whole
body
Scales
Whole
body
Scales
Whole
body
BCF or
BAF"
951.6*
3.692»»»'t»
+ * •*• +
40.95T'm
18. 10*'*"
t4> <•>•*•
«.*, 'tft
•*• •*• + +
28.60t»ttT
t+ + +
,.,«, 'tft
Reference
White and Walker
1981
*** Ray at a' •
Y%0
wIV!Eeaf^84
Sata«arte4
Sauer and
Watabe™ 984
§3^9^984
wS^Ee"?^
Wa^Ite"?^
* Measured concentration of zinc.
»» Bloconcentratloi
i factors (BCFs)
and bloaccumul atlon
_ _ _ .^__.^ i
factors (BAFs) are based on measured concentrations ?' zl"c ["
,:„ *JL ^.i^h +h« n«omatrlc mean factor was calculated Is given
IT a I t\Jii i «*- i *-" 3 * UVM ^ * M..— —. —
_.._ In tissue. Number of exposure concentrations from
fn parentheses when It Is greater than 1.
»»« Factor was converted from dry weight to wet weight basis.
*«»* Steady-state reached.
***** F|a|d study.
f Calculated from authors' data or graph.
t* Steady-state not reached.
Concentration of zinc was the same In exposed and control animals.
ftt
-------
Table 6. Other Data on Effects of Zinc on Aquatic Organ I
Species
Green alga,
Chlorel la vulgar is
Green alga,
Selenastrum capr icornutum
Green alga,
Selenastrum capr t cor nut urn
Green alga,
Chlorel la vulgar Is
Green alga,
Pedlastrum tetras
Green alga,
Scanedesmus quadr Icauda
Perl phyton,
Mixed species
Water weed,
E lodea (Anachar Is)
canadensis
Moss,
F ont 1 na 1 1 s ant ! pyret 1 ca
Bacter turn,
Escher Ichla col 1
Bacterium,
Escher Ichla col 1
Mixed hetartrophlc
bacter la
Mixed haterotrophlc
bacter la
Chemical
Zinc
sul fate
Zinc
phosphate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
-
Zinc
sul fate
Zinc
chloride
Zinc
sul fate
Zinc
sul fate
Zinc
chior Ide
Zinc
chlor Ide
Hardness
Cng/L as
CaCOjl. Duration
FRESHWATER SPECIES
1 hr
14 days
4 hr
3 wk
3 wk
96 hr
3 wk"
1 day
1-6 days
30 mln
0.5 hr
3 days
Concentration
Effect
-------
Table 6. (Continued)
Species
Bacterium,
NItrobacter sp. and
Nltrosomonas sp.
Protozoan,
Mlcroreqma heterostoma
Protozoan,
Parameclum caudatum
Euglena,
Euqlena vlrldls
PI ankton,
Mixed species
Zoopl ankton.
Mixed species
Rotifer,
Phllodlna acutlcornls
Worm,
Aeolosoma headleyl
Tub! field worm,
Tublfex tublfex
Tubl field worm.
Tublfex tublfex
Tubl field worm,
Tublfex tublfex and
Hardness
(•g/L as
Chen leal CaCOj)
Zinc
sulfate
Zinc
sul fate
Zinc
sulfate
-
Zinc
chloride
Zinc 45
sul fate
Zinc 45
sul fate
Zinc 34.2
sul fate
Zinc 224
chloride
Zinc
sul fate
Concentration
n.«r»+ln« Effect CuO/D"
4 hr EC50
28 hr Incipient
Inhibition
1.5 hr Reduced vitality
3 wk BCF=144
2 wk Reduced primary
productivity
100,000
330
3,500
-
15
3 wk Reduced crustacean 100
density and diversity
48 hr lŁ50(5*C)
(10'C)
(15*C)
(20 *C)
(25*C)
48 hr LC50(5BC)
(10'C)
(I5'C)
(20'C>
(25 *C)
48 hr LC50
48 hr LC50
24 hr LC50
1,550
1,300
780
600
500
18,100
17,600
15,600
15,000
13,500
2,980
130,000
46,000
Reference
Will lam son and
Nelson 1983
Br Ingmann and Kuhn
1959b
Mills I976a
Coleman et al . 1971
Marshal 1 et al . 1983
Marshal 1 et al . 1981
Cairns et al . 1978
Cairns et al . 1978
Brkovlc-Popovlc and
Popov Ic 1977a
Qureshl et al . 1980
Whltley 1968
Llmnodrllus hoffmelsterl
-------
Table 6. fContlnued)
SpeCleS
Snail,
Gonlobasls llvescens
Snail,
Nltocrls sp.
Sna 11,
Lymnaea emarqlnata
Snail (adult),
Physa gyrlna
Snail,
Physa Integra
Cladoceran,
Cerlodaphnla dubla
Cl adoceran,
Cerlodaphnla dubla
Cladoceran (<6 hr),
Cerlodaphnla retlculata
Chemical
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
chloride
Zinc
sulfate
Zinc
chloride
Zinc
chloride
Zinc
chloride
Hardness
(«g/L as
CaCO}>
137-171
45
137-171
36
137-171
36
36
36
68
82
90
353
376
392
362
392
Concentration
Duration
48 hr
48 hr
48 hr
30 days
48 hr
7 days
48 hr
48 hr
48 hr
48 hr
48 hr
48 hr
Effect
LC50
LC50(5*C)
(10«C)
(15*C)
(20 'O
(25*0
LC50
No effect
LC50
LC50
Chronic value
(river water)
EC 50 (Immobll
za t Jon; river
water)
EC50 (high
solids)
Cng/L)*
13,500
4,800
4,600
2,800
1,900
1,650
4,150
570
771
4.400
167
1- 164
149
222
366
255
224
114
96
264
195
Reference
Cairns at al . 1976
Cairns et al . 1978
Cairns et al . 1976
Nebeker et al . 1986
Cairns et al . 1976
Carlson et al . 1986
Carlson et al „ 1986
Carl son and Roush
1985
-------
Table 6. (Continued)
Species
Cladoceran (adult),
Daphnla galeata mendotae
Cladoceran (young),
Daphnla galeata mendotae
Cladoceran,
Daphnla maqna
Cladoceran,
Daphnla maqna
Cladoceran,
Daphnla maqna
Cladoceran,
Daphnla maqna
Cladoceran,
Daphnla magna
Cl adoceran,
Daphnla magna
Cladoceran (3-5 days),
Daphnla magna
Cladoceran (adult),
Daphnla magna
Cl adoceran,
Daphnla magna
Chemical
-
Zinc
sul fate
Zinc
sul fate
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
sul fata
Zinc
sul fata
Zinc
sul fata
Hardness
(•g/L as
CaCO}> Duration
2 wk
2 Mk
16 hr
48 hr
45.3 48 hr
45.3 21 days
45.3 21 days
288 24 hr
72 hr
72 hr
45 48 hr
Concentration
Effect (iiq/L)«
BCF =9,400
BCF=5.833
BCF =6, 333
BCF =9 ,933
BCF=6,933
EC50
( Immobll Izatlon)
EC50
(river t«ter)
EC 50
( Immobll Izatlon)
(fed)
EC50
( Immobll Izatlon)
\6% reproductive
Itnpa Irment
EC50
(swimming)
LC50(10*C)
(15*C)
(25 *C)
(30*C)
LCSOdO'C)
(15*C)
(25 *C)
(30'C)
LC50(5*C>
(10*C)
(15*C)
(20*C>
15
30
60
15
30
<1 9,440
1,800
280
158
70
14,000
5,050
1,096
565
14.0
1,316
1,100
1,010
5.0
2,300
1,700
1,100
560
Reference
Marshall at al . 1983
Marshall at al . 1983
Anderson 1944
Brlngmann and Kuhn
1959a,b
Bleslnger and
Chrlstensen 1972
Bleslnger and
Chrlstensen 1972
Bleslnger and
Chrlstensen 1972
Brlngmann and Kuhn
1977
Brag Inskly and
She her ban 1978
Brag Inskly and
Shcherban 1978
Cairns et al . 1978
-------
TabU 6. (ContlnuMl)
Spaclas
Cl adoceran,
Daphnla magna
Cl adoceran,
Daphnla pulex
Cl adoceran
Bosmlna longlrostrls
Cl adoceran,
Eubosmlna coreqon 1
Cope pod (adult),
Tj-opocykops praslnus
Crayfish (adult) ,
Orconectes v Iritis
Mayfly,
Cloeon dlpterum
Mayfly (naiad),
Ephemeral la grand Is
Mayfly,
Ephemeral la subvarla
Damsel f 1 y.
Unidentified
Stonef !y (naiad) ,
Pteronarcys callfornlca
Stonef 1 y,
Acroneurla lycorlas
Caddlsfly,
Hydropsyche batten 1
Chanlcal
Zinc
sulfate
Zinc
sul fate
-
-
Zinc
chloride
Zinc
sulfate
Zinc
sulfate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Hardness
(•g/L as
CaCO,)
130-160
45
-
-
10
10
120
26
30-70
54
50
30-70
50
52
Duration
50-70 days
48 hr
2 wk
2 wk
48 hr
14 days
72 hr
14 days
10 days
96 hr
14 days
14 days
11 days
Effact
Reduced
1 ong ev 1 ty
LC50(5*C)
(10'C)
(15*0
(25*C>
BCF=1 1,930
BCF- 6,300
BCF- 5,183
BCF»1 0,870
8CF- 6,833
BCF- 3,867
EC50
(motll Ity)
1C 50
LC50(10*C)
(15*0
(25'C)
(30 "O
LC50
1C 50
I,C50
LC50
UC50
LC50
CoacaNtratloN
(pg/L)»
100
1,600
1,200
940
280
15
30
60
15
30
60
52
264
2,934
84,000
35,710
6,920
2,846
1,330
>9,200
16,000
26,200
>13,900
32,000
32,000
R«fwwica
Winner 1981
Cairns at al. 1978
Marshall at al. 1983
Marshall at al. 1983
Lalanda and Plnal-
Alloul 1986
Miranda 1986
Braglnskly and
Shcherban 1978
Nehrlng 1976
War nick and Bel 1
1969
Rehwoldt at al . 1973
Nehrlng 1976
War nick and Bel 1
1969
War nick and Bel 1
1969
-------
Tabla 6. (Continued)
Spaclas
Caddlsfly,
Un Identified
Mosquito (pupa),
Aedes aegyptl
Midge,
Chlronomous sp.
Midge (embryo to 3rd In star),
Tanytarsus dIsslmlI Is
Coho salmon (fry),
Oncorhynchus klsutch
Coho salmon (2.9 g),
Oncorhynchus klsutch
Sockeye salmon (alavln)
(acclimated to zinc),
Oncorhynchus nerka
Sockeye salmon (alevln)
(acclimated to zinc),
Oncorhynchus nerka
Sockeye salmon (alevln),
Oncorhynchus nerka
Sockeye salmon,
Oncorhynchus nerka
Rainbow trout,
Salmo galrdnerI
Rainbow trout
(7.62 cm),
Salmo galrdnerI
Ra Inbow trout
(7.62 cm),
Salmo galrdnerI
Rainbow trout (fIngerlInq),
Salmo qalrdnerl
ChaMlcal
Zinc
sul fate
Zinc
chloride
Zinc
sul fate
Zinc
chloride
Zinc
chlor Ide
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
sul fate
Zinc
sulfate
Zinc
sul fate
Zinc
sulfate
Hardness
C*g/L as
CaOM
50
4
50
46.8
3-10
30.5
-
-
-
20-84
320
Duration
96 hr
72 hr
96 hr
10 days
24 hr
1.75 hr
96 hr
115 hr
115 hr
3 mo
285 mln
180 mln
162 mln
Effact
LC50
20% mortal Ity
30* mortality
LC50
LC50
Decrease white
blood eel Is
No effect on
ol faction
LC50
LC50
LC50
None (adult to
smalt)
LT50
Coacantratloa
(•4/L>*
50,100
500
5,000
18,200
36.8
500
654
1,663
>630
447
112
10,000
11,000
11,500
Rafaranca
Rehwoldt at al
Abbas 1 et al .
Rehwoldt at al
Anderson at al
McLeay 1975
. 1973
1985
. 1973
. 1980
Re hn berg and Schreck
1986
Chapman 1978a
Chapman 1978a
Chapman 1978a
Chapman 1978a
Lloyd 1960
15-20
320
320
7 days
3 days
48 hr
LC50 (fed)
LC50 (fed)
LC50
560
3,500
3,860
Lloyd 1961a,b
Lloyd 1961a,b
Herbert and Shir ben
1964
-------
Table 6. (Continued)
Specie*
Rainbow trout,
Salmo galrdnerl
Ra Inbow trout ,
Salmo qalrdnerl
Rainbow trout (3-4 mo).
Salmo qalrdnerl
Rainbow trout (yearling).
Salmo qalrdnerl
Ra Inbow trout
(46.7-125.5 g),
S a 1 mo qalrdnerl
Rainbow trout (13.7 g) ,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Ra Inbow trout (1 yr> ,
Salmo qalrdner 1
Rainbow trout (100.9 g) ,
Salmo qalrdnerl
Rainbow trout ( fry).
Salroo qalrdnerl
Rainbow trout (embryo),
Salmo qalrdnerl
Rainbow trout ( flnqerl Ing
to adult) ,
Salmo qalrdnerl
Rainbow trout (15-17.5 cm).
S a 1 mo qalrdner i
Rainbow trout,
S a 1 mo qalrdnerl
Rainbow trout (200 mm),
S a 1 mo qalrdner i
ChaMlcal
WVI***l**
-------
Tablo 6. (Continued)
00
Species
Rainbow trout,
Salmo galrdnerl
Rainbow trout (yearling),
Salmo galrdnerl
Rainbow trout (2 mo),
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout
(embryo, larva),
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout
(80-120 g),
Salmo galrdnerl
Rainbow trout (50 g),
Salmo galrdnerl^
Rainbow trout,
Salmo galrdnerl
Rainbow trout
(Juvenlle),
Salmo galrdnerl
Rainbow trout
(j uvenl le),
Salmo galrdnerl
Rainbow trout
(fIngerllng),
Salmo galrdnerl
Chealcal
Zinc
sulfate
Zinc
sulfate
Zinc
acetate
Zinc
sulfate
Zinc
chI orIde
Zinc
chloride
Zinc
suI fate
Zinc
sulfate
Zinc
chloride
Zinc
sulfate
Zinc
sulfate
Hardness
(•g/L as
CaCOQ
374
36
104
(92-110)
112
18.7
6.0-6.5
14
(pH-6.0)
Duration
5.1-10.5
hr
85 days
96 hr
24 hr
28 days
40 mln
30 days
Concentration
Effect (P9/L>* Reference
1 ncreased
lactic acid
Inhibited
growth
LC50
LC50(5°C)
(15*C)
(30*C)
EC50 (death and
deformity)
94$ avoidance
Increased gl 1 1
enzymes
15,340
1,120
550
2,800
1,560
2,100
1,060
(1,120)
47
290
Hod son 1976
Watson and McKeown
1976
Hale 1977
Cairns et al . 1978
Blrge 1978; Blrge et
al. 1978.1980,1981
Black and Blrge
1980a, b
Watson and Beamish
1980
72 hr
96 hr
9 days
96 hr
LC50
2,000 Lovegrove and Eddy
1982
Circulatory 1,250
vasoconstrIctIon
Tuurala and Solvlo
1982
HypergIycemla
42 days Damaged
hepatocytes
LC50
352 Wagner and McKeown
1982
431.5 Lei and 1983
670 Spry and Wood 1984
-------
Table 6. (Continued*
Rainbow trout (gamete),
Salmo galrdnerj
Rainbow trout (2.7-3.3 g),
Salmo qalrdneri
Che*lea8
Zinc
sul fate
Rainbow trout (embryo),
Salmo galrdnerI
Zinc
n I trate
Rainbow trout (embryo
with capsule removed),
Salmo qalrdneri
Zinc
n I trate
Hardness
(•g/L as
CaCO»)
Duration
40 mln
Concentration
Effect (»g/U* Reference
385
(pH=6«,99)
30.5
(pH=6.98)
390
(pH=5.49)
32.5
(pH=5.49)
389
(pH=7.00)
385
(pH=6.99)
388
(pH=7.02)
30
'
.
30
9.4 hr
10.4 hr
11.5 hr
16.0 hr
6.3 hr
9.4 hr
12.9 hr
10 hr
9 hr
20 hr
18 hr
18 hr
18 hr
20 hr
36 hr
>168 hr
14 hr
18 hr
36 hr
30 hr
37 hr
58 hr
70 hr
>!68 hr
>168 hr
Reduction In
spermatozoa
survival; no
affect on
fertilization
LT50
LT50
LT50
20,000
19,100
5,780
18,900
5,570
26,900
19,100
13,800
14,000
13,000
12,000
11,000
10,000
9,000
8,000
6,000
2,000
14,000
13,000
1 2,000
11,000
10,000
9,000
8,000
6,000
2,000
Bit lard and Roubaud
1985
Bradley and Sprague
1985
Rom bough 1985
Rombough 1985
-------
Table 6. (Continued)
Species
Rainbow trout (5 days
post fertilization),
Salmo qalrdnerl
Rainbow trout (10 days
post fertilization),
Salmo galrdnerl
Rainbow trout (15 days
post fertilization),
Salmo galrdnerl
Rainbow trout (22 days
post fertilization),
Salmo galrdnerl
Rainbow trout (29 days
post fertilization),
Salmo galrdnerl
Rainbow trout (36 days
post fertilization),
Salmo galrdnerl
Rainbow trout (2 days
post hatch),
Salmo galrdnerl
Rainbow trout (7 days
post hatch) ,
Salmo galrdnerl
Atlantic salmon (parr),
Salmo salar
Atlantic salmon (7.38 g) ,
Salmo salar
Atlantic salmon,
Chemical
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Hardness
(«g/L as
CaCOti Duration
87.7 48 hr
87.7 48 hr
87.7 48 hr
87.7 48 hr
87.7 48 hr
87.7 48 hr
87.7 48 hr
87.7 48 hr
18 4 hr
14 23-25 hr
14
Effect
Concentrat Ion
LC50 24,000
LC50 <1 ,000
LC50 9,100
LC50 7,000
LC50 4,300
LC50 9,200
LC50 3,200
LC50 3,400
EC50 (avoidance) 49.88
LT50 954.4
Incipient 150-1,000
Reference
Shazll 1 and Pascoa
1986
Shazl 1 1 and Pascoa
1986
Shazll 1 and Pascoa
1986
Shazll 1 and Pascoa
1986
Shazll 1 and Pascoe
1986
Shazl 1 1 and Pascoa
1986
Shazl 1 1 and Pascoa
1986
Shazl 1 1 and Pascoa
1986
Sprague 1964 b
Zltko and Carson 1<
Zltko and Carson It
Salmo salar
lethal level
-------
I
i
0Ł
•o
s
00
fe
gOOQOO OOo^O
Or-ft O--iftgO>
^>Oift*'n'O rO»>OO^
O
8
o*
o
9 «-
Q) .
6 vO Ol
I— CD
0
s
CO
!».
Ot
in
c
L.
a
o
88i
CM
00
o>
>
a
u
>-
1
a
<3
&
^
S
s
1
a
a
*
JŁ Ł
8 O!
o CM e
JCO 10
- 5
CO
r»
O
I/I
e
i_
a
O
r- o 2 Q °
o oo o
35
3
o
4-
10
10
y*-
— a
M ">
10 ID U
O *• O *• O O
— "3 — "3 —!e
M i/i si in MO
e
10
— 3
M in
in u fl (O
o •*• oo o*- o*-
5-5 *•Ł 5= fa
rviui MO Mm Mm
A
e
«J « i-
in ^ ID
d) —
f> ^ 10
ii — m
— 3 —
L.
10
1
ic sa
salar
At
Sa
* -» Q * 3
_ O O --^ W
« I/I
m4»
Goldfish (3-5 <
Carasslus aura'
* M
4- 4-
Goldf Ish ( Imma
Carasslus aura;
.!§
••» 4-
Go 1 d f 1 sh
(embryo, larva
Carasslus aura
m
3
Goldfish,
Carasslus aura
" ' a
a i~> " "i
o •
00
9S O
Common carp (3
Cyprlnus carpi
• o
Common carp (2
Cyprlnus carpi
;>
Golden shiner,
Notemfgonus cr
84
-------
Table 6. (Continued!
Species
Fathead minnow (1-2 g) ,
Plmephales promelas
Fathead minnow.
P 1 mepha 1 es prome 1 as
Fathead minnow,
(adult).
Plmephales promelas
Fathead m In now.
( 1 arv a) ,
Plmephales promelas
fathead minnow (larva),
Plmephales promelas
Fathead minnow (<24 hr) ,
oo Plmephales promelas
l_n f
Channel cattish,
(f Ingerl Inq) ,
Ictalurus punctatus
Channel catfish.
(emtx-yo, larva),
Ictalurus punctatus
Channel catfish,
( f Ingerl Ing) ,
Ictalurus punctatus
Guppy (5 mo) ,
Poecll la retlculata
Guppy,
Pncwllla retlculata
Che* leal
Zinc
acetate
Zinc
sul fate
Zinc
chloride
Zinc
chloride
_
Zinc
chloride
Zinc
sul fate
Zinc
chlor Ide
Zinc
sul fate
Zinc
sut fate
7 1 nf
Ł. 1 nc
sul fata
Hardness
(•g/L as
CaCOy)
20
203
103
254-271
392
48
36
55
68
82
90
206-236
90
313
260
Concentration
Pur-*.~ c**~* (.Q/L>« Reference
96 hr LC50
JO mo EC83 (fecundity)
96 hr LC50 (Fish from
pond contaminated
with heavy metal s)
96 hr LC50 (high solids)
7 days Reduced growth
96 hr UC50 (river water)
• 40 hr Decreased blood
osmolarlty
5 days Increased
al ban Ism
14 days LC50 (high
alkalinity)
4 mo Reduced repro-
duction
96 hr LC50 (high
sol Ids)
880
180
6,140
5,960
<2,660
<2,930
125
393
440
556
655
807
12,000
-
8,200
880
54,950
Pickering and
Henderson 1966
Brungs 1969
Blrge et al . 1983
Carl son and Roush
1985
Norberg and Mount
1985
Carlson et al . 1986
Lewis and Lewis 1971
Master-man and Blrge
1978
Reed et al . 1980
Uv lovo and Beatty
1979
Khangarot 1981
-------
Table 6. (Continued)
CD
Species
Guppy (184 mg),
Poecllla retlculata
Guppy ( fry),
Poecllla retlculata
Striped bass (embryo),
Morone saxatlI Is
Striped bass ( fry),
Morone saxatlI Is
Blueqlll (2.5-3.9 g),
Lepomls macrochlrus
Biueglll,
Lepomls macrochlrus
Biueglll (fry),
Lepomls macrochlrus
Biueglll (18.7 g),
Lepomls macrochlrus
Biueglll (39.97 g),
Lepomls macrochlrus
Biueglll,
Lepomls macrochlrus
Biueglll (juvenile),
Lepomls macrochlrus
Biueglll (fry),
Lepomls macrochlrus
Chemical
Zinc
sul fate
Zinc
sul fate
-
-
Zinc
chloride
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
chloride
Zinc
sul fate
Hardness
img/L as
CaCOO
260
30
137
137
44.3
370
51
68
_
36
112
313
Concentration
Durat Ion
48 hr
167.5 hr
20-25 hr
48 hr
96 hr
20 days
3 days
12 hr
4.7 hr
1-24 hr
24 hr
40 mln
14 days
Effect
LC50
1C 50
1C 50
LC50
LC50 (periodic
low D.O.)
LC50(00=1.91)
(00=2.12)
(00=3.46)
(00=3.29)
(00=5.50)
(00=5.53)
Lethal
LT50(20*C)
(30*C)
Increased cough
response
LC50(5*C)
(15*C>
(30 *C)
13jf avoidance
LC50 (high
alkal Inlty)
Ufl/L>«
75,000
1,450
1,850
1,180
4,900
7,200
7,500
10,700
10.500
12,000
10.700
235
32,000
32,000
3.000
23,000
19,100
8,850
43,700
11.000
Reference
Khangarot et al. 1981
Pier son 1981
O'Rear 1971
O'Rear 1971
Cairns and Scheler
1958a; Academy of
Natural Sciences 1960
Pickering 1968
Cairns and Sparks
1971 ; Sparks et al .
1972b.
Burton et al . 1972a
Sparks et al . 1972a
Cairns et al . 1978
Black and Blrge 1980
Reed et al . 1980
-------
Table 6. (Continued)
oo
Species
Largemouth bass
(embryo, larva),
Mlcropterus sal mo Ides
Largemouth bass (juvenile),
Mlcropterus sal mo Ides
Largemouth bass
(embryo, larva),
Mlcropterus sal mo Ides
Largemouth bass
( f Inqerl Inq) ,
Mlcropterus sal mo Ides
Narrow-mouthed toad
(embryo, larva),
Gastrophryne carol Inensis
Marbled salamander
(embryo, larva),
Chemical
Zinc
chloride
Zinc
sul fate
Zinc
chloride
Zinc
sul fata
Zinc
chloride
Zinc
chloride
Hardness
(•g/L as
CaCOj) Duration
93-105 8 days
112 40 mln
9 days
313 14 days
195 7 days
93-105 8 days
Concentration
Effect <»q/L)» Reference
EC 50 (death and 5,160
deformity)
57jl avoidance 7,030
EC 50 (death and 5,180
deformity)
LC50 (high 8,000
alkal Inlty)
0350 (death 10
and deformity)
BC50 (death 2,380
and deformity)
Blrge et al . 1978
Black and Blrge 1980
Slack and Blrge 1980
Reed et al . 1980
Blrge 1978; Blrge et
al. 1979
Blrge et al . 1978
Ambystoma opacum
-------
Table 6. (Continued)
Species
Green alga,
Carter la sp.
Green alga,
Chlamydomonas sp.
Green alga,
Dunallella euchlora
Green alga,
Dunallella euchlora
Green alga,
Dunallei la salIna
Green alga,
Dunallella tertloiecta
Green alga,
Dunallella trertlolecta
Green alga,
Dunallei la tertlolecta
Green alga,
Nanochloris atomus
Go I den-brown alga,
Isochrysls galbana
Go I den-brown alga,
Isochrysls galbana
Got den-brown alga,
Isochrysls galbana
Che»lcal
65Zlnc
Zinc
chloride
Zinc
sulfate
65Zlnc
Zinc
sulfate
Zinc
sul fate
Zinc
chloride
65z,nc
-
-
Salinity
(q/kq)
35
34
-
-
44
-
-
_
42
12
16
20
28
7
12
16
20
28
37
12
16
20
28
Duration
SALTWATER SPECIES
7 days
7 days
12 days
12 days
7 days
1 5" m In
15 mln
72 hr
7 days
48 hr
48 hr
(20 *C)
48 hr
(28 -C)
(
Effect
BCF = 2.184«»»
BCF = 16.12«»»
EC 50 (growth)
EC 50 (growth)
BCF - 43.88«*»
No effect on
potassium re-
tention
EC50 (oxygen
production)
EC50 (growth)
BCF = 16.12*»»
Reduced chlorophyll
_a_ about 65%
Reduced chlorophyll
Ł aboilt 65}
Red uced ch 1 orophy 1 1
a about 65}
Doncentratloi
-
-
>33,600
37,220*
-
6,538
65,380
13,000
-
2,000
430
810
1,200
4,400
1,300
74
520
too
2,300
1,000
3,000
800
3,000
1
Referen<
Styron
1976
Styron
1976
Wlkfors
1982
Wlkfors
1982
Styron
1976
Over net
Overnel
Fisher
Styron
1976
Wilson
1980
Wll son
1980
Wilson
1980
ce
et al.
et al.
and Ukeles
and Ukeles
et al .
1 1975
8 8976
et al. 1984
et al «
and Freeberg
and Freeberg
and Freeberg
-------
Table 6. (Continued)
Salinity
Concentration
00
Species
Golden-brown alga,
Isochrysls galbana
Got den- brown alga,
Isochrysls galbana
Golden-brown alga,
Monochrysls lutherl
Golden-brown alga,
Monochrysls lutherl
Golden- brown alga,
Monochrysls lutherl
Diatom,
Achnanthes brevlpes
Diatom,
Nltzschla longlsslma
Diatom,
Phaeodactylum tricornutum
D I atom ,
Phaeodactylum tricornutum
Diatom,
Phaeodactylum tricornutum
D 1 atom ,
Phaeodactylum tricornutum
Diatom,
Phaeodactylum tricornutum
D 1 atom ,
Phaeodactylum tricornutum
D 1 atom ,
Phaeodactylum tricornutum
Cnealcal
Zinc
chloride
Zinc
sulfate
Zinc
sulfate
Zinc
chloride
Zinc
sul fate
65Zlnc
Zinc
sulfate
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
sul fate
65Zlnc
Zinc
su 1 f ate
Zinc
chlor Ide
(g/kg) Duration
12 days
12 days
15 mln
12 days
12 days
40 7 days
30 1-5 days
11-15 days
13 days
14 days
15 mln
37 7 days
25 10-14 days
12 days
Effect
EC50 (growth)
EC50 (growth)
EC50 (reducted
oxygen pro-
duction)
EC50 (growth)
EC50 (growth)
BCF = 0.04***
Stimulated growth
2J>% reduction
In growth
BCF = 1,800***'*
BCF = 873*** •*
No effect on
oxygen evolution
BCF - 16.12***
19J reduction
In growth
EC50 (growth)
(M9/D*
>33,600
33,100*
1,308-1,961
>33,600
31,010*
<100
25,000
250
10,000
>65,380
3,000
>33,600
Reference
Wikfors and Ukeles
1982
Wikfors and Ukeles
1982
Overnel 1 1976
Wikfors and Ukeles
1982
Wikfors and Ukeles
1982
Styron et al .
1976
Subramanlan et al.
1980
Jensen et al . 1974
Jensen et al •
1974
Jensen et al .
1974
Overnel 1 1976
Styron et al .
1976
Braek et al . 1980
Wikfors and Ukeles
1982
-------
Table 6. {Continued)
Species
Diatom,
P haeodactv lunt tr Icornutum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Skeletonema costatum
Diatom,
Thalassloslra pseudonana
Diatom,
Thalassloslra pseudonana
Diatom,
Thalassloslra pseudonana
Chemical
Zinc
sul fate
Zinc
chlor Ide
Zinc
chlor Ide
Zinc
chlor Ide
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
chlor Ide
Zinc
chlor Ide
Zinc
chloride
Zinc
chloride
Zinc
chloride
Salinity
(q/Kg) Duration
12 days
13 days
12 days
11-15 days
10-14 days
10-14 days
15 mln
25 10-14 days
30 1-3 days
3 days
3 days
11-15 days
13 days
15 days
Concentration
Effect Cnq/L)"
74.2$ reduction
In growth
BCF " 4,000***'*
BCF = 160»»»'t
23* reduction
In growth
BC50 (growth)
BC50 (growth)
No effect on
oxygen evolution
20% reduction
In growth
Stimulated growth
Altered cytoplas-
mlc morphology
BCF = 765
41% reduction
In growth
BCF = MS"*'*
BCF = 350***'*
48,000
50
192. 9f
175.6f
>65,380
100
^200
265
500
Reference
Wlkfors and like las
1982
Jensen et al .
1974
Jensen et al .
1974
Jensen et al . 1974
Braek et al . 1976
Braek et al . 1976
Overnell 1976
Braek et al . 1980
Subraman Ian et al .
1980
Smith 1983
Smith 1983
Jensen et al . 1974
Jensen et al .
1974
Jensen et al .
1974
-------
Tab la 6. (Continued)
CMC|K Che»lcnl
Diatom, Zinc
Thalassloslra pseudonana sulfate
Diatom,
Thalassloslra pseudonana
Diatom, Zinc
Thalassloslra pseudonana chloride
Diatom, Zinc
Thalassloslra rotula sulfate
Phytoplankton (diatom)
DInof lagel late. Zinc
Amph Id In 1 urn carter 1 sulfate
DInof lagal late. Zinc
AntDhldlnlum carter 1 sulfate
DInof lagel late,
Glenodlnlum hat 1 1
DInof lagal late,
Gymnodlnlum splendens
DInof lagel late,
Gymnodlnlum splendens
Salinity
(q/kg) Duration
10-14 days
14 2 days
(12'C)
(20 *C)
(24*C)
(28 'O
72 hr
32 5 days
- •*
10-14 days
10-14 days
28 2 days
14 2 days
(16*C)
(30 'O
28 2 days
(16'C)
(20*C)
(24 'O
(28*C)
(30 *C)
Concentration
Effect <»fl/L>" Reference
EC50 (growth)
Red uced ch 1 orophy 1 1
a about 65}
EC 50 (growth)
EC50 (growth)
•
BAF = 113
EC 50 (growth)
No significant
effect on growth;
Inhibited growth
In presence of 50
M g copper /L
Reduced chlorophyll
a about 65}
Reduced chlorophyll
_a_ about 65%
Reduced chlorophyll
a about 65}
470. 8f
-------
Table 6. (Continued)
• V1WIW «* • \u*n* B »•»••»—•
Species
Dlnof lagel late,
Scrlppslella faeroense
Brown macroalga.
Ascophyllum nodosum
Brown macroalga,
Ascophyllum nodosum
Brown macroalga,
Fucus serratus
Brown macroalga,
Fucus serratus
Brown macroalga,
Fucus spiral Is
Brown macroalga.
Fucus veslculosls
Brown macroalga,
Fucus veslculosls
Brown macroalga.
Lamlnarla dlgltata
Brown macroalga.
Lamlnarla hyperborla
Brown macroalga,
Lamlnarla hyperbor 1 a
Brown macroalga,
Pelvetla canal Iculata
Green macroalga.
Ulva lactuca
Green macroalga.
Ulva 1 actuca
Chemical
Zinc
sul fate
-
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chloride
.
Zinc
chloride
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
chloride
Zinc
chloride
Zinc
chloride
Salinity
(g/kg) Duration
32 50 days
.
33 10 days
33 10 days
1 hr
33 10 days
_
33 10 days
24 days
8-10 days
7 days
33 10 days
6 days
6 days
Concentration
Effect
33< reduction
In cell numbers
BAF * 1,603***'tf
Decreased growth;
no effect at 100 ug/L
Decreased growth;
no effect at 100 ug/L
Altered llpld
metabol Ism
Decreased growth;
no effect at 100 pg/L
BAF = 1,612***'**
Decreased growth;
no effect at 2,900 Mg/L
Reduced growth
Reduced growth of
sporophytes
Abnormal maturation
of gametophytes
Decreased growth;
no effect at 100 Mg/L
BCF = 255*** •*
BCF = 5.150***'*
(»q/D*
10,000
_
250
1,400
>8.8
1,400
-
7,000
MOO
250
5,000
1,400
65.38
6,538
Reference
Kayser 1977
Melhuus et al .
1978
Stromgren 1979
Stromgren 1979
Smith and Ha r wood
1984
Stromgren 1979
Mel huus et al .
1 Q7H
1 7 f O
Stromgren 1979
Bryan 1969
Hopkins and Kaln 1971
Hopkins and Kaln 1971
Stromgren 1979
Harltonldls et
al IQAA
al . I yOJ
Harltonldls et
,! (OCX
fli . i yoj
-------
Table 6. (Continued)
Species
Red macroalga,
Gracllarla verrucosa
Red macroalga,
Gracllarla verrucosa
Red macroalga,
Gracllarla verrucosa
C 1 1 late protozoan ,
Crlstlgera sp.
CIMate prdtozoan,
Euplotes vannus
Clllata protozoan,
Euplotes vannus
Polychaeta worm (juvenile),
Neanthes arenaceodentata
Polychaeta worm (adult),
Neanthes arenaceodentata
Polychaete worm (adult),***
Nereis dlverslcolor
Polychaete worm (adult),***
Nereis dlverslcolor
Salinity
Chemical (g/kg)
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc 34
sul fate
Zinc 35
chloride
Zinc 35
chloride
Zinc
sul fate
Zinc
sul fate
Zinc 0.35
sul fate 3.5
17.5
Zinc 17.5
sul fate
Duration
6 days
6 days
6 days
4-5 hr
48 hr
48 hr
28 days
28 days
96 hr
34 days '
Effect
BCF = 107.5***'*
BCF = 16.25***'*
BCF = 3.225***'*
Reduced growth
\0% reduction
In growth
lOOf reduction In
In growth
LC50
LC50
LC50
BCF - 26*57*
19.71
15.47
3.314
2.867
1.274
1.204
Concentration
Ug/L>*
65.38
653.8
6,538
50.63
10.000
100,000
900
1.400
ii:o88
94,000
18:888
25,000
25,000
100,000
100,000
250,000
250.000
Reference
Harltonldls et
al. 1983
Harltonldls et
al. 1983
Harltonldls et
al. 1983
Gray and Ventll la
1973; Gray 1974
Persoone and '
Uyttersprot 1975
Persoone and
Uyttersprot 1975
Relsh et al . 1976
Relsh et al . 1976
Mart-tone 1973
Polychaata worm (adult). Zinc
Ophryotrocha dladema chloride
31
48 hr
LC50
330-1,000
Parker 1984
-------
Table 6. (Continued)
Species Chealcal
Polychaate *orm. Zinc
Ophryotrocha dladema sulfate
Polychaata worm. Zinc
Ctenodrllus serratus sulfate
Polychaete worm (larva). Zinc
Capital la capltata sulfate
Polychaate worm (adult). Zinc
Capltella capltata sulfate
Mud snail (adult). Zinc
Nassarlus obsoletus chloride
Mud snail (adult). Zinc
Nassarlus obsoletus . chloride
Mud snail (adult). Zinc
Nassarlus obsoletus chloride
Blue mussel (adult). Zinc
Mytllus edulIs sulfate
Blue mussel (adult). Zinc
MytHus edul Is sulfate
Blue mussel (adult). Zinc
Mytllus edulIs chloride
Blue mussel (adult), Zinc
Mytllus edulIs chloride
Salinity
(oAg)
25
25
25
22
35
Duration
2t days
21 days
>16 days
28 days
72 hr
72 hr
72 hr
7 days
7 days
Appro*.
to days
6 days
4 days
14 days
Effect
Concentration
(»g/L)* Reference
Chronic value;**** 223.6
(acute-chronic ratio*
6.261)
Chronic value;**** 223.6
(acute-chronic ratio »
31.75)
Abnormal develop-
ment
LC50
Depressed oxygen ^2,000
consumption
Inhibited locomotor 10,000
bahav lor
MortalIty 50,000
IC50 >5,000
K50 (byssal thread 1,800
production)
LT50
(IO*C)
(I6*C)
(22 *C)
Reduced resis-
tance to thermal
shock
3,000
3.000
3,000
800-1,000
Relsh and Carr 1978
Relsh and Carr 1978
50-100 Relsh et al, 1974
1,250 Relsh et al. 1976
Maclnnes and Thurberg
1973
Maclnnes and Thirberg
1973
Maclnnes and Thurberg
1973
Martin et al. 1975
Martin et al. 1975
Cotter et al ., 1982
Cotter et al. 1982
-------
Table 6. (Continued)
Species Che»lca>
Blue mussel (adult). Zinc
Mytllus edulIs chloride
Blue mussel (embryo). Zinc
Mytllus edulIs chloride
Blue mussel (adult),
Mytllus edulIs
.Pacific oyster (larva). Zinc
Crassostrea qlgas sulfate
Pacific oyster (embryo). Zinc
Crassostrea glgas sulfate
Pacific oyster (larva). Zinc
Crassostrea glgas sulfate
Pacific oyster Zinc
(6-day larva), chloride
Crassostrea glgas
Pacific oyster Zinc
(6-day larva), ' chloride
Crassostrea glgas
Pacific oyster Zinc
(16-day larva), chloride
Crassostrea qlgas
Pacific oyster Zinc
(16-day larva), chloride
Crassostrea glgas
Pacflclc oyster (sperm). Zinc
Crassostrea qlgas chloride
Pacific oyster
(19-day larva),
Crassostrea qlgas
Salinity
(q/kq)
33.1
30
29
29
29
34
34
34
34
27
34
Duration
2-6 days
72 hr
3 days
6 days
2 days
5 days
4 days
4 days
4 days
4 days
60 mln
20 days
Effect
EC50 (shell growth)
EC50 (development)
to vel Iger)
Red uced she! 1
deposition
Abnormal development
and decreased growth
IJC50
Delayed and reduced
larval settlement
EC50 (growth)
LC50
EC 50 (growth)
LC50
Concentration
60
>96<314
>200
M25
241.5*
125
80
>100
95
>100
EC50 (tertll Izatlon) 443.6
success)
Reduced larval
settlement
10-20
Reference
Stromgren 1982
Dlnnel et al . 1983
Man ley et al . 1984
Brereton et al . 1973
Brereton et al .
1973
Boyden et al . 1975
Watl Ing 1982
Watl Ing 1982
Watl Ing 1982
Watl Ing 1982
Dlnnel et al . 1983
Watl Ing 1983
-------
Species
Pacific oyster
(19-day larva) ,
Crassostrea qlgas
Pacific oyster (Juvenile),
Crassostrea qlgas
Clam ( larva) ,
Mullnla lateral Is
Clam ( larva) ,
Mul Inla lateral ts
Qua hog clam ( larva) ,
Mercenar la mercenar la
Co pa pod (adult) , '
Paracalanus parvus
Copepod (adult) ,
Pseudod laptomus coronatus
Copepod (adult).
Acartla clausl
Copepod (adult).
Acartla simplex
Copepod (adult),
Scutel 1 Idlum sp.
Zooplankton (copepod
and euphausld)
Barnacle (adult) ,
Balanus balanoldes
Barnacle (adult) ,
Ralanus balanoldes
Che* leal
-
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chlor Ide
Zinc
chloride
Zinc
chloride
"•
Zinc
nitrate
Zinc
nitrate
Salinity
(g/kg)
34
34
34
34
24
35
30
30
35
35
"
-
-
Duration
6 days
23 days
72 hr
72 hr
8-10 days
24 hr
72 hr
72 hr
'
24 hr
24 hr
*«
2 days
5 days
Effect
EC50 (larval
settl Ing)
LC50
53 % mortal Ity
EC 50 (uptake of
calcium)
UC50
LC50
LC50
LC50
IC50
LC50
BAF = 1,670
LC90
LC90
(XMC«nTT*TI
-------
Specie*
Isopod (adult) ,
Idotea bait lea
Isopod (adult).
1 dotea bait lea
Isopod (adult) ,
Idotea bait lea
Isopod (adult),
Idotea bait lea
lospod (adult),
1 dotea bait lea
Isopod (adult),
Jaera alblfrons
lospod (adult),
Jaera alblfrons
1 so pod (adult) ,
Jaera alblfrons
Isopod (adult),
Jaera alblfrons
Grass shrimp (larva).
Pal aemonetes |>uqjo.
Chad leal
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fata
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
chloride
Salinity
(q/kg>
13.6
20.4
34.0
27.2-34.0
13.6
20.4
O*J 1
27.2
34.0
34.0
13.6
20.4
27.2
34.0
13.6
20.4
27.2
34.0
3.4
17-34
3-3!
Duration
48 hr
80 hr
W Ki-
ll 1
120 hr
120 hr
<24 hr
30 hr
TOK'*•
nt
54 hr
120 hr
120 hr
120 hr
120 hr
120 hr
35 days
IX
Effact
LT50
40* mortal Ity
No effect on osmo-
regulatory ability
LT50
Affected osmo-
requlatory abll Ity
80* mortal Ity
30* mortality
6* mortal Ity
16* mortality
84* mortal Ity
44* mortality
40* mortal Ity
22* mortal Ity
Affected osmo-
regulatory ability
No effect on osmo-
regulatory ability
Mortal Ity related
to sal In Ity and
temoarature: altered
HICen TT«T 101
(•9/0*
10,000
10,000
10,000
20,000
20,000
10,000
20,000
20,000
20,000
>250
i
Rafaranca
Jonas 1975
Jones 1975
Jones 1975
Jones 1975
Jones 1975
Jones 1975
Jonas 1975
Jones 1975
Jones 1975
McKenney 1
HcKanney a
1979,1981
development rates
-------
Table 6. (Continued)
Species
Pink shrimp (adult) ,
Panda 1 us montagul
American lobster (adult),
Homarus amerlcanus
American lobster (adult),
Homarus amerlcanus
Green crab (adult),
Carclnus maenas
Green crab (adult),
Carclnus maenas
Green crab (adult),
,c Carclnus maenas
oo
Green crab (adult),
Carclnus maenas
Mud crab ( larva) ,
Rh 1 thropanopeus harr 1 s 1 t
Mud crab ( larva) ,
Rhl thropanopeus harr Is) 1
Fiddler crab Sadult),
Uca pugl lator
Starfish (adult).
Aster las forbesll
Chemical
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
65Zlnc
chloride
65Zlnc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
sul fate
Salinity Concentration
(q/kq) Duration Effect J ,000
2,212
Portman 1968
Hay a et al . 1983
Hay a et al . 1983
Connor 1972
Portman 1968
Ren fro et al .
1975
Ren fro et al .
1975
Ben 1 j ts-C 1 aus and
Benljts 1975
Ben IJ ts-C 1 aus and
Benljts 1975
Wels 1980
Galtsoff and
Loosanoff 1937
-------
Table 6. (Continued)
Species Che*leaI
Sand dollar (sperm). Zinc
Dendraster excentrlcus chloride
Sand dollar (embryo). Zinc
Dendrastar excentrlcus chloride
Sea urchin (embryo). Zinc
Arbacla punctulata chloride
Sea urchin (embryo), Zinc
Arbacla punctulata chloride
Sea urchin (embryo). Zinc
Arbacla punctulata sulfate
Sea urchin (embryo), Zinc
Arbacla punctulata suI fate
Sea urchin (embryo). Zinc
Arbacla punctulata acetate
Sea urchin (gamete), Zinc
Arbacla punctulata chloride
Sea urchin (gamete), Zinc
Arbacla punctulata chloride
Green sea urchin (sperm). Zinc
S trongyIocentrotus chloride
droebachlensls
Green sea urchin (embryo), Zinc
S trongyIocentrot us chloride
droebachI ens Is
Red sea urchin (sperm), Zinc
StrongyIocentrotus chloride
franclscanus
Salinity
(g/kg)
27
30
27
30
27
Duration
60 mln
72 hr
21-42 hr
21-42 hr
21-42 hr
21-42 hr
21-42 hr
4-12 mln
4-12 mln
60 mln
5 days
60 mln
Effect
BC50 (fertll I-
zatlon success)
EC50 (development
to pi uteus stage)
Inhibited gastril-
lation
MortalIty and
Inhibition of
gastrulatlon
Inhibited gastru-
latlon
Mortal Ity and
Inhibition of
gastrulatlon
Inhibited gastru-
latlon
Stimulated sperm
motlllty
Reduced sperm
mot) I Ity
EC50 (fertll I-
zatlon success)
Concentration
(»a/L)* Reference
28 Olnnel et al. 1983
580-820 Olnnel et al . 1983
1,199 Waterman 1937
3,998 Waterman 1937
810
3,564
1,634
3,269
147.6
382.8
EC50 (development >26.6<50.6
to pi uteus stage
Waterman 1937
2,314 Waterman 1937
BC50 (fertll I-
zatlon success)
313.3
Waterman 1937
Young and Nel son 1974
Young and Nelson 1974
Dlnnel et al. 1983
Dlnnel et al . 1983
Dlnnel et al. 1983
-------
Table 6. (Continued)
Salinity
ChewleaI (g/kg) Duration
Effect
Concentration
(H9/L)» Reference
Purple sea urchin (gamete),
S trongy 1 ocentrotu s
purpuratus
Purple sea urchin (gamete),
Strongy 1 ocentrotus
purpuratus
Purple sea urchin (gamete),
Strongy locentrotus
purpuratus
Purple sea urchin (sperm),
Strongy locentrotus
purpuratus
Purple sea urchin (embryo),
Strongy locentrotus
purpuratus
Atlantic herring (embryo),
Clupea harengus
Atlantic herring (embryo),
Clupea harengus
Atlantic herring (embryo),
Clupea harengus
Atlantic herring (embryo
and larva),
Clupea harengus
Atlantic herring (larva),
Clupea harengus
Atlantic herring (larva),
C lupea harengus
Atlantic barring (larva),
Clupea harengus
-
-
-
Zinc
chloride
Zinc
chloride
Zinc
sulfate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sul fate
Zinc
sulfate
Zinc
sulfate
100-400 mln
0-100 mln
100-400 mln
i
27 60 mln
30 5 days
21 17 days
21 17 days
21 17 days
21 27 days
21 27 days
21 27 days
2! 27 days
Enhanced sperm
2,000
>100
6,000
>50
>500
>2,000
>6.000
Tlmourlan and
Matchmaker 1977
T 1 mour 1 an and
Watchmaker 1977
Tlmourlan and
Watchmaker 1977
Dlnnel et al. 1983
Dlnnel et al . 1983
Somasundaram et al
1984 a
Sonasundaram et al
1984 a
Somasundarum et al
1984 a
Somasundaram et al
1984a
Somasundaram et al
1984a
Somasundaram et al
1984 a
Somasundaram et al
1984a
-------
TabU 6. (Continued)
Species
Atlantic herring (larva),
Clupea harengus
Co ho salmon (sperm),
Oncorhynchus klstuch
Rainbow trout (yearling),
Salmo galrdnerl
Atlantic salmon (smolt),
Salmo salar
Mummlchog (adult),
Fundulus heteroclltus
Mummlchog (adult),
Fundulus heteroclltus
Mummlchog (adult),
Fundulus heteroclltus
Mummlchog (adult),
Fundulus heteroclltus
Mummlchog (adult),
Fundulus heteroclltus
Mummlchog (adult),
Fundulus heteroclltus
Chemical
Zinc
sulfate
Zinc
chloride
Zinc
sul fate
Zinc
sul fata
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chlor Ide
Salinity
(Q/kq)
21
27
5.8
It. 5
16.3
24.1
5.8
It. 5
16.3
24.1
24
24
24
20
20
20
Duration
14 days
60 mln
48 hr
48 hr
192 hr
48 hr
48 hr
96 hr
96 hr
96 hr
Effect
Ultrastructural
changes In bra In
eel Is and somatic
muscle tissues
EC50 (fertll I-
zatlon success)
LC50
LC50
100$ survival
1001 mortal Ity
BCF =• 7f643«»»»f
(fish that died
during exposure)
BCF =• 35.61 »»»•*
BCF - 18.
30$ mortal Ity;
hi sto pathological
lesions In oral
epithelium
Concentration
<»g/L)» Ref
>500 Somasundaram et al
~~ t984c,d
1,208 Dlnnel et al. 1983
27,000*
64,000;
64,ooo;
34,000'
16,000*
3 5, 000 *
32, 000 I
27,000f
43.000
157,000
157,000
36,000
60,000
60,000
Herbert and
Make ford 1964
Herbert and
Makeford 1964
Elsler 1967
Elsler 1967
Elsler 1967
Elsler and
Gardner 1973
Elsler and
Gardner 1973
Elsler and
Gardner 1973
-------
Table 6. (Continued)
Species
Mummlchog (adult),
Fundulus heterocl Itus
Mummlchoq (adult),
Fundulus heterocl Itus
Mummlchog (embryo),
Fundulus heterociltus
Mummlchog (juvenile),
Fundulus heterociltus
Mummlchog (juvenile),
Fundulus heterociltus
Mosqultof Ish (adult) ,
Gambusla aft In Is
Mosqultof Ish (adult),
Gambusla afflnls
i — • "
NJ Spot ( juvenile) ,
Lelostomus xanthurus
Spot ( juvenile) ,
Lelostomus xanthurus
Salinity
CheMlcal (q/kg)
Zinc
chloride
Zinc 10-30
chloride
Z Inc 30
chloride
Zinc 25
chloride
Z Inc 30
chloride
tftt 30
ttft 30
fttt 30
ttft 30
Duration
14 days
14 days '
96 Ir
70 days
56 days
120 days
120 days
28 days
28 days
Conceit trat lot
Effect f»g/L)*
Increased activity
of 1 Iver enzyme
Enhanced regeneration
of tall fin and
am el (orated effects
of methyl mercury
Ainel (orated terato-
gen Ic effects of
methyl mercury
Inhibited scale
calcification
BCF = 33.91-240.0
( scales)
BCf » 8* ( uptake 4
Trent Mater alone)
BAF =45* (uptake 4
from food ana water)
BCF = 3* (uptake %
from Mater alone)
BAF = 28* (uptake
from food and Mater)
2,200
>_1,000
10,000
760-
7,100
210-
7,880
650
650
650
650
1
Reference
Jacklm 1973
Me Is and We Is 1980
Wats et si, 198!
Sauer and Matabe 1984
Sauer and Watabe 1984
Mlljls.and
Sunda 1984
Mlllls and
Sunda 1984
Ml II Is. and
Sunda 1984
Will Is. and
Sunda 1984
* Concentration of zinc, not the chemical.
** Field study.
*"* Converted from dry weight to wet weight basis.
**** Static test; concentrations not measured.
* Derived from authors' data or graph.
** Geometric mean of data from four stations, but concentrations In water varied widely.
ttt
tttt
Animals obtained from sediment heavily contaminated with zinc.
N Itrllotr lacetlc acid (NTA) was used to buffer the concentration of zinc Ions.
-------
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