&ER&
United States
Environmental Protection
Agency
Office of Water
Regulations and Standards
Criteria and Standards Division
Washington, DC 20460
EPA 440/5-88^301
February 1988
Water
Ambient
Water Quality
Criteria
for
Chloride-1988
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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
CHLORIDE
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORY
DULUTH, MINNESOTA
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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 accession No. PB88-175 047
11
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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.
Guidance 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 has been developed by EPA.
William A. Whittington
Di rector
Office of Water Regulations and Standards
111
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ACKNOWLEDGMENTS
Duane k. Benoit
(author)
Environmental Research Laboratory
Duluth, Minnesota
Charles ET. Stephan
(document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
IV
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CONTENTS
Page
Foreword i i i
Acknowl edgments i v
Tables vi
Introduction 1
Acute Toxicity to Aquatic Animals 2
Chronic Toxicity to Aquatic Animals 3
Toxicity to Aquatic Plants 4
Bi oaccumulat ion 5
Other Data 5
Unused Data 6
S umma ry 7
National Criteria , 8
Implementation 9
References 25
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TABLES
Page
1. Acute Toxicity of Chloride to Aquatic Animals 11
2. Chronic Toxicity of Chloride to Aquatic Animals 16
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios 17
4. Toxicity of Chloride to Aquatic Plants '. 19
5. Other Data on Effects of Chloride on Aquatic Organisms - 22
VI
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Introduction
The major anthropogenic sources of chloride in surface waters are deicing
salt, urban and agricultural runoff, and discharges from municipal wastewater
plants, industrial plants, and the drilling of oil and gas wells (Birge et al.
1985; Dickman and Gochnauer 1978; Sonzogni et al. 1983). Beeton (1965)
reported that concentrations of chloride had been rising in Lake Erie, Lake
Ontario, and Lake Michigan since the early 1900s, and in Lake Huron since the
1950s, but Sonzogni et al. (1983) stated that the rate of change of chloride
inputs to the Great Lakes had stabilized or decreased.
Chloride has long received special attention from researchers interested
in fish. In 1937, Ellis discussed the concept that "fresh-water fish tolerate
an osmotic pressure of the external medium equal to that of their own blood if
the various salts and substances in the water are balanced against each other
so as to exclude the specific toxic effects" and presented supporting data.
Chloride has been used as a nutrient and prophylactic for fish (Hinton and
Eversole 1979; Phillips 1944). It has also been suggested for use as a
reference toxicant (Adelman and Smith 1976a,b; Threader and Houston 1983).
Because anthropogenic sources of chloride are unlikely to pose a threat
to saltwater species, this document concerns effects on only freshwater
species. Unless otherwise noted, all concentrations of chloride in water
reported herein from toxicity and bioconcentration tests are expected to be
essentially equivalent to dissolved chloride concentrations. All
concentrations are expressed as chloride, not as the chemical tested. 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), hereinafter referred to as the Guidelines, and the response to
public comment (U.S. EPA 1985a) is necessary in order to understand the
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following text, tables, and calculations. Results of such intermediate
calculations as recalculated LC50s and Species Mean Acute Values are given to
four significant figures to prevent roundoff errors in subsequent
calculations, not to reflect the precision of the value. The latest
comprehensive literature search for information for this document was
conducted in August 1985; some more recent information was included.
Acute Toxicitv to Aquatic Animals
Data that may be used, according to the Guidelines, in the derivation of
a freshwater Final Acute Value for chloride are presented in Table 1. When
compared on the basis of mg of chloride/L, the chlorides of potassium,
calcium, and magnesium are generally more acutely toxic to aquatic animals
than sodium chloride (Biesinger and Christensen 1972; Dowden 1961; Dowden and
Bennett 1965; Hamilton et al. 1975; Patrick et al. 1968; Trama 1954). Only
for sodium chloride, however, are enough data available to allow derivation of
a water quality criterion. In addition, it seems likely that most
anthropogenic chloride in ambient water is associated with sodium, rather than
potassium, calcium, or magnesium (Dickman and Gochnauer 1978; Sonzogni et al.
1983).
Results listed in Table 1 from Dowden and Bennett (1965), Hamilton et al.
(1975), and Kostecki and Jones (1983) were obtained from 24- and 48-hr tests,
rather than the 96-hr tests specified in the Guidelines. Use of such results
is considered acceptable for chloride because the acute values changed little
from 24 to 48 or 96 hours, depending on the species, in acute toxicity tests
on chloride. For example, ratios of 24-hr and 48-hr LCSOs for sodium chloride
with a midge and a daphnid were 0.91 and 0.81, respectively (Dowden and
Bennett 1965; Thornton and Sauer 1972). Reed and Evans (1981) obtained a
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ratio of 1.0 for 24-hr and 14-day LCSOs determined with the channel catfish,
bluegill., and largemouth bass (Table 5). Adelman and Smith (1976a,b) and
Adelman et al. (1976) obtained ratios of 24- and 96-hr LCSOs of 0.74 and 0.97
with goldfish and fathead minnows, respectively, in tests in which the fish
were fed (Table 5).
Adult fingernail clams were more sensitive than juveniles (Anderson
1977), but for the American eel (Hinton and Eversole 1978) and the bluegill
(Cairns and Scheier 1959) smaller organisms were slightly more sensitive than
larger ones. No pronounced relationships have been observed between the acute
toxicity of chloride to freshwater animals and hardness, alkalinity, or pH.
Species Mean Acute Values (Table 1) were calculated as geometric means of
the acute values from tests on sodium chloride, and then Genus Mean Acute
Values (Table 3) were calculated as geometric means of the Species Mean Acute
Values. Of the twelve genera for which acute values are available, the most
sensitive genus, Daphnia. was only 6 times more sensitive than the most
resistant, Angui11 a. Invertebrates were generally more sensitive than
vertebrates. The Final Acute Value for chloride was calculated to be 1,720
mg/L using the procedure described in the Guidelines and the Genus Mean Acute
Values in Table 3. The acute value for Daphnia pulex. is lower than the Final
Acute Value.
Chronic Toxicity to Aquatic Animals
The available data that are usable according to the Guidelines concerning
the chronic toxicity of chloride are presented in Table 2. In the life-cycle
test with Daphnia pulex. survival was as good as in the control treatment at
chloride concentrations up to 625 mg/L (Birge et al. 1985). At 314 mg/L.
reproduction was as good as in the control, but at 441 and 625 mg/L,
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reproduction was reduced by 27 and 39%, respectively. Thus, the chronic
limits are 314 and 441 mg/L, the chronic value is 372.1 mg/L, and the
acute-chronic ratio is 3.951.
In an early life-stage test with rainbow trout, a chloride concentration
of 2,740 mg/L killed all the exposed organisms (Spehar 1987). Survival was
54% at 1,324 mg/L, but was 97% or higher at 643 mg/L and at two lower
concentrations and in the control treatment. The mean weights of the fish
alive at the end of the test at 1,324 mg/L and the lower tested concentrations
were within 5% of the mean weight of the fish in the control treatment. The
chronic value and the acute-chronic ratio obtained with, the rainbow trout were
922.7 mg/L and 7.308, respectively.
In an early life-stage test with the fathead minnow, Pimephales promelas,
Birge et al. (1985) found that weight was as good as in the control treatment
up to a chloride concentration of 533 mg/L. Survival was reduced 9% by a
concentration of 352 mg/L and was reduced 15% by 533 mjc/L. The chronic value
is 433.1 mg/L, and the acute-chronic ratio is 15.17;
The three acute-chronic ratios available for chloride are 7.308, 15.17,
and 3.951 (Table 3). The geometric mean of these three is 7.594, which is
used as the Final Acute-Chronic Ratio. Division of the Final Acute Value by
the Final Acute-Chronic Ratio results in a Final Chronic Value of 226.5 mg/L,
which is substantially lower than all three chronic values in Table 2.
Toxicitv to Aquatic Plants
Data on the toxicity of chloride to aquatic plants show a wide range of
sensitivities (Table 4). The alga, Spirogvra setiformis. was extremely
sensitive to the effects of chloride; inhibition of growth, chlorophyll, and
fixation of 14C occurred at 71 mg/fc (Shitole and Joshi 1984). Growth of
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Netriurn digitus was affected at 200 mg/L, but the other sixteen tested species
were affected by concentrations ranging from 642 to 36,400 mg/L. A Final
Plant Value, as defined in the Guidelines, cannot be obtained because no test
in which the concentrations of chloride were measured and the endpoint was
biologically important has been conducted with an important aquatic plant
species.
Eyster (1962) reported that a concentration of 0.18 mg/L stimulated the
growth of many algae, and Sonzogni et al. (1983) discussed the possibility
that concentrations above 10 mg/L might shift phytoplanktbn communities toward
nuisance, taste-and-odor-causing blue-green algae. When chloride was added to
a small stream at a concentration of 610 mg/L, the algal density decreased
whereas the bacterial density increased.
Although most of the data on toxicity of chloride to freshwater plants
has been obtained with sodium chloride, some evidence indicates that a similar
cation-anion toxicity relationship exists for both aquatic plants and
animals. Patrick et al. (1968) demonstrated that potassium chloride was 2.3
times more toxic to a diatom than sodium chloride (Table 4), although calcium
chloride was 1.3 times less toxic than sodium chloride. Tuchman and Stoermer
(Manuscript a,b) found that potassium chloride had a greater inhibitory effect
on algal population dynamics and nutrient uptake than sodium chloride.
Bioaccumulation
No data that are usable according to the Guidelines are available
concerning the accumulation of chloride by freshwater species.
Other Data
Additional data on the lethal and sublethal effects of chloride on
freshwater species are presented in Table 5. Anderson (1944,1948) and
5
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Biesinger and Christensen (1972) found the same cation-anion toxicity
relationship that is apparent in Table 1. Sreenivasan et al. (1979) reported
that the rotifer, Brachionus rubens. tolerates chloride up to at least 1,400
mg/L. Wallen et al. (1957) reported that magnesium chloride-was less toxic to
the mosquitofish than "sodium chloride; however, these tests were conducted in
very turbid water and therefore the results might be atypical. A concen-
tration of 13% sodium chloride in the diet of trout caused no ill effects,
whereas 25 mg in gelatin capsules caused edema and death of brook trout
(Phillips 1944). Food consisting of 12% sodium chloride did not affect growth
of Atlantic salmon (Shaw et ai. 1975). Hasan and Macintosh (1986) and Tomasso
et al. (1980) reported that chloride reduced the acute toxicity of nitrite to
fish.
Unused Data
Some data concerning the effects of chloride on aquatic organisms and
their uses were not used because the tests were conducted with species that
are not resident in North America (e.g., Coetzee and Hattingh 1977; Das and
Srivastava 1978; Ferri and Sesso 1982; Katz and Ben-S^sson 1984; Meech and
Thomas 1980; Schiewer 1974,1984; Stangenberg 1975; Vaidya and Nagabhushanam
1979). Jennings (1976) compiled data from other sources. Data were not used
when chloride was a component of an effluent (Birge et al. 1985). Reports by
Batterton et al. (1972), Hosiaisluoma (1976), and Palmer and Maloney (1955)
provided no usable data on the toxicity of chloride. Arnold (1974), Davis et
al. (1972), and Edmister and Gray (1948) did not adequately describe their
test procedures or results or both.
Results of some laboratory tests were not used because the tests were
conducted in distilled or deionized water without addition of appropriate
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salts (e.g., Kardatzke 1980,1981; Lee 1973; .Mahajan et al. 1979; Pappas and
Pappas 1983; Stamper 1969; Thornton and Wilhm 1974,1975: Zaim and Newson 1979)
or were conducted in chlorinated or "tap" water (e.g., Kumar and Srivastava
1981). Christensen (1971/72) and Christensen and Tucker (1976) exposed plasma
or enzymes. Length of exposure was not reported by Batterton and Van Baalen
(1971). High control mortalities occurred in tests reported by Lewis (1971).
Tests conducted without controls (e.g., Vosjan and Siezen 1968) or with too
few test organisms (e.g., Leblanc and Surprenant 1984) were also not used.
Hughes (1968,1973) did not adequately acclimate the test organisms. Ten-day
LCSOs (Threader and Houston 1983) were not used because the fish had not been
fed during the tests.
Many studies were not used because they addressed the metabolism,
regulation, or transport, rather than toxicity. of chloride (e.g., Carrasquer
et al. 1983; Castille and Lawrence 1981; De Renzis and Maetz 1973; Greenway
and Setter 1979a,b; Hinkle et al. 1971; Konovalov 1984; McCormick and Naiman
1984; Ooshima and Oguri 1974; Perry et al. 1984; Shomer-Ilan and Waisel 1976;
Sullivan et al. 1981; Ticku and Olsen 1977). Some references were not used
because they were foreign-language reports for which no translation was
available and no useful data could be obtained from the English abstracts
(e.g., Frahm 1975; Mushak 1968; Schiewer 1976; Turoboyski 1960).
Summary
Although few data are available concerning the toxicity of any chloride
salt other than sodium chloride, the data that are available indicate that,
when compared on the basis of mg of chloride/L, the chlorides of potassium,
calcium, and magnesium are generally more toxic to freshwater species than
sodium chloride. Based on tests on sodium chloride, the acute sensitivities
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of freshwater animals to chloride ranged from 1,470 mg/L for Daphnia pulex to
11,940 mg/L for the American eel. Invertebrate species were generally more
sensitive than vertebrates. Results from tests with a variety of species show
that if freshwater animals do not die within the first 24 hr of the test, they
probably will not die during periods ranging from 48 hr to 11 days. No
relationships have been observed between the acute toxicity of chloride to
freshwater animals and hardness, alkalinity, pH, or life-stage of the test
organisms.
A life-cycle test with Daphnia pulex and early life-stage tests with the
rainbow trout and fathead minnow produced chronic values of 372.1, 922.7, and
433.1 mg/L, respectively. The acute-chronic ratios were calculated to be
3.951 for Daphni a pulex. 7.308 for rainbow trout, and 15.17 for the fathead
minnow. Freshwater plants were affected at concentrations of chloride ranging
from 71 to 36,400 mg/L. No data are available concerning bioaccumulation of
chloride by freshwater organisms.
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 of dissolved
chloride, when associated with sodium, does not exceed 230 mg/L more than once
every three years on the average and if the one-hour average concentration
does not exceed 860 mg/L more than once every three years on the average.
This criterion probably will not be adequately protective when the chloride is
associated with potassium, calcium, or magnesium, rather than sodiuit In
8
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addition, because freshwater animals have a narrow range of acute
susceptibilities to chloride, excursions above this criterion might affect a
substantial number of species.
Implementation
As discussed in the Water Quality Standards Regulation (U.S. EPA 1983a)
and the Foreword to this document, a water quality criterion for aquatic life
has regulatory impact only after it has been adopted in a State water quality
standard. Such a standard specifies a criterion for a pollutant that is
consistent with a particular designated use. With the concurrence of the U.S.
EPA, States designate one or more uses for each body of water or segment
thereof and adopt criteria that are consistent with the use(s) (U.S. EPA
I983b,1987). In each standard a State may adopt the national criterion, if
one exists, or, if adequately justified, a site-specific criterion.
Site-specific criteria may include not only site-specific criterion
concentrations (U.S. EPA 1983b), but also site-specific, and possibly
pollutant-specific, durations of averaging periods and frequencies of allowed
excursions (U.S. EPA l~985b). The averaging periods of "one hour" and "four
days" were selected by the U.S. EPA on the basis of data concerning how
rapidly some aquatic species react to increases in the concentrations of some
pollutants, and "three years" is the Agency's best scientific judgment of the
average amount of time aquatic ecosystems should be provided between
excursions (Stephan et al. 1985; U.S. EPA 1985b). However, various species
and ecosystems react and recover at greatly differing rates. Therefore, if
adequate justification is provided, site-specific and/or pollutant-specific
concentrations, durations, and frequencies may be higher or lower than those
given in national water quality criteria for aquatic life.
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Use of criteria, which have been adopted in State water quality
standards, for developing water quality-based permit limits and for designing
waste treatment facilities requires selection of an appropriate wasteload
allocation model. Although dynamic models are preferred for the application
of these criteria (U.S. EPA 1985b), limited data or other considerations might
require the use of a steady-state model (U.S. EPA 1986). Guidance on mixing
zones and the design of monitoring programs is also available (U.S. EPA
1985b,1987).
10
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Table (. Acute Toxicity of Chloride to Aquatic Aniwals
Species
Snoi 1 ,
Physo gyring
Snoi 1 ,
Physo heterost ropho
F i ngernai 1 c lam
(adul t >5 cm) ,
Muscu li urn tronsversum
tingerno.il c'lorn
(adult >5 cm) ,
Muscul i urn tronsversum
Fi ngernai 1 cl am
( juveni le <5 cm) ,
Uuscul i urn transversum
F i ngernai 1 c 1 am
( j uven i 1 e <5 cm) ,
Muscu 1 i urn t ransyersum
F i ngerna i 1 c 1 am
( j uven i 1 e < 5 cm) ,
Muscu 1 i urn transyersum
Clodoceran (1st instar),
Dophn i a mag no
Method" Chemical
F , M Sodi urn
chloride
S, U Potassium
chloride
S, M Potassium
chlor i de
S, M Potassium
chloride
S, M Potassium
chl or i de
S , M Potass i urn
chloride
S, M Potassium
chloride
S , U Sodi um
chloride
Hardness LC5D Species Mean
(rag/L as or EC50 Acute Value
CaCfO (mq/l)b («
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Table I (continued)
Species
Clodoceron,
Dopfani o moqno
Clodoceron,
Dophni a moqno
Ctadoceran,
Dophni o moqna
Clodoceron ,
Dophn i o moqno
Cl odoceran ,
Oophnia moqno
Clodoceron,
Oophnio moqno
Clodoceron,
Dophni o moqna
Cl adoceran ,
Oophnio moqna
Cl adoceran ,
Dophni o maqno
Cladoceran,
Dophni o maqno
Hardness
("9/L os
Method41 CheMical CaCOj
S, U Potassium
chl or i de
S, U Calcium
chlor i de
S, U Sodium
chl or i de
S, U Calcium
chl ori de
S, U Magnesium
chloride
S, U Sodium
chlor i de
S, U Potassium 45
chlori de
S, U Calcium 45
chl or i de
S, U Magnesium 45
chlori de
S, U Sodium 45
chlor i de
LC50 Species Uean
or EC50 Acute Value
(ma/L)b (M/UC
171
486
2,024
1,923
2,774
3,583
86
92
409
2,565 2,650
Reference
Dowden 1961
Dowden 1961
Dowden 1961
Dowden and Bennett
1965
Dowden and Bennett
1965
Dowden and Bennett
1965
Biesinger and
Christensen 1972
Biesinger and
Christensen 1972
Biesinger and
Christensen 1972
Biesinger and
Christensen 1972
12
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Table I. (continued)
Species
Cladoceran,
Dophni a pul ex
Isopod,
Li rceus font i nal i s
Coddisfly,
Hvdropt i la anqusta
Uosqui to ( larva) ,
Cul ex sp.
Midge,
Ch i ronomus ott enuot us
Midge,
Cr i cotopus t r i f asc i a
Midge,
Cr i cotopus t r i f asc i a
Ameri can eel ( 55 mm) ,
Anqui 1 1 a rost rat a
Ameri can eel (972 mm) ,
Anqui 1 1 a rost rota
Ra-i nbow trout ,
Sal mo qairdneri
Rai nbow trout ,
Sa Imo qa i rdner i
Hardness
("9/L as
Method" Chemical CaCO,)
R, M Sodium 93
chl ori de
F, M Sodium IOQ
chlor i de
S. U Sodium 124
chl ori de
S, U Sodium
chl ori de
S , U Sod i um
chl or i de
S, U Potassium 124
chl or i de
S, U Sodium 124
chl or i de
S, U Sodium 44
chloride
S, U Sodium 44
chloride
R, U Sodi um
chl 01 i de
r, M Sodium 46
chloride
LC5U
or EC50
(.Q/L)b
1,470
2,950
4,039f
6,222f
4,900
1 ,434
3,795
10,900
13,085
3,336"
6,743
Species Mean
Acute Value
U«/L)C
1 ,470
2,950
4,039
6,222
4,900
-
3,795
II ,940
Reference
Dirge et al
Birge et al
Hamilton et
Oowden and
1965
. 1985
. 1985
al. 1975
Bennett
Thornton and Sauer
1972
Homi 1 ton et
Kami 1 ton et
Hinton and
1978
Hinton and
al. 1975
al. 1975
Cversol e
Eversol e
1979
Kost eck i and Jones
6,743
1983
Spehar 1987
13
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Table I. (continued)
Species
Goldfish,
Carassius auratus
Goldfish.
Carassius auratus
Fathead minnow,
Pimepholes promelas
Bluegi 1 1 ,
Lepomis macrochi rus
Bluegi 1 1 ,
Lepomis macrochirus
Bl uegi 1 1 ,
Lepomis macrochirus
Bluegill (3.9 cm),
Leoomis macrochi rus
Bluegill (6.1 cm),
Le.Domis macrochirus
Bluegill (14.2 cm),
Lepomis macrochirus
Bluegi 1 1 ,
Lepomis macrochirus
Hardness
(•9/L as
Method0 CNe.ical CaCO,)
w__^__ «_ __— » J1*
S. U Sodium
chlori de
S, U Sodium 149
chlori de
r, U Sodium 100
chlori de
S, U Potassium 39
ch 1 or i de
S, U Calcium 39
chl or i de
S, U Sodium 39
chlor i de
S, U Calcium
chlori de
S, U Calcium
chlori de
S, U Calcium
chloride
S, U Potass i urn
chl or i de
LC50 Species Mean
or CC50 Acute Value
(«a/L)k (.«/Lie
8,3889
9,455h 8,906
6,570 6.570
956
6,804
7,846
6,080
6,080
7,232
965
Reference
Oooden and Bennett
1965
Threader and Houston
1983
Birge et ol 1985
Trama 1954
Troma 1954
Trama 1954
Cairns and Scheier
1959
Cai rns and Schei er
1959
Ca i rns and Schei er
1959
Academy of Natural
Sciences I960,
Patri ck et al. 1968
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Table I. (cont inued)
Species
Bluegi I 1 ,
Lepomi s mocroch I rus
Bluegi 1 1 ,
Lepomi s mocrochi rus
Bluegi 1 1 ,
Lepomi s mocroch I rus
Bluegi 1 1 ,
Lepomi s mocroch i rus
Bluegi II ,
Lepomis mocrochi rus
Bluegi II .
Lepomis mocrochi rus
Hardness
(»9/L as
Method" Chemical CaCOj
i-1 —
S. U Calcium
chl or i de
S, U Sodium
chl ori de
S, U Potassium
chlori de
S, U Calcium
chlori de
S, U Sodium
chlori de
F, M Sodium 100
chlori de
LCSO Species Mean
or CC50 Acute Value
(•Q/L)b Ua/Uc
6,816
7,897
2.6409
5,3449
8.6169
5,870 5,870
Reference
Academy of Natural
Sciences I960;
Patrick et al . 1968
Academy of Natural
Sciences I960;
Patrick et al . 1968
Dowden and Bennett
1965
Dowden and Bennett
1965
Dowden and Bennett
1965
Birge et al . 1985
S = static; R = renewal, F = flow-through; U = unmeasured; U = measured
Concentration of chloride not the chemical
0 Only data obtained with sodium chloride were used in calculation of Species Mean Acute Values Data for other
salts are presented for comparison purposes only.
Test temperature = 7°C; the other tests with this species were ot 17°C.
e Not used in calculations because quantitative values are available for this species
This value is from a 48-hr test (see text)
" This value is from a 24-hr test (set- text)
This value »a:; derived from the published 'jr
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Table 2. Chronic Toxicity of Chloride fo Aquatic Animals
Species
Cladoceron ,
Dophni o pulex
Rainbow trout,
Solmo qoi rdner i
Fathead minnow,
Pimepholes promelas
Test0 Chemical
LC Sodium
chlor ide
ELS Sodium
chloride
ELS Sod i urn
chl or i de
Hardness
H/L 99
CaCO,)
FRESHWATER SPECIES
100
46
100
Limits Chronic Value
(.a/L)b l-g/Ll
314-441 372.1
643-1,324 922.7
352-533 433.1
Reference
Birge et al. 1985
Spehor 1987
Birge et al . 1985
LC = life-cycle or partial life-cycle; ELS = early life-stage.
Measured concentrations of chloride.
Acute-Chronic Ratio
Species
Cladoceran,
Daphn i o pulex
Ra i nbo* trout,
Solmo qoi rdner i
Fathead minnow,
P i mepholes promelos
Hardness
(«g/L as
_CaC03J_
100
46
IUU
Acute Value
(ma/I)
1 ,470
Chronic Value
(-Q/II
372 1
Ratio
3.951
6,743
6,570
922 7
433 I
7 308
1517
16
-------
Table 3. Ranked Genus Uean Acute Values with Species Mean Acute-Chronic Ratios
Genus Uean
Acute Value
Rank0 Ufl/Ll
12 11,940
II 8,906
10 6,743
9 6,570
8 6,222
7 5.870
6 4,900
5 4,039
4 3,795
3 2,950
2 2,541)
Species
FRESHWATER SPECIES
Amer i con eel ,
Anqui 1 1 a rost rata
Goldfish,
Carass i us aurat us
Rai nbow trout ,
Sal mo qairdneri
Fathead mi nnow,
Himephol es promel as
Mosqui to,
Cul ex sp.
Bluegi 1 1 ,
Lepomis macrochi rus
Midge,
CHironomus attenuatus
Caddisf ly ,
Hydropt i 1 a anqust a
Midge,
Cri cotopus tr i f asc i a
Isopod,
L i reus f ont i nal i s
Snail,
Pliy^a qvrina
Species Uean
Acute Value
(«a/Hb
II ,940
8.9U6
6,743
6.57U
6,222
5,870
4,901)
4,039
3,795
2,950
2,540
Species Uean
Acute-Chronic
Ratio6
7.308
15.17
17
-------
Table 3. (continued)
Ronfc0
1
Genus Mean
Acute Value
Ua/D
1 ,974
Species
Cl adoceran ,
Dophn i a moqno
Cl adoceran ,
Daphnio pul ex
Species Ueon
Acute Value
2,650
1 ,470
Species Mean
Acute-Chronic
Ratio0
_
3 951
Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
b from Table I
0 From Table 2
Final Acute Value = I,720 mg/L
Criterion Maximum Concent rat ion = (I,720 mg/L) / 2 = 860.0 mg/L
Final Acute-Chronic Ratio = 7.594 (see text)
Final Chronic Value = (1,720 mg/L) / 7.594 = 226 5 mg/L
18
-------
Species
Table 4. Toxicity of Chloride to Aquatic Plants
Concentration
Chemical
Durat ion
(days)
Effect
Reference
FRESHWATER SPECIES
Alga,
AnocystIs nIdulons
Sod i urn
chloride
Growth inhibition >24,300 Schlexer 1974
Alga,
Anoboeno variabilis
Sodium
chloride
Crontti Inhibition
14.300 Schfewer 1974
Alga, Sodium
Chlomvdomonos reinhardtii chloride
Alga, Sodium
Chlorello emerson ii chloride
3-6
8-14
Growth inhibition
Growth inhibition
3,014 Reynoso et al . 1982
7.000 Setter et al. 1982
Alga,
Chl orelI a fusco fusca
Sodi urn
chlori de
Growth inhibition
18,200 Kessler 1974
Alga, Sod i urn
ChlorelI a fusco rubescens chloride
28
Growth i nhi bi t ion
24,300 Kessler 1974
Alga, Sodium
ChlorelI a fusco vacuoloto chlori de
28
Growth i nh i bi t i on
24,300 Kessler 1974
Alga,
Chlorella kessleri
Sod i urn
chloride
28
Growth i nhi bi t ion
18,200 Kessler 1974
Alga,
ChlorelI a Iuteovi r i d i s
Sod i urn
chloride
28
Growth i nhi bi t i on
36,400 Kessler 1974
19
-------
Table 4. (continued)
Species
Alga,
Chi orel la mi nut iss'ima
Alga,
Chlorel la protot hecoi des
Alga,
Chlorel la soccharophi 1 io
Alga,
Chlorel la vul gar i s
Alga,
Chlorel la vulqoris
Alga,
Chlorella vulqoris tertia
Alga,
Chlorel la vul gar is vul aoris
Alga,
Chlorel )o zo! i nqiensis
Alga,
Pj thophoro oedoqoni a
Alga,
Spiroavra setiformis
Desmi d ,
Net r i um d i q i t us
Durot ion
Chemical (days)
Sodium 26
chloride
Sodium 28
chloride
Sodi um 28
chloride
Potassium 90-120
chloride
Sodium 90-120
chloride
Sodi um 26
chl or i de
Sodium 28
chlor i de
Sod i um 28
chlor i de
Sodium 10
chl or i de
Sodi um 1 0
chlor i de
Sod i um 21
cli 1 or i de
Concentration
Effect («
-------
Table 4. (continued)
Species
Desmi d,
Net r i urn d i.q i t us
Di atom,
Ni tzschi o 1 i nearis
Oi atom,
Ni tzschi a 1 i near! s
Diatom,
Ni t zschi a 1 i near i s
Eurasian watermi 1 foi 1 ,
Myri ophyl 1 urn spicatum
Eurasi an natermi 1 foi 1 ,
Myri ophyl 1 urn spi cot urn
Angiosperm (seed) ,
Pot omoqet on pect i not us
Angiosperm (9-wk old
plants) ,
Potamoqeton pectinotus
Angiosperm (13-wk old
pi ants) ,
Potamoqeton pectinatus
Duration
Chemical (days)
Sodium 21
chl ori de
Potassium 5
chlori de
Cal c i urn 5
chloride
Sodium S
chloride
Sodium 32
chlori de
Sodium 32
chlori de
Sodium 28
chl ori de
Sodium 35
chlori de
Sodium 35
chloride
Concentration
Effect («a/Lla
Growth inhibition 250
EC50 642
EC50 2,003
EC50 1,482
507. reduction in 3,617
dry weight
502 reduction in 4,964
dry weight
Reduced germination 1,820
Reduced dry weight 1 ,820
Reduced shoots and 1 , 820
dry weight
Reference
Hosiaisluoma 1976
Academy of Natural
Sciences I960; Patrick
et al. 1968
Academy of Natural
Sciences I960; Patrick
et al. 1968
Academy of Natural
Sciences I960; Patrick
et al 1968
Stanley 1974
Stanley 1974
Teeter 1965
Teeter 1965
Teeter 1965
Concentration of chloride, not the chemical
21
-------
Table 5. Other Data on Effects of Chloride on Aquatic Organises
Species
Alga,
Chloral In pyrenoidoso
Protozoan ,
Poromeci urn tetrourel i o
Cladoceran (1st instar),
Oophnio moqno
Cladoceran (1st instar),
Dophni o moqno
Cladoceran (1st instar),
Dophnio moqna
Cladoceran ,
Dophnio moqno
Cladoceron ,
Dophni o moqno
Cladoceran,
Dophnio moqno
Cladoceron ,
Dophni o moqno
Cladoceron,
Dophni o moqno
Chemical
Sodium
chloride
Sodi um
chloride
Potassium
chlori de
Calci um
chloride
Sodium
chl or i de
Potass! um
chloride
Calci um
chloride
Magnesi um
chloride
Sod i um
chloride
Potass i um
chloride
Hardness
(•g/L as Concentration
CoCOJ Duration Effect Uq/D"
FRESHWATER SPECIES
24 hr Inhibited 301
growth
5 days 177. reduction in 350
eel 1 division
16 hr LC50 179
16 hr LC50 853
16 hr LC50 3,747
64 hr Incipient 207
i nhi bi t i on
64 hr Incipient 589
i nhi bi t i on
64 hr Incipient 555
i nhi bi t i on
64 hr Incipient 2,245
inhibition
45 21 days Reproductive 44
imp a i rnien t
Reference
Kalinkina. 1979; Kalintina
and Strogonov 1980
Kalinkina et al. 1978
Cronkite et al 1985
Anderson 1944
Anderson 1944
Anderson 1944
Anderson 1948
Anderson 1948
Anderson 1948
Anderson 1948
Biesinger and Christensen
1972
22
-------
Table 5. (continued)
Species
Clfldoceran,
Dophni o mognq
Clfldoceran ,
Dophni o moqno
Cladoceron,
Dophni o mogno
Caddisfly,
Hvdroot i 1 a onausta
Goldfish,
Corossi us qurotus
Shiners,
Notropis sp .
Fathead mi nnow (II irk) ,
Pitnephql es promel as
Channel catfish,
Ictol urus punctotus
Uosqui tof ish,
Gambus i a of f i ni s
Uosqui tof ish,
Gambus i a of finis
Uosqui tof ish ,
Gambus i a of f i n i s
Chemical
Cal ci urn
chloride
Magnesium
chloride
Sodi urn
chlori de
Potass i urn
chl oride
Sodi urn
chloride
Sodi urn
chloride
Sodi urn
chl ori de
Sod i urn
chl ori de
Potassium
chl ori de
Col c i urn
chloride
Uognes i um
chloride
Hardness
(»g/L as
CaCO,) Duration
y —
45 21 days
45 21 days
45 21 days
124 48 hr
24 hr
96 hr
5 days
24 hr
96 hr
412 24 hr
1 4 days
24 hr
96 hr
24 hr
96 hr
24 hr
96 hr
Effect
Reproduct i ve
impa i rment
Reproduct i ve
impa i rment
Reproduct i ve
impai rment
LC50
LC5Q (fed)
LC5Q (fed)
Threshold LC50
Reduced surv i val
LC50 (fed)
LC50 (fed)
Threshold LC50
LC50 (fed)
LC5Ud
LC50d
LC5Ud
Concentrat ion
(mq/L)"
206°
239C
1 ,062°
2,119
6,037
4,453
4,442
1,525
4,798
4,640
4 640
8,000
8.000
4,800
442
8,576
8,576
14,060
12,370
Reference
Biesinger and Christensen
19.72
Biesinger and Christensen
1972
Biesinger and Christensen
1972
Hamilton et al. 1975
Adelman and Smith 1976o,b
Adelman et al 1976
Van Horn et al. 1949
Adelman and Smith I976a b
Adelman et al. 1976
Reed and Evans 1981
Walle.n et a I . 1957
Wallen et al 1957
Wai len et al. 1957
23
-------
T«bU 5. (continued)
Species
Uosqui tof ish,
Combusio of f i nis
Bluegill ,
Leooinis mocrochi rus
lorgemouth boss (juvenile),
Micropterus sol mo ides
Cheoicol
Sodi um
chloride
Sodium
chloride
Sodi um
chl or ide
Hardness
(•9/L os
CoCO,)
412
412
Duration Effect
24 hr LC50d
96 hr
24 hr LC50 (fed)
14 doys
24 hr LCSO (fed)
14 days
Concentration
(•q/iV
II ,040
10,710
8,000
8,000
8,500
8,500
Reference
Wallen et al 1957
Reed and Cvans 1981
Reed and Evans 1981
Concentration of chloride, not the chemical.
This value was derived from the published graph.
Concentrations not measured in test solutions.
Turbidity = <25 to 320 mg/L
24
-------
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