United States
Environmental Protection
Agency
Office of Water
Office of Research and Development
Washington • DC 20460
EPA xxx/x-xx-xxx
XXXX1994
WATER
«yEPA Ambient Aquatic Life Water
Quality Criteria for:
HEXACHLOROBENZENE
(HCB)
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823R94005
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
HEXACHLOROBENZENE (FRESHWATER) :
(CAS Registry Number 118-74-1)
AUGUST 1994
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF WATER
OFFICE OF SCIENCE AND TECHNOLOGY •
HEALTH AND ECOLOGICAL CRITERIA DIVISION
WASHINGTON D.C.
OFFICE OF RESEARCH AND DEVELOPMENT
. ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
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NOTICES
This document has been reviewed by the Environmental Research
Laboratories, Duluth, MN and Narragansett, RI, Office of Research and
Development and the Health and Ecological Criteria Division, Office of Science
and Technology, 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.
11
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FOREWORD
Section 304(a)(1) 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) (1) 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 represent maximum acceptable pollutant
concentrations in ambient waters within that state that are enforced through
issuance of discharge limitations in NPDES permits. 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.
Alternatively, states may use different data and assumptions than EPA in
deriving numeric criteria that are scientifically defensible and protective of
designated uses. It is not until their adoption as part of state water
quality standards that criteria become regulatory. Guidelines to assist the
states and Indian tribes in modifying the criteria presented in this document
are contained in the Water Quality Standards Handbook (December 1983) . This
handbook and additional guidance on the development of water quality standards
and other water-related programs of this Agency have been developed by the
Office of Water.
This document, if finalized, would be guidance only. It would not
establish or affect legal rights or obligations. It would not establish a
binding norm and would not be finally determinative of the issues addressed.
Agency decisions in any particular situation will be made by applying the
Clean Water Act and EPA regulations on the basis of specific facts presented
and scientific information then available.
Tudor T. Davies
Director
Office of Science and Technology
111
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ACKNOWLEDGMENTS
Daniel J. Call
(Freshwater author)
University of Wisconsin-Superior
Superior, Wisconsin
Robert L. Spehar
(Co-author and document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
IV
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CONTENTS
Page
Notices •. ii
Foreword iii
Acknowledgments •.• iv
Tables ' vi
Introduction 1
Acute Toxicity to Aquatic Animals '•.... 3
Chronic Toxicity to Aquatic Animals '-. . 4
Toxicity to Aquatic Plants •• 5
Bioaccumulation ' 5
Other Data 9
Unused Data 10
Summary 12
National Criteria 13
References -....• 28
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TABLES
Page
1. Acute Toxicity of Hexachlorobenzene to Aquatic Animals 14
2. Chronic Toxicity of Hexachlorobenzene to Aquatic Animals 16
3. Ranked Genus Mean Acute Values with Species Acute-Chronic Ratios ... 17
4. Toxicity of Hexachlorobenzene to Aquatic Plants 19
5. Bioaccumulation of Hexachlorobenzene by Aquatic Organisms 20
6. Other Data on Effects of Hexachlorobenzene on Aquatic Organisms .... 25
VI
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Introduction
Hexachlorobenzene (HCB) has been detected in environmental samples from
around the world in recent years, and is recognized as a global-pollutant
(Ballschmiter and Zell 1980; Brevik 1981; Brunn and Manz 1982; Chovelon et al.
1984; Ciborowski and Corkum 1988; Galassi et al. 1981; Gobas and Mackay 1987;
Herve et al. 1988; Jan and Malnersic 1980; Johnson et al. 1974; Kaiser 1977;
Kuehl et al. 1983,1984; Laska et al.. 1976; Marquenie et al. 1986; Mhlanga and
Madziva 1990; Muncaster et al. 1989, 1990; Niemi et al. 1986; Niimi 1979; Ober
et al. 1987; Paasivirta et al. 1981; Sackmauerova et al. 1977; Schmitt et al.
1985; Skaftason and Johannesson 1982; Suns and Hitchin 1992; Swackhamer and
Kites 1988; Tarhanen et al. 1989; Tsui and McCart 1981; Veith et al. 1979b).
Contamination of Lake Ontario with HCB and other chlorobenzenes has occurred
since 1915, with larger amounts in recent decades (Oliver and Nicol 1982).
However, it should be noted that concentrations of HCB in Lake Ontario
sediment cores indicate a trend of deceased concentration near the surface of
the cores, an observation which correlates with decreased chlorobenzene
production since the mid-1960s (Eisenreich et al. 1989).
HCB is soluble in water to about 5 or 6 ^g/L (Abernethy et al. 1986;
Metcalf et al. 1973; Yalkowsky et al. 1979), and its concentrations in rivers
and lakes are generally reported in terms of ng/L (Niimi and Cho 1981). It
has an octanol/water partition coefficient (log P) of 6.18 (Neely et al.
1974) . The common occurrence of HCB in tissues of aquatic organisms can be
attributed to its high affinity for lipids and its persistence in the
environment. Metabolic transformation of HCB is considered to.be
insignificant (Gobas and Mackay 1987) . Fate information on HCB indicates that
photolysis, oxidation or hydrolysis are not important processes for this
chemical in aquatic systems (Callahan et al. 1979), although some photolysis
of HCB appears to occur in aquatic systems in increased amounts in the
presence of nitrogenous compounds (Hirsch and Hutzinger 1989) . Limited
information indicates that volatilization might be important in the absence of
other processes (Callahan et al. 1979).
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Connor (1984) estimated that HCB contributed little to increased risk
of cancer associated with consumption of freshwater fish from contaminated
water. Residues found in fish from the environment are usually reported in
low hg/g concentrations (e.g., Cleland et al. 1987, I988a,b; Johnson et al.
1987; Niimi and Oliver 1989; Peterson and Ray 1987; Schmitt et al. 1990; Suns
et al. 1991; Tarhanen et al. 1989), although some highly contaminated waters
have had fish with residues that were two to three orders of magnitude greater
(Koss et al. 1986; Kype-Hutter et al. 19"86; Luckas and Oehme 1990). HCB did
not induce the liver microsomal mixed-function oxidase (MFO) enzyme system in
rainbow trout (Lau and Addision 1981; Tyle et al. 1991), even though it has
been shown to be an inducer of cytochrome P-448 and P-450 in mammals (Linko et
al. 1986) .
HCB is used as a seed grain fungicide, a peptizing agent in the
production of nitroso and styrene rubber for tires, a wood preservative, a
porosity controller in the manufacture of graphite electrodes, a fluxing agent
in aluminum smelting, and in pyrotechnics manufacture (Courtney 1979;
Quinlivan et al. 1975/1977; U.S. EPA 1980a; Young et al. 1980). The degassing
of aluminum smelt with chlorine gas resulted in HCB production and river
contamination in one documented case (Vogelgesang et al. 1986). HCB is
largely derived as a byproduct of general chlorobenzene production (Eisenreich
et al. 1989) . HCB wastes also originate from the production of certain
pesticides (Cleveland et al. 1982), chlorinated solvents, vinyl chloride
monomers, and chlorine or sodium chlorate when produced electrolytically
(Quinlivan et al. 1975/1977). Some of the commercial formulations of HCB
contain toxic impurities, including pentachlorobenzene, polychlorinated
dibenzo-p-dioxins, and polychlorodibenzofurans (Villanueva et al. 1974).
HCB loading to North American watersheds has been shown to occur via
atmospheric precipitation and runoff (Johnson et al. 1987; Strachan 1985).
HCB is readily adsorbed by suspended sediments and algae (Autenreich and
DePinto 1991). Suspended sediments, especially near industrial discharges,
have been shown to be responsible for considerable transport of HCB in river
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systems (Lau et al. 1989). Elevated concentrations of HCB have been
identified in certain industrialized areas, such as the St. Clair River near
Sarnia, Ontario (.Chan et al. 1986; Kauss and Hamdy 1985; King and Sherbin
1986; Oliver and Kaiser 1986). Annual loadings from municipal sources were
insignificant relative to industrial loadings (Marsalek 1986).
A comprehension 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 1985) is necessary in order to understand
the following text,, tables, and calculations. Results of such intermediate
calculations as recalculated LCSOs and Species Mean Acute Values are given to
four significant figures to prevent round-off error in subsequent
calculations, not to reflect the precision of the values. The criteria
presented herein supersede previous national aquatic life water quality
criteria for HCB (U.S. EPA 1980) because these new criteria were derived using
improved procedures and additional information. The latest comprehensive
literature search for information for this document was conducted in April,
1993; some more recent information was included. Data in the files of the
U.S. EPA's Office of Pesticide Programs concerning the effects of
hexachlorobenzene on aquatic organisms and their uses have been evaluated for
possible use in the derivation of aquatic life criteria.
This document does not contain information concerning the effects of
HCB on saltwater species.
Acute Toxicitv to Aquatic Animals
Data that could potentially be used, according to the Guidelines, in
the derivation of a freshwater Final Acute Value for HCB are presented in
Table l. Twenty-six acute tests were conducted with fourteen genera and
sixteen species. The only experimentally determined acute values were at
concentrations that are at least 1,000 times the water solubility limit. In
those tests where concentrations of HCB approached the solubility limit,
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mortalities were insufficient to calculate definitive acute values .
'Therefore, the LC50 or EC50 was reported as a "greater than" value.
Some acute exposures were continued for longer than 96 hr with no
resultant mortalities. For .example, survival of adult crayfish, Procambarus
clarki, was unaffected over a period of 20 days at a mean HCB concentration of
27.3 ng/L, and the largemouth bass, Micropterus salmoides. was unaffected over
10 days at 25.8./ig/L (Laseter et al . 1976; Laska et al . 1978) . Because so few
quantitative Species Mean Acute Values are available for freshwater species,
the procedures described in the Guidelines cannot be used to calculate a Final
Acute Value. However, the data strongly suggest that acute toxicity does not
occur at concentrations below the water solubility limit for HCB of 6
Chronic Toxicitv to Aquatic Animals
The available data- that are useable according to the Guidelines
concerning the chronic toxicity of HCB are presented in Table 2. Six chronic
tests have been conducted with five species. The oligochaete, Lumbriculus
variegatus , was exposed to a mean concentration of 4.7 ^g/L of HCB for 49 days
with no significant adverse effects upon survival, growth or asexual
reproduction (Nebeker et al . 1989). In a 7-day life-cycle test with the
i
cladoceran, Ceriodaphnia dubia. HCB did not cause any measurable effect upon
survival or reproduction at concentrations as high as 7.0 MSF/L (Spehar 1986).
The amphipod, Hvalella azteca. was unaffected in its survival and reproduction
in two tests at mean HCB exposure levels of 4.5 and 3.8 \iq'/l> for 30 days
(Nebeker et al . 1989). :
Rainbow trout, Oncorhvnchus mvkiss, were exposed to HCB in a 90 -day
early life-stage test (Spehar 1986) . No adverse effects on hatching,
survival, or growth were observed at the highest tested concentration of 3.68
ng/L (Table 2) . Similarly, fathead minnows, Pimephales promelas, were not
affected at exposures up to 4.8 M9/L in a 32-day early life-stage test (Ahmad
et al. 1984; Carlson and Kosian 1987). Survival at hatch, survival at 32
days, and wet weight were the same at all exposure concentrations as in the
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control.
Because chronic values are not available for any species, neither a
Final Chronic Value nor a Final Acute-Chronic Ratio can be calculated for HCB.
Toxicitv to Aquatic Plants
Data are available on the toxicity of HCB to two species of aquatic
plants (Table 4). Geyer et al. (1985) reported that the green alga,
Scenedesmus subspicatus. was not affected in 4 days by HCB at a concentration
of 10 jjg/L, Calamari et al. (1983) observed that a concentration above water
solubility (27 M9/D caused a slight growth inhibition (12 percent) in a 4-day
exposure of Selenastrum capricornutum. Based on these available data, a
Final Plant Value, as defined in the Guidelines, cannot be obtained.
Bioaccumulation ;
The available data that are useable according to the Guidelines
concerning HCB accumulation are shown in Table 5. HCB exposure of the
oligochaete, Lumbriculus variegatus. at concentrations between 0.8 and 5.8
/Kj/L for 28-49 days resulted in bioconcentration factors (BCFs) ranging from
4,600 to 106,840 (Nebeker et al. 1989, 1990; Schuytema et al'. 1988). Oliver
(1987) exposed mixed oligochaetes consisting of mainly Tubifex tubifex and
Limnbdrilus hoffmeisteri to 0.250 M9/L HCB f°r 79 days. With a whole body
lipid content of 1.0 percent, the BCF (both normalized and not lipid-
normalized) was 3,120. \
Nebeker et al. (1989) showed, that whole body BCFs for amphipods,
Gammarus lacustris. exposed to HCB concentrations of 0.4 to 3.3 M9/L ranged
from 18,750 to 33,000 in 28-day exposures. Lipid-normalized BCFs based on a
lipid concentration of 5.3 percent ranged from 3,538 to 6,226.- The BCF (not
lipid-normalized) for this same species exposed to 4.5 M9/L f.or 30 days in
another study was 41,200 (Schuytema et al. 1990). The amphipod, Hvalella
azteca. was exposed to HCB for 30 days in 10 separate tests at concentrations
between 0.3 and 4.5 jxg/L (Nebeker et al. 1989). Whole body lipid content was
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2.3 percent. Lipid-normal!zed BCFs were between 9,617 and 32,609. Three
exposures of Hvalella azteca to HCB for 28 days at 1.1 to 5.7 /ig/L yielded
whole body BCFs that were not lipid-normalized between 13,900 and 23,000
(Schuytema et al. 1988, 1990). Oliver and Niimi (1983) reported that'
equilibration had not yet occurred after a 119-day exposure of rainbow trout
to HCB at a concentration of 0.00032 ng/L, at which time the BCF was 12,000
{1,412, lipid-normalized). An exposure to 0.008 fJ.g/L resulted in a BCF of
20,000 (2,353, lipid-normalized) with the trout. Veith et al. (1979a)
determined the BCF for rainbow trout to be 5,500 after a 32-day exposure
period. Common carp, Cyprinus carpio, exposed to 0.366 ng/L of HCB for 21
days with whole body lipid content ranging between 1.5 and 6.5 percent had a
lipid-normalized BCF of approximately 3,020 (Tadokoro and Tomita 1987) .
HCB residues in fathead minnows continually increased in 28-day tests
to concentrations that were from 19,635 to 39,000 times greater than the
concentrations of HCB in water (U.S. EPA 1980b;. Kosian et al. 1981). Percent
lipid determinations for this species were different in these studies and
yielded lipid-normalized BCFs of 10,908 and 3,361 to 4,577, respectively. In
ciddition, HCB was found to be in equilibrium with the water concentrations in
one study (U.S. EPA I980b) but not in the other (Kosian et al. 1981) after 28
days. Following a rapid uptake during the first week of exposure, HCB
residues in fathead minnows gradually increased through 115 days (Veith et al.
1979a) . HCB residues in the minnows were from 16,200 to 45,700 times greater
than concentrations in water following exposures of 32 to 115 days. Lipid-
normalized BCFs ranged from 2,132 to 6,013. Carlson and Kosian (1987)
obtained similar BCFs that ranged from 4,568 to 7,026 (lipid-normalized) for
fathead minnows exposed for 32 days. Fathead minnows exposed to 1.3 and 2.0
M9/L of HCB for 28 days had BCFs (not lipid-normalized) of 29,600 'and 50,600
(Schuytema et al. 1988). Other BCFs for fathead minnows exposed :tp 0.3 and
3.8 /Kj/L for 28 days in five separate exposures ranged from 12,240 to 21,140
(Nebeker et al. 1989). Lipid-normalized BCFs for these fish (6.9 percent
lipid) were between 1,774 and 3,064. Bioconcentration equilibrium was
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reached in this study after the 28-day exposure period which is in contrast to
the results shown by Kosian et al. (1981). Higher BCFs (not lipid-normalized)
of 95,400 and 93,800 were reported for fathead minnows by Schuytema et al.
(1990) .
In a test with a mixture .of chlorinated benzenes, an apparent steady-
state BCF of 15,660 was obtained for HCB with the guppy, Poecilia reticulata
within 7 days (Konemann and Van Leeuwen 1980) . One-year-old male guppies
exposed to 1.96 ng/L of HCB for 42 days had a non-normalized BCF of 19,500 and
a lipid-normalized BCF of 6,500 (Opperhuizen and Stokkel 1988). Green
sunfish, Lepomis cvanellus. bioconcentrated HCB to a level that was 21,900
times the water concentration (Veith et al. 1979a) .
Other studies showed that coho salmon (Oncorhvnchus kisutch) and green
sunfish accumulated HCB when fed contaminated food (Leatherland and Sonstegard
1982; Sanborn et al. 1977). Crayfish (Procambarus clarki) exposed at a
contaminated field site to a mean HCB concentration of 74.9 M9/L had a mean
whole-body concentration factor of 1,464 (Laseter et al. 1976). Fox et al.
(1983) found a direct correlation between HCB concentrations in surficial
sediments of Lake Ontario and HCB concentrations in oligochaetes that inhabit
the sediments. They also reported that HCB accumulation was greater at the
higher trophic levels. One study showed that uptake via food might be more
important than direct uptake from water for top carnivores, particularly in
waters where HCB concentrations are very low (Niimi and Cho 1980). However,
other studies indicate that the water might be a more important source for HCB
accumulation than the food (Callahan et al. 1979). Studies have indicated
that HCB and other lipophilic, persistent chlorinated organics are passed from
parent to offspring via the yolk and oil of the fish egg (Niimi 1983; Westin
et al. 1985) . Survival and growth of larvae might be affected by this route
of uptake in some fish species.
Several investigators have studied the elimination of HCB from a
variety of aquatic species. Norheim and Roald (1985) determined the half-life
of HCB in rainbow trout that had been injected intraperitoneally and
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maintained at a water temperature of 7°C to be 81, 146, and 139 days in liver,
fat, and muscle, respectively. Niimi and Cho (1981) reported the biological
half-life of HCB to be 224 to 770 days in rainbow trout fed HCB and maintained
at a water temperature of 15°C. In a subsequent study (Niimi and Palazzo
1985) , HCB-fed rainbow trout held at 12 and 18°C had HCB half-lives of 173 and
198 days, respectively, whereas fish held at 4°C did not eliminate HCB. In
contrast, studies by U.S: EPA (1980b) and Nebeker et al. (1989) show that HCB
elimination is rapid, approaching zero in less than 30 days, once fish are
placed in clean water. 'Crayfish that were exposed to 74.9 ^g/L for 10 days
under field conditions eliminated about 15% of the HCB after three days in
clean water. Males eliminated 47% and females 64% after 25 days (Laseter et
al. 1976) . These authors also found that largemouth bass eliminated from 73.1
to 91.4% of the whole body HCB residue during 13 days in uncontaminated water.
McKim e't al. (1985) studied the uptake efficiency of HCB and 13 other
chemicals by rainbow trout gills. HCB was among the chemicals most
efficiently removed from water by gills. However, it did not appear to be
removed much more efficiently than several chlorophenols, which by comparison
to HCB, have a reduced capacity for bioaccumulation.
.•
The high accumulation levels of HCB in aquatic organisms .can be
explained by its slow ra;te of conversion to water soluble metabolites,
combined with an efficient uptake from water due to its high n-octanol water
partition coefficient of 6.18. However, experimentally determined rates of
depuration appear to be substantially more rapid than those for other
persistent chemicals, such as DDT. Callahan et al. (1979), in a review of the
water-related environmental fate of HCB, suggest that biomagnification of HCB
in aquatic systems probably does not occur. ' >
No U.S. FDA action level or other maximum acceptable concentration in
tissue, as defined in the-Guidelines, is available for HCB. Therefore, a
Final Residue Value cannot be calculated. :
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Other Data :
Additional data on the lethal and sublethal effects'Of HCB on
freshwater species are presented in Table 6. A green alga, Ankistrodesmus
falcatus. was unaffected in a 4-hr exposure to 3 pig/L (Wong et al. 1984) .
Chlorophyll was slightly reduced (<10 percent) in the green alga, Chlorella
pyrenoidosa, following a 46 hr exposure to 1 ng/L of HCB, but growth was
stimulated, as measured by chlorophyll production after 90 days (Geike and
Parasher 1976). Reduced growth was shown in this species when they were
exposed to 10,000 ^g/L (Parasher et al. 1978), a concentration much higher
than the water solubility limit for HCB. The green alga Oedoaonium cardiacum
bioconcentrated HCB 623 times above the concentration in water after 7 days
(Laseter et al. 1976). No effect was observed in the protozoan, Colpidium
campvlurn, exposed to HCB at 10,000 M9/L for 43 hr (Dive et al. 1980), and .
Yoshioka et al. (1985) found that the 24-hr EC50-for the protozoan,
Tetrahvmena pyriformis, was greater than 50,000 pig/L. However, Figueroa and
Simmons (1991) showed that a concentration of 2.0 M9/L caused a'50 percent
reduction in the DNA content of the diatom, Cvclotella meneghiana. following a
48 hr exposure. The authors discussed the use of the DNA measurement as a
quantitative parameter for determining the toxicity effects of chlorobenzenes
on algae.
Daphnia magna were not adversely affected after 24 to 28.3 hours at
concentrations, that exceeded the solubility of HCB in water (Calamari et al.
1983; Sugatt et al. 1984). However, a concentration of IS./xg/L caused a 50
percent inhibition in reproduction (EC50) in daphnids after 14 days (Calamari
et al. 1983) . Another cladoceran species, Moina macrocopa, was not adversely
affected (i.e., mortality was <50 percent) at water solubility (Yoshioka et
al. 1986). Shucked mussels (Elliptic complanata) bioconcentrated HCB 3,650
times after 11 days of exposure (Russell and Gobas 1989). Nebeker et al.
(1989) observed that a concentration of 3.3 fig/L caused significant mortality
(40 percent) to the amphipod, Gammarus lacustris. after 28 days, although this
mortality was not much greater than that observed in other HCB concentrations.
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The authors felt that the mortalities were probably not due to HCB because all
surviving animals appeared healthy and normal. Crayfish, Procambarus clarki,
exposed to higher concentrations ranging from 27.3 to-36.1 ^g/L appeared to
accumulate much less HCB than amphipods. BCFs (not lipid-normalized) for this
species were between 75 and 149 (Laseter et al. 1976).
Due to insufficient deaths, LCSOs could not be determined for rainbow
trout exposed to 27 jig/L for 24 hr (Calamari et al. 1983), for fathead minnows
exposed to 3.8 Mg/L for 28 days (Nebeker et al. 1989), or for guppies exposed
to >320 ng/L for 14 days (Konemann 1979,1981). However, 5 ng/L caused
hepatopancreas damage in crayfish and 3.5 to 25.8 ^tg/L caused liver, kidney
and gallbladder damage in largemouth bass after 10 days of exposure (Laseter
et al. 1976). Studies with largemouth bass showed that BCFs (not lipid-
normalized) ranged from 18,200 to 44,400 after 15 days of exposure (Laseter et
al. 1976) .
Unused Data
Some data on the effects of HCB on aquatic organisms and their uses
were not used because the studies were conducted with specie's that are not
resident in North America (e.g., El Nabawi et al. 1987; Hattori et al. 1984;
Huang et al. 1986; Kammann et al. 1990; Kasokat et al. 1989; Sugiura et al.
1984; Venant and Cumont 1987). Data were not used when HCB was a component of
a mixture or wettable powder (e.g., Gjessing et al. 1984; Mayer and Ellersieck
1986; Poels et al. 1980). Anliker et al. (1988), Chiou (1985), Chiou et al.
(1977), Connell and Schuurmann (1988), Davies and Dobbs (1984), Glass et al.
(1977), Gobas and Mackay (1987), Gombar (1987), Hawker and Connell (1986,
1988), Kaiser et al. (1984), Klein et al. (1984), Koch (1982a',b) , Matsuo
(1980,1981), Oliver (1984a), Sabljic (1987), Sabljic and Protic (1982), and
Schuurmann and Klein (1988) compiled data from other sources.: Johnson and
Finley (1980) was not used because the data from this publication were re-
ctnalyzed and subsequently published in another article. Studies were not used
if the exposure duration was not specified (e.g., Blum and Speece 1991).
10
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Tests were not used when only physiological effects or enzyme activity
were measured (e.g., Gluth and Hanke 1984; Hanke et al. 1983; Law and Addison
1981). Schmidt-Bleek et' al. (1982) did not adequately describe the methods
used for the toxicity tests. Toxicity data were not used when the test was
conducted in distilled water (e.g., Abernethy et al. 1986; Bobra et al. 1985).
Studies of HCB residues in aquatic organisms were not used when there
were insufficient tissue residue data or accompanying data on HCB
concentrations in the water to determine" a bioconcentration or bioaccumulation
factor (e.g., Atuma and Eigbe 1985; Clark et al. 1984; DeVault 1985; Evans et
al. 1982; Giesy et al. 1986; Glass 1975; Heida 1983; Jaffe and Hites 1986;
Kaiser 1982; Kaiser and Valdmanis 1978; Keck and Raffenot 1979; Kuehl et al.
1980,1981; Niimi 1979; Norstrom et al. 1978; Paasivirta et al.1983a,b;
Pennington et al. 1982; Schmitt et al. 1985; Schuler et al. 1985; Swain 1978;
Veith et al. 1977,1981; Wiemeyer et al. 1978; Zitko 1971). Results of studies
in which HCB was administered by gavage, injection, or in the food were not
used (e.g., Clark and Mackay 1991; Devault et al. 1988; Hall et al.. 1987;
Holmes 1988; Ingebrigtsen and Skaare 1983; Niimi and Oliver 1988; Safe et al.
1976; Saiki and Schmitt 1986). ' .
Studies using radiolabeled HCB in which only radioactivity was measured
in the water or in exposed organisms were not used (e.g., Clark and Mackay
1991; Freitag 1987; Freitag et al. 1982,1984,1985; Geyer et al;. 1981,1984;
Mailhot 1987; Niimi and Oliver 1988; Schauerte et al. 1982). Results of
laboratory bioaccumulation tests were not used when the test was not flow-
through or renewal (e.g., Belluck and Felsot 1981; Korte et al. 1978; Lu and
Metcalf 1975; Metcalf et al. 1973; Zitko and Hutzinger 1976), or when the
concentration of HCB in the test solution was not adequately measured (e.g.,
Isensee 1976; Isensee et al. 1976; Knezovich and Harrison 1988). Studies of
the bioaccumulation of HCB by organisms inhabiting contaminated sediment were
not used (Knezovich and Harrison 1988; Oliver 1984b; Schrap and Opperhuizen
1989) . Bioconcentration data were not used when the duration of exposure was
not specified (e.g., Neely et al. 1974), or if the exposure duration was short
11
-------
and if evidence for Che establishment of an equilibrium between water and fish
was not presented (e.g., Opperhuizen et al. 1988).
Studies on the dynamics and transport of HCB at the sediment-water
interface were not used (Baker et al. 1985; Gerould and Gloss 1986; Karickhoff
and Morris 1985). Studies were not used if HCB residues in environmental
samples were only reported as "less than" values or were below analytical
detection limits (e.g., DeVault et al. 1988; Hall et al. 1987; Holmes 1988;
Saiki and Schmitt 1986) .
Summary
Data on the acute toxicity of HCB are available for sixteen species.of
freshwater animals. In nearly all tests, the highest concentrations were not
acutely toxic and only greater-than ECSOs or LCSOs could be reported for this
document. The definitive LCSOs that could be calculated ranged from 7,000 to
13,500 M9/L, which are approximately 1,000 to 2,250 times the water solubility
limit. Because not enough definitive acute values exist to meet the minimum
data base requirements according to the Guidelines, a Final Acute Value for
HCB and freshwater organisms cannot be calculated.
Chronic toxicity tests with HCB have been conducted using five species
of freshwater animals. No adverse effects were observed with any of the
species at the highest tested concentrations, which were near water
solubility. Therefore, neither a Final Chronic Value nor a Final Acute-
Chronic Ratio for this chemical and freshwater organisms can be calculated.
Tests with HCB and two species of algae were conducted and only slight
adverse effects were observed at concentrations above water solubility. No
Final Plant Value, as defined in the Guidelines, can be calculated for HCB and
freshwater plants.
Bioaccumulation of HCB has been determined with a variety of freshwater
species. Invertebrate BCFs that are not lipid-normalized ranged from 3,120 to
106,840 compared to 5,500 to 95,400 for fish. Hexachlorobenzene accumulates
to high levels in freshwater organisms due to its high n-octanol water
12
-------
partition coefficient combined with its slow rate of conversion to water
soluble metabolites, but it appears to depurate more rapidly than other
persistent chemicals indicating that biomagnification in aquatic systems
probably does not occur. Because there is no FDA action limit or an available
maximum dietary intake value derived from a chronic feeding study or a long-
term field study with wildlife, a Final Residue Value for HCB cannot be
calculated.
Other data from a variety of tests showed, in general, that HCB did not
adversely affect the survival, growth and reproduction of the tested species
at or below the water solubility limit of 6 ^g/L. Although HCB caused some
sublethal effects such as DNA reduction and histological damage at
concentrations below this solubility limit, the ecological implications of
theses effects are unknown, and water quality criteria based upon these
endpoints cannot be derived at this time.
Based on the above test results, not enough data are available
according to the Guidelines to calculate a Final Acute Value, Final Chronic
Value, Final Plant Value or a Final Residue Value for HCB.
National Criteria • •
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" do not allow for the derivation of national criteria for
hexachlorobenzene (HCB) 'based on the available test information. The
available data indicate .that HCB does not cause significant adverse effects on
the survival, growth and reproduction of freshwater aquatic life at or below
the water solubility limit of approximately 6
13
-------
Table 1. Acute Toxicity of Hexachlorobenzene to Aquatic Animals
Species
Hydra (adult).
Hydra sp.
Oligochaete,
Lumbficulus varieaatus
Snail (adult),
Aplexa hypnomm
Cladoceran,
Cefiodaphnia dubia
Amphipod,
Gammarus lacustris
Amphipod (adult),
Gammarus pseudolimnaeus
Amphipod,
Hyalella azteca
Amphipod,
Hvalella azteca
Crayfish (adult),
Procambarus clarki
Crayfish (juvenile),
Procambarus sp.
Stonefly (nymph),
Pteronarcys sp.
Midge (3rd-4th instar),
Tanvtarsus dissimilis
Rainbow trout (0.5 g),
Oncorhvnchus mvkiss
Rainbow trout (juvenile),
Oncorhvnchus mykiss
Rainbow trout (juvenile).
Method*
S.M
F.M
S.M
S.M
F,M
S.M
F.M
F.M
F.M
S.M
S.M
S.M~
F.M
F.M
F.M
Hardness
{rrsg/L as
Chemical CaCOJ
FRESHWATER SPECIES
97% 49.7
2535
97% 49.5
45
25-35
97% 49.5
25-35
25-35
-
-
97% 47.4
97% -40.7
97% 44.3
97% 44.3
45 46
LC50
or EC50
(J/Q./I-1
>65.9
>4.7
>77.6
>7.0
>3.3
>77.6
>3.8
>4.5
>27.3
>5.2
>69.7
>58.V
>80.9
>80.9
>3.76
Species mean
Acute value
if/g/U
>65.9
>4.7
>77.6
>7.0
>3.3
>77.6
-
>4.5
-
>27.3
>69.7
>58..V
-
>80.9
Reference
Sabourin et al. 1986
Nebeker et al. 1989
Sabourin et al. 1986
Spehar 1986
Nebeker et al. 1989
Sabourin et al. 1986
Nebeker et al. 1989
Nebeker et al. 1989
Laseter et al. 1976;
Laskaet al. 1978
Laseter et al. 1978;
Laska et al. 1978
Sabourin et al. 1986
Call et al. 1983.
Ahmad et al. 1984;
Call et al. 1983
Ahmad et al. 1984;
Call et al. 1983
Spehar 1986
Oncorhvnchus mvkiss
-------
Table 1. (continued)
Species
Fathead minnow (30 days).
Pimephales promelas
Fathead minnow (0.7g),
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Channel catfish (0.8g),
Ictalurus punctatus
Channel catfish 11. 3g),
Ictalurus punctatus
Channel catfish (sac fry).
Ictalurus punctatus
Bluegill (1.5g),
Lepomis macrochirus
Bluegill (1g),
Lepomis macrochirus
Bluegill (1.6g),
Lepomis macrochirus
Largemouth bass.
Micropterus salmoides
Largemouth bass (0.5g),
Micropterus salmoides
Method'
F,M
S.U
F,M
S.U
S,U
S.U
F.M
S,U
F,U
F,M
S.U
Hardness
tmg/L as
Chemical CaCO,)
97% 45
96% 44
2535
96% 44
96% 40
96% 272
97% 45.4
96% 272
96% 272
-
96% 272
LC50
or EC50
U/Q./LI
>7
> 10,000
>3,8
13,500
• > 100,000°
7,000
>78.4
1 2,000
> 1 ,000
>25.8
12,000
Species mean
Acute value
Urti/Li Reference
Veith et al. 1983a,b;
Ahmad et al. 1984;
Carlson and Kosian 1987
Mayer and Ellersieck 1986
> 10,000 Nebeker et al. 1989
Mayer and Ellersieck 1986
Mayer and Ellersieck 1986
9,720 Mayer and Ellersieck 1986
Cadet al. 1983
Mayer and Ellersieck 1986
12.000 Mayer and Ellersieck 1986
Laseter et al. 1976;
Laskaet al. 1978
12,000 Mayer and Ellersieck 1986
• S = static; R = renewal; F = flow-through; M = measured; U = unmeasured.
° Not used in calculation of Species Mean Acute Value.
-------
Table 2. Chronic Toxicity of Hexachlorobenzene to Aquatic Animals
Species
Oligochaete,
Lumbrlculus variegatus
Amphipod.
Hvalella azteca
Amphipod,
Hvalella azteca
Cladoceran,
Ceriodaphnia dubia
Rainbow trout,
Oncorhvnchus mykiss
Fathead minnow,
Pimephales promelas
Hardness
(mg/L as
Test' Chemical CaCOJ
FRESHWATER
LC - 25-35
LC - 25-35
LC - 25 35
LC - 45
ELS - 43-47
ELS 97% 44-46
Chronic
Limits
Ua/L)"
SPECIES
>4.7C
>4.5C
>3.8e
>7.0e
>3.68C
>4.8C
Chronic
Value
uva/Ll
>4.7
>4.5
>3.8
>7.0
>3.68
>4.8
Reference
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Spehar 1986
Spehar 1 986
Ahmad et al. 1984;
Carlson and Kosian 1987
' LC = life-cycle or partial life-cycle; ELS = early life-stage.
° Measured concentrations of hexachlorobenzene.
' Highest tested concentration; no tested concentration caused an unacceptable effect.
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
Rank*
14
13
12
11
10
9
8
7
6
5
4
3
Genus Mean
Acute Value
0/a/LI
12,000
12.000
> 10,000
9,720
>80.9
>77.6
>77.6
>69.7
>65.9
>58.1
>27.3
>7.0
Species
FRESHWATER !
Largemouth bass.
Micropterus salmoides
Bluegill,
Lepomis macrochirus
Fathead minnow,
Pimephales promelas
Channel catfish.
Iclalurus punctatus
Rainbow trout.
Oncorhynchus mykiss
Snail,
Aplexa hypnorum
Amphipod,
Gammarus pseudolimnaeus
Amphipod,
Gammarus Lacustris
Stonefly.
Pteronarcvs sp.
Hydra (adult).
Hydra sp.
Midge,
Tanvtarsus dissimilis
Crayfish,
Procambarus clarki
Cladoceran.
Species Mean
Acute Value
12,000
12,000
>10,000
9,720
>80.9
>77.6
>77.6
>3.3
>69.7
>65.9
>58.1
>27.3
>7.0
Species Mean
Acute-Chronic
Ratio'
Ceriodaphnia dubia
-------
Table 3. (Continued)
Rank*
2
1
Genus Mean
Acute Value
(JJQ/L)
>4.7
>4.5
Species
Oligochaete,
Lumbriculus varieqatus
Amphipod,
Hyalelja azteca
Species Mean
Acute Value
>4.7
>4.5
Species Mean
Acute-Chronic
Ratio'
C
_c
* Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
° From Table 1.
•' Acute-chronic ratio was not calculated, as values ot both numerator and denominator were "greater than" values.
Fresh water
Final Acute Value = Cannot be calculated (see text)
Criterion Maximum Concentration = Cann. , be calculated
Final Acute-Chronic Ratio = Cannot be calculated (see text)
Final Chronic Value = Cannot be calculated
-------
Table 4. Toxicity of Hexachlorobenzene to Aquatic Plants
Species
Hardness
(mg/L as Duration
Chemical CaCCs) (days)
Effect
Concentration
Reference
Alga,
Scenedesmus subspicatus
Alga.
Selenastrum capricornutum
98.0
FRESHWATER SPECIES
4 EC50
4 EC12
-27
Geyer et al. 1985
Calamari et al. 1983
Analytical grade.
vo
-------
Table S. Bioaccumulation of Hexachlorobenzene by Aquatic Organisms
Species
Oligochaete,
ILumbficulus vanegalus)
Oligochaete,
(Lumbficulus variegatus)
Oligochaete,
(Lumbficulus variegatusl
Oligochaete,
(Lumbficulus variegatus)
Mixed oligochaetes,
(Tubifex tubitex and
Limnodrilus hoffmeisteri)
KJ
Amphipod,
(Gammarus lacustris)
Amphipod,
(Gammafus lacustris)
Amphipod,
(Gammarus lacustfis)
Amphipod,
(Gammarus lacustris)
Amphipod,
(Gammarus lacustris)
Amphipod,
(Gammarus lacustris) . ••„-•.'..
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Concentration in
Chemical Water Uro/LI'
0.8
2.2
1.0
1.9
4.7
5.8
0.250
0.4
0.8
1.0
1.8
3.3
4.5 .
0.3
0.4
Duration
(days)
28
44
49
49
49
28
79
28
28
28
28
28
30
30
30
Tissue
FRESHWATER SPECIES
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body . .
Whole body
Whole body
Percent
Lipids
1.8
1.8
1.8
1.0
5.3
5.3
5.3
5.3
5.3
-
2.3
2.3
BCFor
BAF"
4,600
13,200
50.000"
106,840"
47.450"
25,100
3.120
20,000
18,750
33,000
29,440
23,940
. , 41,200 .
28,330
35,000
Normalized
BCF or BAF<
-
27,800
59,400
26,400
-
3,120
3.774
3,538
6.226
5,555
4,517
•
12,317
15.217
Relerence
Schuytema et al. 1988
Schuytema et al. 1988
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Schuytema et al. 1990
Oliver 1987
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
...Schuytema et al. 1990
Nebeker et al. 1989
Nebeker et al. 1989
-------
Table 5. (Continued)
Species Chemical
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod.
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Rainbow trout (juvenile),
Oncorhvnchus mvkiss
Rainbow trout (juvenile).
Oncorhvnchus mvkiss
Rainbow trout (fingerling).
Oncorhvnchus mvkiss
Concentration in Duration
Water U/g/L)1 (days)
0.5 30
0.7 30
0.7 30
OB 3O
.O »JV/
2.0 30
3.3 30
3.8 30
4.5 30
1.1 28
2.5 28
5.7 28
0.00032 119 -
0.008 105
32
Percent
Tissue Lipids
Whole body 2.3
Whole body 2.3
Whole body 2.3
Whole body 2.3
Whole body 2.3
Whole body 2.3
Whole body 2.3
Whole body 2.3
Whole body
Whole body
Whole body
Whole body 8.5 ...
less digestive
tract
Whole body 8.5
less digestive
tract
Whole body
BCF or
BAF"
28.000
40,000
38,570
75.000
24.500
22.120
26,580
38.220
13,900
23.000
20.700
. .12,000V
20,000*
5,500
Normalized
BCF or BAFC
12,174
17,391
16.770
32,609
10,652
9.617
11,557
16,617
-
1,412
2,353
,
Reference
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Schuytema et al. 1988
Schuytema et al. 1988
Schuytema et al. 1 990
Oliver and Niimi 1 983
Oliver and Niimi 1983
Veith et al. 1979a
-------
Table 5. (Continued)
Concentration in Duration
Chemical Water uvg/U* (days) Tissue
Percent BCF or
BAF"
Normalized
BCF or BAFC Reference
Common carp (20-30g),
Cyprinus carpio
Fathead minnow (0.73g),
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (newly
hatched fry),
Pimephales promelas
Fathead minnow (30 days),
Pimephales promelas
Fathead minnow (90 days),
Pimephales promelas
Fathead minnow (adult),
Pimephales promelas
Fathead minnow (adult),
Pimephales promelas
Fathead minnow (adult),
Pimephales promelas
Fathead minnow (juvenile), 97%
Pimephales promelas
Fathead minnow (juvenile), 97%
0.366
0.18
0.17
0.16
0.15
0.18
-5
-5
-5
-5
-5
-5
4-4.8
0.3
21
28
28
28
28
28
-115
-40
115
-32
-115
-32
32
32
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
- -^
-1.5-6.5'
1.8
9.22
9.52
8.52
9.27
7.6"
7.6"
7.6"
7.6"
7.6"
7.6"
-
3.8
-
19.635
33,000'
32,000"
39,000'
37.000'
45,700
18,200
1 7,800
18,500
16,600
16,200
20,200-
23,400
26,700
3,020'
10,908
3.579
3,361
4,577
3,991
6,013
2,395
2,342
2,434
2.184
2,132
' -
7,026
Tadokoro and Tom
U.S. EPA 1980b
Kosian et al. 1981
Kosian et al. 1981
Kosian et al. 1981
Kosian et al. 1981
Veith et al. 1979a
Veith et al. 1979a
Veith et al. 1979a
Veith et al. 1979a
Veith et al. 1979a
Veith et al. 1979a
Ahmad et al. 1984
Carlson and Kosian
Pimephales promelas
-------
Table 5. (Continued)
pecies
Concentration in Duration
Chemical Water U/q/LI' (days) Tissue
Percent BCF or
lipids BAF"
Normalized
BCF or BAFC Reterence
Fathead minnow (juvenile), 97%
Pimephales promelas
Fathead minnow (juvenile), 97%
Pimephales promelas
Fathead minnow (juvenile), 97%
Pimephales promelas
Fathead minnow (44 mg),
Pimephales promelas '
Fathead minnow (150 mg),
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow
(Pimephales promelas)
Fathead minnow
(Pimephales promelas)
Guppy (1 yr old
-------
' Measured concentration of hexachlorobenzene.
" Bioconcentration factors (BCFs) and bioaccumulation factors (BAFs) are based on measured concentrations of hexachlorobenzene in water and tissue.
c When possible, the factors were normalized to 1 % lipids by dividing the BCFs and BAFs by the percent lipids.
" A quartz sand substrate was provided for the test organisms.
• The hexachlorobenzene concentration had not equilibrated between water and fish, and the value presented is based upon residues in the fish tor the exposure period indicated.
1 The study was conducted with fish at several lipid content levels, and a single overall lipid-normalized BCF was reported.
9 The hexachlorobenzene concentration had not equilibrated between water and fish at 28 days, and the value presented is based upon residues in the fish on day 28.
" Reported by Veith (1980).
-------
Table 6. Other Data on Effects of Hexachlorobenzene on Aquatic Organisms
Species
Hardness
(mg/L as
Chemical CaCOJ
Result
Duration
Effect
FRESHWATER SPECIES
Green alga.
Ankistrodesmus falcatus
Green alga,
Chlorella pyrenoidosa
Green alga,
Chlorella pyrenoidosa
Green alga,
Chlorella pyrenoidosa
Green alga,
Oedogonium cadiacum
Diatom,
Cyclotella meneghiniana
Protozoan.
Colpidium campylum
Protozoan,
Tetrahvmena pyriformis
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran (<24 hr),
Daphnia manna
Cladoceran ( - 5 days),
Moina macrocopa
Mussel,
Elliptic complanate
Amphipod,
-
-
-
-
-
Reagent
grade
-
Analytical
grade
Analytical
grade
Analytical • . -
grade
134
Analytical
grade
-
25 35
4 hf
46 hr
90 days
76 hr
7 days
48 hr
43 hr
24 hr
24 hr
• 14 days •
28.3 hr
3hr
11 days
28 days
EC50
Reduced
chlorophyll
Increased
chlorophyll
Reduced growth
BCF
EC50
(DNA reduction)
No effect
EC50-
EC50
EC50 • - •-. .
EC10
(immobilization)
LC50
BCF = 3,650
40% mortality
>3
1
1
10,000
623
2
10,000
> 50,000
>27
- 16
>6«
>6*
-0.28
3.3"
Reference
Wong et al. 1984
Geike and Parasher 1976
Geike and Parasher 1976
Parasher et al. 1978
Laseter et al. 1976
Figueroa and Simmons
1991
Dive et al. 1980
Yoshioka et al. 1985
Calamari et al. 1983
Calamari et al. 1983
Sugatt et al. 1984
Yoshioka et al. 1986
Russell and Gobas 1989
Nebeker et al. 1989
Gammarus lacustris
-------
Table 6. (Continued)
Hardness
(mg/L as
Species Chemical CaCO,)
Crayfish (juvenile),
Procambarus clarki
Crayfish (male),
Procambarus clarki
Crayfish (female),
Procambarus clarki
Crayfish (male),
Procambarus clarki
Crayfish (juvenile),
Procambarus clarki
Rainbow trout. Analytical 320
Oncorhynchus mvkiss grade
Atlantic salmon,
Salmo salar
Fathead minnow (juvenile), - 25-35
Pimephales promelas
Guppy (2-3 mo), - 25
Poecilia reticulata
Largemouth bass,
Micropterus salmoides
Largemouth bass,
Micropterus salmoides
Largemouth bass,
Micropterus salmoides
Largemouth bass/ ' '• - -
Micropterus salmoides
Largemouth bass,
Micropterus salmoides
Duration
10 days
1 0 days
1 0 days
1 0 days
1 0 days
24 hr
96 hr
28 days
1 4 days
1 0 days
1 0 days
1 5 days
1 5 days
1 5 days
Effect
Damaged the
hepatopancreas
Whole body
BCF = 149
Whole body
BCF = 83
Whole body
BCF - 112
Whole body
BCF = 75
LC50
Accumulation
coefficient = 753
No mortality or
effects upon
growth
LC50
Damaged the liver
and kidney
Damaged the
gallbladder
Whole body
BCF - 44,000
Whole body
BCF - 33,800
Whole body
BCF = 18.200
Result
u/g/U
5
27.3
27.3
36.1
36.1
>27
6.6
3.8
>320
3.5
25.8
2
2
2
Reference
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Calamari et al. 1983
Zitko 1977
Nebeker et al. 1 989
Konemann 1979. 1981
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
-------
Table 6. (Continued)
Species
Largemouth bass,
Micropterus salmoides
Hardness
(mg/L as
Chemical CaCO,l
-
Duration
1 5 days
Effect
Whole body
BCF = 32.500
Result
t^g/U
2
Reference
Laseter et al.
1976
' The tested concentration was at saturation, which was estimated to be pg/L based on Metcalf et al. (1973).
" See text.
ro
-j
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