Draft
3/14/86
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
PARATHION
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
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NOTICES
This document has been reviewed by the Criteria and Standards Division,
Office of Water Regulations and Standards, U.S. Environmental Protection
Agency, and approved for publication.
Mention of trade names or 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.
ii
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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 a 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.
James M. Conlon
Acting Director
Office of Water Regulations and Standards
111
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ACKNOWLEDGMENTS
Loren J. Larson
(freshwater author)
University of Wisconsin-Superior
Superior, Wisconsin
Jeffrey L. Hyland
Sam R. Petrocelli
(saltwater authors)
Battelle New England Laboratory
Duxbury, Massachusetts
Charles E. Stephen
(document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
David J. Hansen
(saltwater coordinator)
Environmental Research Laboratory
Narragansett, Rhode Island
Clerical Support:
Shelley A. Heintz
Terry L. Highland
Diane L. Spehar
Nancy J. Jordan
IV
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CONTENTS
Page
Foreword iii
Acknowledgmenta iv
Tables vi
Introduction 1
Acute Toxicity to Aquatic Animals 3
Chronic Toxicity to Aquatic Animals 4
Toxicity to Aquatic Plants 5
Bioaccumulation 6
Other Data 6
Unused Data 9
Summary 12
National Criteria 13
References 37
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TABLES
Page
1. Acute Toxicity of Parathion Co Aquatic Animals 15
2. Chronic Toxicity of Parathion To Aquatic Animals 22
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios 23
4. Toxicity of Parathion to Aquatic Plants 27
5. Bioaccumulation of Parathion by Aquatic Organisms ........ 28
6. Other Data on Effects of Parathion on Aquatic Organisms 29
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Introduction*
Farathion (0,0-diethyl 0-4-nitrophenyl phosphorothioate, sometimes
called ethyl parathion or parathion-ethyl) is one of several organophosphorus
pesticides developed to replace the more persistent organochlorine pesticides.
It is now a restricted-use pesticide that is effective against a wide-range
of insect pests on many fruit, nut, vegetable, and field crops. It is
usually formulated as an emulsifiable concentrate, but is also available in
granules, dusts, aerosols, oil sprays, and wettable powders. These formulations
often contain large percentages of unspecified ingredients, which are often
considered inert. Although no studies have compared the relative toxicities
of technical-grade parathion and its various formulations, other organo-
phosphorus insecticides (e.g., chlorpyrifos) have been shown to differ
substantially in this regard. Although some data obtained from studies
on formulations are discussed, data from such studies are not used in
deriving criteria.
The toxicity of parathion is the result of metabolic conversion
to its oxygen analogue, parathion-oxon (paraoxon) and its subsequent binding
to and inhibition of various enzyme systems (e.g., cholinesterases, car-
boxylases, acetylcholinesterases and mitochondrial oxidative phosphorylases).
Its inhibition of acetylcholinesterase (AChE) is generally accepted to be
* An understanding of the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses"
(Stephan et al. 1985), hereafter referred to as the Guidelines, is necessary
in order to understand the following text, tables, and calculations.
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its most critical toxic effect. Inhibition of AChE results in accumulation
of the neurotransmitter acetylcholine in synapes, disrupting normal
neural transmission. Although even substantial reductions in brain AChE
activity in fish have not always been fatal, the effect of this condition on
normal activities (e.g., feeding, reproduction, predator-prey relationships,
etc.) in nature is not known. Farathion has also been demonstrated to
produce teratogenic effects in fish embryos (Solomon 1977; Solomon and
Weis 1979; Tomita and Matsuda 1961).
Parathion is less persistent than organochlorine pesticides and
has such a great affinity for organic material that it is quickly sorbed to
sediments and suspended particulate matter. Miller et al. (1967) observed
a rapid decrease in concentration after application of parathion to irriga-
tion water and attributed it to degradation. It is more likely that
sorption contributed greatly to this decrease. The persistence of parathion
in water is dependent on chemical hydrolysis and biodegradation (Ahmed
and Casida 1958; Faust 1975; Faust and Gomaa 1972; Comaa and Faust 1977;
Ludemann and Herzel 1973; Mackiewicz et al. 1969; Mulla 1963; Van Middlem
1966; Zuckerman et al. 1970). Graete et al. (1970) reported that the
portion of parathion degradation attributable to abiological in natural
lake sediments means was negligible. Movement and persistence of parathion
has been described in a natural pond (Mulla et al. 1966; Nicholson et al.
1962), a model stream (Laplanche et al. 1981), and a model ecosystem
(Dortland 1980). Several studies report concentrations of parathion in
water (Braun and Frank 1980; Dick 1982; Harris and Miles 1975; Greve
et al. 1972; Kannan and Job 1979; Sethunathan et al. 1977) and in biota
(Chovelon et al. 1984; Haddadin and Alawi 1974; Hesselberg and Johnson
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1972; Perry et al. 1983). U.S. EPA (1975) and vom Rumker et al. (1974)
reviewed the use, distribution, fate, and effects of parathion.
Unless otherwise noted, all concentrations reported herein are
expressed as parathion, not as the material tested. The criteria presented
herein supersede previous aquatic life water quality criteria for parathion
(U.S. EPA 1976) 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
1983a), which may include not only site-specific criterion concentrations
(U.S. EPA 1983b), but also site-specific durations of averaging periods
and site-specific frequencies of allowed excursions (U.S. EPA 1985).
The latest literature search for information for this document was conducted
in February, 1985; some newer information was also used.
Acute Toxicity to Aquatic Animals
The results of acute tests that were considered useful for deriving
water quality criteria for parathion are listed in Table 1. The most
striking disparity of values within a species in Table 1 is for the
crayfish, Orconectes nais. An early instar was 375 times more sensitive
to parathion than adults. The LC50 of 0.04 \ig/l> for this early instar of
Orconectes nais is the lowest available acute value.
Freshwater Species Mean Acute Values (Table 1) were calculated as
geometric means of the available acute values, and then Genus Mean Acute
Values (Table 3) were calculated as geometric means of the available
freshwater Species Mean Acute Values. Of the 31 genera for which acute
values are available, the most sensitive genus, Orconectes. is over
130,000 times more sensitive than the most resistant, Tubifex and
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Linmodrilus. Although nine of the 31 freshwater genera are fishes, the
fifteen most sensitive genera are all invertebrates. However, the two
most resistant genera are also invertebrates. Acute values are available
for more than one species in each of five genera, and the range of Species
Mean Acute Values within four of the genera is less than a factor of 1.9.
In the fifth genus, the Ganmarus, the acute values for mature individuals of
the two species are similar, but acute values are available for younger
individuals, which are apparently more sensitive, for only one of the species.
The freshwater Final Acute Value for parathion was calculated to be 0.1298
pg/L using the procedure described in the Guidelines and the Genus Mean
Acute Values in Table 3. The acute value for the crayfish, Orconectes
naia, is about one-third the Final Acute Value.
Data on the acute toxicity of parathion are only available for two
saltwater species (Table 1). The 96-hr LC50 for the Korean shrimp,
Palaemon macrodactylus, was 11.5 pg/L in a static test and 17.8 pg/L in a
flow-through test (Earnest 1970). Korn and Earnest (1974) reported that
the 96-hr LC50 for the striped bass, Morone saxatilis, was 17.8 pg/L.
Acute values are not available for enough species to allow calculation of
a saltwater Final Acute Value.
Chronic Toxicity to Aquatic Animals
Chronic tests on parathion have been conducted with three freshwater
invertebrates and three freshwater fishes (Spacie 1976; Spacie et al.
1981). Because of experimental problems, especially high control mortality,
only data for Daphnia magna, the fathead minnow, and the bluegill are con-
sidered acceptable for use in deriving criteria. Some data are available from
these studies on long-term effects on survival (Table 5), but it is not
known whether other effects were more or less sensitive. For example, in
4
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an exposure that began with brook trout embryos, an LC50 of 75 (Jg/L was
obtained, but the duration was not given. In addition, 32 pg/L caused
developmental abnormalities, whereas 10 pg/L reduced percent hatch, but
did not cause abnormalities.
In the life-cycle test with I), magna. the 21-day LC50 was 0.14 pg/L,
and the number of young produced was reduced by 0.12 Mg/L, but not by
0.0817 pg/L. Chronic exposure of bluegill larvae produced no statistically
significant effect on length at 30, 60, and 90 days. There was also no
statistically significant effect on number of eggs spawned, percent
hatch, or survival of larvae at 7, 14, 21, and 30 days.
Fathead minnows were reported to be significantly affected by chronic
exposure to parathion at 9.0 pg/L, but not at 4.4 pg/L. The Acute-
Chronic Ratio for fathead minnows is 79.45, whereas that for bluegills is
2,121 (Table 2).
The three Acute-Chronic Ratios available for parathion are 10.10,
79.45, and 2,121. The two highest ratios were obtained with two fish
species that are acutely quite resistant to parathion. The ratio of
10.10 was obtained with an invertebrate that is acutely fairly sensitive
to parathion. Thus it seems reasonable to use 10.10 as the Final Acute-
Chronic Ratio. Division of the freshwater Final Acute Value of 0.1298
pg/L by the Final Acute-Chronic Ratio of 10.10 results in a Final Chronic
Value of 0.01285 pg/L.
No data are available on the chronic toxicity of parathion to
saltwater animals.
Toxicity to Aquatic Plants
Data are available on the toxicity of parathion to two freshwater
algae (Table 4). The blue-green alga, Microcystis aeruginosa. was affected
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at 30 pg/L> whereas the green alga, Scenedesmus quadricauda was not
affected by concentrations below 390 pg/L.
No data are available concerning the toxicity of parathion to saltwater
plants.
Bioaccumulation
Spacie (1976) and Spacie et al. (1981) reported long-term bioconcentration
factors (BCFs) for the brook trout, fathead minnow, and bluegill (Table 5),
and short-term BCFs are available for the brown trout, brook trout, and
bluegill (Table 6). The BCFs determined with brook trout did not show a
consistent relationship with either concentration in water or duration of
exposure (Tables 5 and 6); the 260-day BCFs ranged from 31 to 232 for
muscle tissue. The 260-day BCFs based on whole-body measurements with
fathead minnows ranged from 32.9 to 201.4. The short-term BCFs measured
with bluegills increased steadily with duration of exposure from 80.5 at
12 hr to 462 at 72 hr, but the BCF at 540 days was only 27.
No data are available on the bioaccumulation of parathion by saltwater
species that can be used in the derivation of water quality criteria.
No U.S. FDA action level or other maximum acceptable concentration
in tissue is available for parathion, and, therefore, no Final Residue
Value can be calculated.
Other Data
Additional data on the effects of parathion on aquatic organisms are
given in Table 6. The majority of the data are LCSOs for durations
other than 96 hours. Ahmed (1977) observed a range in 24-hr LCSOs from
1.8 pg/L to 40 Mg/L with six freshwater coleopteran species. Because of
its wide use as a mosquito larvicide, many data are available on acute toxicity
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to mosquito larva. However, standard methods for testing effectiveness of
larvicides prescribe a 24-hr test duration. The 24-hr LCSOs for seven
species of mosquitos in three genera range from 0.47 to 68 pg/L. Gutierrez
et al. (1977) reported LCSOs from 1.8 to 70 pg/L for larvae of resistant
populations of Culex pipiens.
Kynard (1974) observed avoidance of parathion by mosquitofish, and
Weiss (1961) found inhibition of AChE in brains of several freshwater
fishes. Effects on locomotor behavior of goldfish, bluegills, and largemouth
bass were reported by Rand (1977a,b) and Rand et al. (1975). Sun and
Taylor (1983) studied effects of parathion on acquisition and retention
of a conditioned response in goldfish.
Various studies have examined the effect of a detergent (Solon and
Nair 1970; Solon et al. 1969), herbicides (Lichtenstein et al. 1975), and
an N-alkyl compound, SKF-525A (Gibson and Ludke 1973) on the toxicity of
parathion. Banas and Sprague (1981) reported that prior exposure of rainbow
trout did not affect the LC50.
Several studies evaluated the effectiveness of using trout for
detecting pollutants including parathion (Jung 1973; Morgan 1975,1976;
Van Hoof 1980). Morgan (1977) reported that fishes were able to detect
parathion at 15Z 48 hr-LC50. Mount and Boyle (1969) examined the use of
the concentration of parathion in fish blood to diagnose causes of fish .kills.
Ghetti and Gorbi (1985) studied the effects of a simulated parathion
spill on a stream. Albright et al. (1983), Gasith and Perry (1980,1983,1985),
Gasith et al. (1983a,b), and Grzenda et al. (1962) reported community
effects of parathion on a pond. Warnick et al. (1966) found that increases
in the concentrations of organochlorine compounds in water correlated with
application of parathion to a pond. They postulated that these compounds
were released from decomposing tissues of intoxified organisms.
7
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At a concentration of 1,000 pg/L, parathion reduced the rate of
growth of natural saltwater plankton communities by 9.9Z in 4 hr (Butler
1964). Juvenile pink shrimp, Penaeue duorum, had a 48-hr EC50 of 0.24
pg/L, whereas the ECSOs for other penaeid and palaemonid shrimp ranged
from 1.0 to 5.5 pg/L (Butler 1964; Lowe et al. 1970; U.S. Bureau of
Commercial Fisheries 1966,1967). Grass shrimp, Palaemonetes pugio.
exposed to 0.1 or 0.5 pg/L were more susceptible to predation by gulf
killifish, Fundulus grandis (Farr 1977). Limb regeneration and time to
molting of the fiddler crab, Uca pugilator, were apparently unaffected by
exposure to parathion for 2 to 3 weeks, but all crabs exposed to 100 pg/L
died (Weis and Mantel 1976). The 96-hr EC50 based on shell deposition
was 850 Mg/L or higher for the eastern oyster, Crassostrea virginica
(Butler 1963,1964; Lowe et al. 1970; U.S. Bureau of Commercial Fisheries
1966). Lowe et al. (1971) found that growth of juvenile oysters was not
reduced by exposure to 0.8 Mg/L for 252 days. Davis and Hidu (1969)
reported a 782 reduction in length of oyster larvae after a 12-day
exposure to 1,000 Mg/L.
The sensitivity of saltwater fishes to parathion did not differ
greatly. The 48-hr LCSOs were 15 Mg/L for longnose killifish, Fundulus
similis; 18 pg/L for spot, Heiostomus xanthurus; 36 pg/L for sheepshead
minnows, Cyprinodon variegatus; and 100 pg/L for striped mullet, Muzil
cephalus (Butler 1964; Lowe 1979; and U.S. Bureau of Commercial Fisheries
1966,1967). Fin regenerative ability was reduced in adult mummichogs,
Fundulus heteroclitus, exposed to 10 pg/L for 10 weeks (Weis and Weis
1975) and this fish had a 50Z incidence of circulatory failure when
exposed to 10,000 pg/L for three days (Weis and Weis 1974).
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Inhibition of acetylcholinesterase (AChE) in saltwater fishes is a
function of degree and duration of acute exposure and appears associated
with death. Regardless of concentration and duration of exposure, when
40 to 60Z of the sheepshead minnows, pinfish, and spot died, survivors
had AChE reductions of >_ 82.3Z (Coppage 1972, Coppage and Mathews 1974).
Reductions of AChE of up to 82Z were observed without death in a 120-hr
exposure of sheepshead minnows to 5 pg/L parathion (Coppage 1972).
White et al. (1979) reported 57 to 90Z inhibition of brain cholinesterase
activity in dead laughing gulls, Larus artricilla. contaminated with
parathion applied to crops. Death of chicks was suspected to be a result
of parathion in their food.
Unused Data
Some data on the effects of parathion on aquatic organisms were not
used because the studies were conducted with species that are not resident
in North American (e.g., Basak and Konar 1976; Bellavere and Gorbi 1984;
Bowman et al. 1981; Butler 1964; Dortland 1980; Fleming 1981; Gregory et
al. 1969; Gupta et al. 1979; Hashiomoto and Nishiuchi 1981; Hudson et al.
1979; luhnke and Ludemann (1978); Nishiuchi and Hashimoto 1967; Nishiuchi
and Yoshida 1972; Palawski et al. 1983; Panwar et al. 1976; Price 1976,1978;
Rattner 1982; Shah et al. 1983; Siva-Prasada et al. 1983; Weiss 1959) or
because the test species was not obtained in North America and was not
identified well enough to determine if it is resident in North America
(e.g., Lahav and Sarig 1969). Tarpley (1958) conducted tests with brine
shrimp, which species are too atypical to be used in deriving national
criteria. Data were not used if parathion was a component of a mixture
(e.g., Macek 1975) or if the test chamber contained sediment (D'Asaro
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1982; Farr 1977,1978). Cole and Plapp (1974) did not verify that the
parathion was dissolved off the test tubes by the test solution.
Anderson (1959), Chiou et al. (1977), Henderson et al. (1959>,
LeBlanc (1984), Ramke (1969), Sato and Kubo (1965), Surber (1948), and
Tarzvell (1959a,b) only presented data that had been published elsewhere.
Some studies were not used because test procedures or materials were not
adequately described (e.g., Gillies et al. 1974; Hart and Womeldorf 1977;
Rleerekoper 1974; Konar and Basak 1973; Lahav and Sarig 1969; Leva11en
and Wilder 1962; Micks and Rougeau 1977; Moore 1970; Mulla 1980; Wilder
and Schaefer 1969; and Zboray and Gutierrez 1979).
Data were not used if the organisms were exposed to parathion by
injection or gavage or in food (e.g., Benke et al. 1973,1974; Carlson 1973;
Hashimoto and Fukami 1969; Ring et al. 1984; Loeb and Kelly 1963; and
Murphy et al. 1968).
Bradbury (1973a,b), Chambers (1976), Dortland (1978), Dortland et
al. (1976), Estenik and Collins (1979), Goldsmith et al. (1976), Hiltibran
(1974,1982), Hitchcock and Murphy (1971), Huddart (1978), Ludke et al.
(1972), McDonald and Fingerman (1979), Murphy et al. (1968), Nollenberger
(1982), Nollenberger et al. (1981), Schoor and Brausch 1980, Weiss (1959),
Weiss and Gakstatter (1964,1965), Whitmore and Hodges (1978), and Yahalomi
and Perry (1981) only exposed enzymes, excised tissues, or cell cultures or
conducted other biochemical or histological studies. Bourquin et al.
(1977a,b), Garnas and Crosby (1979), Lewis et al. (1984), Pritchard and Bourquin
(1977), and Pritchard et al. (Manuscript a,b) only studied the metabolism
of parathion.
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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., Burchfield and Storrs 1954; Goldsmith 1978;
Goldsmith and Carlson 1979; Lewallen 1959,1962; Lichtenstein et al.
1966; and Yasuno et al. 1965) or if too few test organisms were exposed
(e.g., Carlson 1973; Ludemann and Neumann 1961).
Hughes (1970,1973) did not acclimate the test organisms to the
dilution water for a long enough period of time. Laboratory studies
using formulations of parathion were not used (e.g., Alexander et al.
1982; Basak and Konar 1976a,b; Chang and Lange 1967; Davey et al. 1976;
Gaufin et al. 1961; Hilsenhoff 1959; Labrecque et al. 1956; Mohamed and Gupta
1984; Panwar et al. 1982; Singh and Singh 1981, Sreenivasan and Swaninathan
1967; Srivastava et al. 1977; Verma et al. 1981). Field studies in which
the concentration of parathion was not measured were not used (e.g., Ahmed
and Washino 1977; Benge and Fronk 1970; Chang and Lange 1967; Davey and
Meisch 1977; Davey et al. 1976; Gahan 1957; Grigarick and Way 1982;
Labrecque 1956; Mulla and Isaak 1961; Mulla et al. 1963,1964,1978;
Myers et al. 1969; Stewart 1977).
High control mortalities occurred in tests reported by Fleming et
al. (1982). High pesticide residues were found in field collected worms
by Naqvi (1973), and the concentration of solvent was too high in studies by
Poorman (1973).
Microcosm studies were not used (e.g., Dortland 1980; Francis et al.
1980; Miller et al. 1966; Tu and Sanborn 1975).
Results of laboratory bioconcentration tests were not used if the
test was not flow-through or renewal (e.g., Verma and Gupta 1976) or the
concentration in water was not measured (e.g., Kortus et al. 1971). A
11
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bioconcentration study by Schmidt and Weidaaa (1961) was not used because
radio-labeled parathion was not adequately identified as the source of
residue radioactivity. Reports of concentrations of parathion in wild
aquatic organisms (e.g., Badawy and El-Dib 1984; Bradbury 1973a,b; Butler
and Schutzmann 1978) were not used to calculate bioaccumulation factors
if the number of measurements of the concentration was too small or if
the range of the measured concentrations was too great.
Summary
The acute values for thirty-five freshwater species in twenty-nine
genera range from 0.04 pg/L for an early instar of a crayfish, Orconectes
nais, to 5,230 pg/L for two species of tubifid worms. Chronic toxicity
values are available for two freshwater fish species, the bluegill and
the fathead minnow, with chronic values of 0.24 (Jg/L and 6.3 pg/L, and
acute-chronic ratios of 2,121 and 79.45, respectively. Two freshwater algae
were affected by toxaphene concentrations of 30 and 390 pg/L, respectively.
Bioconcentration factors determined with three fish species ranged from
27 to 573.
The acute values that are available for saltwater species are 11.5
and 17.8 pg/L for the Korean shrimp, Palaemon macrodactylus and 17.8 pg/L
for the striped bass, Morone saxitalis. No data are available concerning
the chronic toxicity of parathion to saltwater species, toxicity to
saltwater plants, or bioaccumulation by saltwater species. Some data
indicate that parathion is acutely lethal to commercially important
saltwater shrimp at concentrations as low as 0.24 pg/L. Measurement of
AChE might be useful for diagnosing fish kills caused by parathion.
12
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National Criteria
The procedure* 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 parathion does not exceed 0.013 pg/L more than once every three years
on the average and if the one-hour average concentration does not exceed
0.065 pg/L more than once every three years on the average.
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms
and Their Uses" require the availability of specified data for the derivation
of a criterion. Very few of the required data are available concerning
effects on parathion on saltwater species.
The allowed average excursion frequency of three years is the Agency's
best scientific judgment of the average amount of time it will take an
unstressed aquatic ecosystem to recover from a pollution event in which
exposure to parathion exceeds the criterion. Stressed systems, for
example one in which several outfalls occur in a limited area, would be expected
to require more time for recovery. The resiliencies of ecosystems and
their abilities to recover differ greatly, however, and site-specific
criteria 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. Limited data or other considerations might make their use
impractical, in which case one must rely on a steady-state model. The
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Agency recommends interim use of 1Q5 and 1Q10 for the Criterion Maximum
Concentration (CMC) design flow and 7Q5 and 7Q10 for the Criterion Continuous
Concentration (CCC) design flow in steady-state models for unstressed and
stressed systems, respectively. These matters are discussed in more
detail in the Technical Support Document for Water Quality-Based Toxics
Control (U.S. EPA 1985).
14
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Tablo I. Acvte ToHlclty of ParatMoN to Aquatic AftlMls
Specie*
LCN Species
or BC30 Acute Volvo
MotHoo* CMmlcal" (.o/U*** (.oA)
Roi
Tub 1 field worm,
Llonodrllus sp.
Tublfleld worm,
Tub If ex sp.
Cladocoran,
Oaphnla magna
Cladocoran «24 hr) ,
Daphnla magna
Cladocoran, «24 hr) ,
Daphnla magna
Cladocoran (<24 hr) ,
Daphnla magna
Cladocoran (1st Instar) ,
Daphnla pulex
Cladocoran (1st Instar),
Slmocephalus sorrulatus
Isopod,
Asollus brovlcaudus
Isopoda (mature) ,
Asellus brevlcaudus
Anphlpod (mature) ,
Gammarus fasclatus
Anph 1 pod ( natur e) ,
Gommarus fasclatus
Anphlpod (mature) ,
Gammarus fasclatus
S, U
S, U
S, U
S, M
S, U
F, M
s, u
S, U
S, U
S. U
S, U
F. U
S, U
FRESHWATER
Analytical
(99.61)
Analytical
(99.61)
-
Reagent
(99*)
Analytical
(99*)
Reagent
(99*)
Technical
(98.7*)
Technical
(98.7*)
Technical
(98.7*)
Technical
(98.7*1
Technical
(98.7*1
Tochn leal
(98.7*)
Technical
(98.7*)
SPECIES
5,230»»"
5,230"»"«
1.8
1.27
1.3
1.0
0.60
0.47
600
2,130
4.5*
1.3*
5,230 Whltten and Goodnight
1966
5,230 Whltten and Goodnight
1966
Brlngmann and Kuhn 1960
Spacle 1976; Spacle
et al. 1981
Dor t land 1980
1.0 Spacle 1976; Spacle
et al. 1981
0.60 Johnson and Flnley
1980
0.47 Johnson and Flnley
1980
Sanders 1972
1,130 Johnson and Flnley
1980
Sanders 1972
Sanders 1972
Johnson and Flnley
1980; Sanders 1972
-------
Table 1. (eontlMMdl
Species
MetOod* Chemical**
LC30 Seecle* Mean
or GC90 Acute Vale*
Reference
Amph 1 pod ( Immature) ,
Gammarus fasclatus
Amphlpod (Immature),
Gammarus fasclatus
Amphlpod (Immature),
Gammarus fasclatus
Amphlpod ( Immature) ,
Gammarus fasclatus
Amphlpod (mature),
Gammarus lacustrls
Prawn,
P a laemonetes kad 1 akens 1 s
Prawn (mature) ,
Palaemonetes Kadi akens Is
Crayfish (mature) ,
Orconectes nals
Crayfish (early Instarl ,
Orconectes nals
Crayfish (mature),
Procambarus sp.
Phantom midge,
Chaoborus sp.
Phantom midge,
Chaoborus sp.
Phantom midge,
Chaoborus sp.
MBBVMMMH
F, M
F, M
F, M
F, M
S, U
F, U
S, U
S, U
S, U
S, U
S, U
S, U
S, U
Reagent
(99*)
Reagent
(99*)
Reagent
(99*)
Reagent
(99*)
Technical
(98.7*)
Technical
(98.7*)
Technical
(98.7*)
Technical
(98.7*)
Technical
(98.7*)
Technical
(98.7*)
-
-
-
0.43 - Spacle 1976; Spacle
et al. 1981
0.62 - Spacle 1976; Spacle
et al. 1981
0,26 - Spacle 1976; Spacle
et al. 1981
0.25 0.3628 Spacle 1976; Spacle
et al. 1981
3.5 3.5 Johnson and Flnlay
1980; Sanders 1969
5.0 - Sanders 1972
•1.5 2.739 Johnson and Flnley
1980; Sanders 1972
15* - Sanders 1972
0.04 0.04 Sanders 1972; Johnson
Flnley 1972
<250 <250 Johnson and Flnley
1980
48ft - Collins and Shank 1983
0.8ttf - Collins and Shank 1983
'.0 n 0.8944 Collins and Shank 1983
-------
Ta»l* 1. (eoHtlNMd)
LC50 Species
or BWO Acete Valee
Ufl/LI» (.oA)
\l
Mayfly,
Cloeon dlptenm
Mayfly.
Cloeon dlpterua
Mayfly.
Cloeon dlptenm
Mayfly (Juvenile),
Hexagenla blllneata
Omselfly (Juvenile),
Ischnura vent leal Is
Damsel fly,
Lestes congener
Stonefly,
Pteronarcel la bad la
Stonefly (naiad),
Pteronarcys callfornlca
Stonefly (2nd year class).
Pteronarcys callfornlca
Stonefly (naiad),
Acroneurla paclflca
Stonefly (2nd year class),
Claassenla sabulosa
s.
s.
R,
s.
s.
s.
s,
s,
s,
s,
s.
u
u
u
u
u
u
u
u
u
u
u
Analytical
(991)
Analytical
(99*1
Analytical
(99*)
Technical
(98.7|)
Technical
(98.71)
Technical
(>94?)
Technical
(98.7)1)
Technical
(9531)
Technical
(98.7|)
Techn leal
(9531)
Technical
(98.731)
2.5
2.6
1.7
15
0.64
3.0
4.2
32
5.4
2.9
1.5
Oortland 1980
Oortland 1980
2.227 Dortland 1980
15 Johnson and Flnley
1980
0.64 Johnson
1980
3.0 Federle
1976
and
and
Flnley
Collins
4.2 Johnson and Flnley 1980;
Sanders and Cope 1968
Jensen and Gaufln 1964
13.15 Johnson and Flnley 1980;
Sanders and Cope 1968
2.9 Jensen and Gaufln 1964
1.5 Johnson and Flnley 1980;
Sanders and Cope 1968
-------
Table 1.
Species
Chemical**
LC50 Specie*
or GCSO Acute Valve
». -^
nVT
Crawling water beetle
(adult),
Peltodytes sp.
Midge,
Chlronomus rlparlus
Midge,
Chlronomus rlparlus
Midge,
Chlronomis rlparlus
Chlronomld (4th Instar),
Chlronomis tentans
Cutthroat trout (0.3 g),
Saline clarkl
Rainbow trout (1.0 g) ,
Salmo galrdnerl
Rainbow trout
( embryo, 0 hr),
Salmo galrdnerl
Rainbow trout
(embryo, 24 hr),
Saliio galrdnerl
Rainbow trout
(embryo, 14 day),
Salmo galrdnerl
Rainbow trout
(embryo, 28 day),
Salmo galrdnerl
Rainbow trout
S, U
S. U
S, U
S, U
F, M
S, U
S, U
R, U
R, U
R, U
R, U
R, U
Technical
(>94f)
-
-
-
Reagent
(.99%}
Technical
(98.71)
Technical
(98.7*)
(99* )
(991)
(991)
(991)
(99%}
7.0 7.0
B.4"
1.6tft .
'•8 tf 1.697
31.0 31.0
1.560 1,960
1,430
10,000f
10.000f
10,000f
10.000f
10,000f
Federle and Collins 1971
Collins and Shank 1983
Collins and Shank 1983
Collins and Shank 1983
Spacle 1976; Spacle
et al. 1981
Johnson and Flnley 1980
Johnson and Flnley 1980
Van Leeuwen et al. 1985
Van Leeuwen et al. 1985
Van Leeuwen et al. 1985
Van Leeuwen et al. 1965
Van Leeuwen et al. 1985
(fry, 42 day),
Salmo galrdnerl
-------
Tiki* 1. tCONtlMMdl
Species
LC30 Specie*
•r BC90 Ac*t* Vale*
Chemical** U«A)»»» Ua/LI
R*t
Rainbow trout
(fry, 77 day),
Salmo galrdnerl
Brown trout (16-19 cm),
Salmo trutta
Brook trout (Juvenile),
Salvellnus fontlnalls
Lake trout (0.7 g) ,
Salvellnus namavcush
Goldfish (Juvenile),
Carasslus auratus
Goldfish (0.9 g),
Carasslus auratus
Fathead minnow (adult),
Plmephales prone las
Fathead minnow (1-1.9 g) .
Plmephales promelas
Fathead minnow (1-1.9 gl ,
Plmephales promelas
Fathead minnow (1-1.9 g) ,
Plmephales promelas
Fathead minnow (1-1.9 g) ,
Plmephales promelas
Fathead minnow (Juvenile),
Plmephales promelas
R, U
F, M
F, M
S, U
S. U
S, U
S, M
S, U
S, U
S, U
S, U
S, U
w^^M^^^mi«mi»
(99*)
Reagent
(99*)
Reagent
(99*)
Techn leal
(98.7*)
Technical
(99*)
Technical
(98.7*)
Reagent
(99*)
Technical
(96.9*)
Technical
(96.9*)
Technical
(96.9*)
Technical
(96.9*)
Techn leal
(99*1
1,400 1,419
1,910 1,910
1,760 1,760
1,920 1,920
2,700
1,630 2,223
1,600
1 ,400
1,600
2,800
3,700
1 ,300
Van Leeuwen et al. 1989
Spacle 1976; Spacle
et al. 1981
Spacle 1976; Spacle
et al. 1981
Johnson and Flnley 1980
Pickering et a). 1962
Johnson and Flnley 1980
Spacle 1976; Spacle
et al. 1981
Henderson and Pickering
1998
Henderson and Pickering
1998
Henderson and Pickering
1998
Henderson and Pickering
1998
Pickering et al. 1962
-------
Teble 1.
X)
Specie*
Fathead minnow (0.8 g) ,
Plmephales promelas
Fathead minnow (1.8-4.0 cm),
Plmephales promelas
Fathead minnow (adult),
Plmephales promelas
Channel catfish (1.4 g) ,
Ictalurus punctatus
Mosqultoflsh (1.1 g),
Gambusla afflnls
Guppy (6 mo) ,
Poecllla reticulate
Green sun fish (1.1 g) ,
Lepomls cyanellus
Blueglll (Juvenile),
Lepomls macrochlrus
Blueglll (1.5 g) ,
Lepomls macrochlrus
Blueglll (1.0 g).
Lepomls macrochlrus
Blueglll (Juvenile),
Lepomls macrochlrus
Largemouth bass (0.7 g) ,
Hlcropterus salmoldes
Western chorus frog (1 wk) ,
Pseudacrls trl seriate
Wet***
S, U
F, M
F, M
S, U
S, U
S, U
S, U
S. U
S, U
S, U
F, M
S, U
S, U
CM..C.I"
Techn Ice 1
(98.7*)
Analytical
(98.7*)
Reagent
(99<)
Technical
(98.7*)
Techn leal
(98.7*)
Techn leal
(99*)
Technical
(98.7*1
Technical
Technical
(96.5*)
Technical
(98.7*1
Reagent
(99*1
Technical
(98.7*1
Technical
(98.7*1
ICM
er EC30
Uo/LI»*«
2,350
1,410
900
2,650
320
56
930
95
710
400
510
620
1,000
wpQCIvS MpVM
Acute Velee
(.oAl
-
-
839.6
2,650
320
56
930
-
510
620
1,000
RereireejCe
Johnson and Flnley 1980
Solon et al. 1969;
Solon and Nalr 1970
Spacle 1976; Spacle
et al. 1981
Johnson and Flnley 1980
Johnson and Flnley 1980
Pickering et al. 1962
Johnson and Flnley 1980
Pickering et al. 1962
Henderson and Pickering
1958
Johnson and Flnley 1980
Spacle 1976; Spacle
et al. 1981
Johnson and Flnley I960
Sanders 1970
-------
T«bl« 1. leoiitlMiMd)
Korean shrimp (adult),
Palaemon macrodactvlus
Korean shrimp (adult),
Palaemon macrodactylus
Striped bass (Juvenile).
Morone saxatllls
MetOod* Oemlcel**
LC90
or GC50
SALTWATER SPECIES
F, U
S. U
F, U
(99*)
199%}
(99*)
17.8
11.9
17.8
Specie*
Ac«te Velwe
14.31
17.8
Ret
Earnest 1970
Earnest 1970
Korn and Earnest 1974
* S » static; R " renewal; F • flow-through; U * unmeasured; M * Measured.
** Percent purity Is given In parentheses when available.
**' If the concentrations were not measured and the published results were not reported to be adjusted
for purity, the published results ware multiplied by the purity If It was reported to be less than
97*.
••"• Llmnodrllls sp. and Tub If ex sp. were tested together, but appeared to be equally resistant.
* Not used In calculation of Species Mean Acute Value because data are available for a more
sensitive life stage.
** 4*C; not used In calculations.
ttt 22.c.
-------
Table 2. Chronic Toxic I ty of ParctMon to Aquatic Animal*
Xi
Specie*
Cladoceran,
Oaphnla magna
Fathead minnow,
Plmephales promelas
Blueglll,
Lepomls macrochlrus
Limit* Chromic Valve
Test* Chemical** («o/LlM* UaAl
FRESHWATER SPECIES
LC Reagent 0.0817-0.12 0.0990
(99|)
LC Reagent 4.4-9.0 6.293
(99|)
LC Reagent 0.17-0.34 0.2404
(99*)
Reter—~
Spacle 1976;
et al. 1981
Spacle 1976;
et al. 1981
Spacle 1976;
et al. 1981
Spacle
Spacle
Spacle
• LC • life-cycle or partial life-cycle.
** Percent purity
Is given In parentheses when available.
*** Results are based on measured concentrations of parathlon.
Acute-Chronic Ratio
Acute Valee Chronic Valve
Specie* doA) UgA!
Cladoceran, 1.00 0.0990
Oaphnla magna
Fathead minnow, 900 6.293
Plmephales promelas
Ratio
10.10
79.45
Blueglll,
Lepomls macrochlrus
510
0.2404 2,121
-------
Table 3. Ranked Geam Mew Acute Valaes vltfc Species N»aa Acute-Cfcroale Ratios
V)
taah*
31
30
29
28
27
26
23
24
23
22
Aorte Valao
UoA)
5,230
5,230
2,650
2,223
1,838
1,494
1,130
1,000
839.6
688.7
Species
FRESHWATER SPECIES
Tub 1 field worm,
Tubl f ex sp.
Tub (field worn,
Llmnodrllus sp.
Channel catfish,
Ictalurus punctatus
Goldfish,
Carasslus auratus
Brook trout,
Salvellnus fontlnalls
Lake trout,
Salvellnus naaaycush
Cutthroat trout,
Salno clarkl
Brown trout,
Salmo trutta
Rainbow trout,
SB Imo galrdnerl
Isopod,
Asellus brevlcaudus
Mestern chorus frog,
Pseudacrls trlserlata
Fathead minnow,
Plmephales prom* las
Green sunflsh,
Lepomls cyanellus
Blueglll,
Species Nea*
Acvte Value
5,230
5,230
2,650
2,223
1,760
1,920
1,560
1,510
1,415
1,130
1,000
839.6
930
510
Species Mesa
Acvte-Cfcroalc
Ratio***
-
-
-
-
-
-
-
79.45
-
2,121
LepomIs Mcrochlrus
-------
T«bU 3.
*••*•
21
20
19
18
17
16
15
14
13
12
11
10
9
GMMS Mee»
Acute VelM
620
320
<250
56
31.0
15
13.15
7.0
4.2
3.0
2.9
2.739
2.227
Specie*
Largamouth bass,
Mlcropterus salmi des
Mosqultoflsh,
Gaabusla afflnls
Crayfish,
Procanbarus sp.
Guppy,
Poecllla reticulate
Midge,
Chlronoaus tentans
Mayfly,
Hexagenla blllneata
Stonefly,
Pteronarcys callfornlca
Beetle.
Pel tody tea spp.
Stonefly,
Pteronarcel la bad la
Damsel fly.
Lestes congener
Stonefly,
Acroneurla paclflca
Prawn,
Palaeaonetes kadlakensls
Mayfly,
Acvt* Velee Acvte-Cfcroitlc
(»fl/Ll** Hatlo***
620
320
<250
56
31.0
15
13.15
7.0
4.2
3.0
2.9
2.739
2.227
•
-
- '
-
-
-
-
-
Cloeon dlpterum
-------
Table 5. CcofltMeed)
Vi
Keek"
8
7
6
5
4
3
2
1
Ante Valee
(.flA)
1.697
1.5
1.127
0.8944
0.7746
0.64
0.47
0.04
Specie*
Midge,
Chlronomus rlparlus
Stonefly,
Claassenla sabulosa
Amphlpod,
Gammarus fasclatus
Amphlpod,
Gammarus lacustrls
Phantom midge,
Chaoborus sp.
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla pulex
Damsel fly,
Ischnura vent lea Us
Cladoceran,
Slmocephalus serrulatus
Crayfish,
Orconectes nals
Species Neaa
Acute Valve
1.697
1.5
0.3628
3.5
0.8944
1.0
0.60
0.64
0.47
0.04
Specie* Mean
Acute-Chronic
Ratio*"
**
_
-
10.10
-
-
* Ranked from 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 data are available so that the Final Acute
Value Is not unnecessarily lowered.
•• Fro* Table 1.
»•» From Table 2.
-------
Table 3. (continued)
Fresh water
Final Acute Value • 0.1296 tfg/L
Criterion Maximum Concentration • (0.1298 wg/L) / 2 - 0.0649 wg/L
Final Acute-Chronic Ratio- 10.10 (see text)
Final Chronic Value - (0.1296 ug/U / 10.10 • 0.01285 Mg/L
-------
Table 4. Twlclty of PeratMo* to Aquatic Pleats
Species
•
Blue-green alga,
Mlcrocvstls aeruglnosa
Green alga,
Scenedesms quadrlcauda
Duration
Chealcal* (days? Effect
FRESH HUTER SPECIES
8 Incipient
Inhibition
8 Incipient
Inhibition
Remit
30
(34)
390
Reference
Brlngmann and
I978a, b
Brlngmann and
1977; 1978a, b
Kuhn
Kuhn
* Percent purity Is given In parentheses when available.
*• If the concentrations Mare not measured and the published results Mere not reported ID be adjusted for purity, the published
results were Multiplied by the purity If It MS reported to be less than 97K.
-------
Table 5. Bl
lotion of Parat*loo by Aquatic OrgaalajM
Saocloo
BrooK trout,
Salvellnus fontlnells
Fathead minnow.
Plmaphales promelas
Blueglll,
Lepouls macrochlru*
Concentration Duration
Chemical* In Motor WUM
-------
V)
Seeefe*
Table 6. Other Data oa t*e Effects of Parattiloa oa Ajeatlc Orgaali
Raaalt
Chemical* Duration Effect (•aAIM Reference
•^•iBi^^B^B^MM ^^•••••••B ^MMMM^HMl^RM*^ ^M»^BMMMM «MMBM«M«» •^•l^BBaMVBl^mn
FRESHWATER SPECIES
Bacterlu*,
PseudoMonas put Ida
CM late,
Colpldlum campy 1 urn
Worm,
Tub If ex tub If ex
Cladoceran,
Daphnla magna
Cladoceran «24 hr old),
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran (adult),
Daphnla pulex
Cladocaran (adult),
Molna macrocopa
Prawn,
Palaemonetes kadlakansls
Mayfly,
Stenonema femoratum
Mayfly,
Stenonema vlcarlum
Mayfly, (larva).
16 hr
43 hr
18 hr
18-36 hr
24 hr
26 hr
Reagent 7 days
(99%} 14 days
21 days
Technical 3 hr
Technical 3 hr
Technical 24 hr
48 hr
48 hr
65 mln
Incipient
Inhibition
Change In
growth rate
Onset of symptoms
Onset of death
LC50
LC90
EC 50
LC50
LC50
LC50
EC50
WO
(22 *C)
EC50
LT50
>f
10,000
10,000
100,000
4
0.8
0.39
0.31
0.16
0.8
8.1
7.1.
n.e;
7.4}
6.6T
30.0
1.7
29.0
1.000
Brlngmann and Kuhn 1977
Dive et al. 1980
Ludemann and Neumann 19605
Ghettl and Gorbl 1985
Frear and Boyd 1967
Spacle 1976; Spacle et al.
1981
Nlshluchl and Hashimoto
1967,1969
Nlshluchl and Hashimoto
1967,1969
Naqvl and Ferguson 1970
Collins and Shank 1983
Collins and Shank 1983
Ghettl and Gorbl 1985
Baetls rhodanl
-------
Table i. Ccoatlmeel
Result
Specie*
Stonefly,
Allocapnla sp.
Beetle ( larva) ,
Hydrophllus trlangularls
Beetle (adult),
Hygrotus sp.
Beetle (adult),
Laccophllls declplens
Beetle (adult),
Theneonectus baslllarls
Beetle (adult),
Troplsternus lateral Is
Beetle ( larva) ,
Troplsternus lateral Is
Mater bug (adult),
Belostoma sp.
Caddlsfly,
Cheumatopsyehe sp.
Caddlsfly (larva),
Hydropsyche pellucldula
Caddlsfly,
Hydropsyche sp*
Mosquito (4th Instar)
Aedes aegyptl
Mosquito (larva),
Aedes nlqromaculls
Chemical*
Techn leal
Technical
Technical
Technical
Techn leal
Techn leal
Technical
—
-
~
32-P labeled
Technical
Duration
48 hr
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
48 hr
110 mln
48 hr
24 hr
24 hr
Effect
EC50
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
BC50
(4'C)
(22*C)
LT50
ecso
(4«C>
(22'C)
LCSO
LCSO
2.2
17
28
12
1.8
32
40
60
21.0
2.5
1,000
36.0
1.3
4.8
40
35
3.5
tf — a •«-•• r •
KeTereace
Collins and
Ahmed 1977
Ahmed 1977
Ahmad 1977
Ahmed 1977
Ahmad 1977
Ahmad 1977
Ahmed 1977
Col 1 Ins and
Shank 1983
Shank 1983
Ghettl and Gorbl 1985
Collins and
Schmidt and
Mulla at al
Shank 1983
Maldaas 1961
. 1970
-------
Takleft.
Resvlt
VJO
Specie*
Mosquito (4th Instar),
Aedes nlqromaculls
Mosquito (4th Instar),
Aedes taenlorhynchus
Mosquito (4th Instar),
Anopheles freebornl
Mosquito ( larva) ,
Anopheles freebornl
Mosquito (4th Instar),
Anopheles quadrlmacu>atu«
Mosquito (4th Instar),
Culex plplens
Mosquito (4th Instar),
Culex plplens
Mosquito (3rd-4th Instar),
Culex plplens
Mosquito ( larva) ,
Culex tar sal Is
Midge ( larva) ,
Chlronomus plumesus
Midge (4th Instar),
Chlronoaus rlparlus
Midge (2nd and 4th Instar),
Chlronomus ten tans
Chemical*
Technical
32-P labeled
Technical
Technical
32-P labeled
Technical
Techn leal
Technical
Technical
-
Technical
Reagent
(99* )
Duration
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
1 day
2 day
5 day
8 day
14 day
Effect
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
27
68
3.6
2.2-15.0
(24 values)
0.7
6.0
4.5
4.5
0.45
5.0
5.8
39
2.5
660
135
7.3
2.2
2.6
Reference
Mulla et al. 1978
Schmidt and We Ideas 1961
Womeldorf et al. 1970
Ahmed 1977
Schmidt and Weldaas 1961
Mulla et al. 1962
Mulla et al. 1964
Chen et al. 1971
Ahmed 1977
Ludemann and Neumann 1960c
Estenlk and Collins 1979
Spacle 1976; Spacle et al.
1981
-------
TabU«. (OMtlMatf)
RCMlt
Seecles
Brovn trout,
Salmo trutta
Brook trout,
Salvellnus fontlnalls
Brook trout,
Salve! Inus fontlnalls
Brook trout,
Salvellnus fontlnalls
Goldfish (1.0 g),
Cyprlnus auratus
Common carp (3.9 g) ,
Cyprlnus carplo
Common carp (1.1 g) ,
Cyprlnus carp to
Golden shiner,
(DOT-susceptlble),
Notemlqonus crysoleucas
Golden shiner
(DOT-reslstant),
Notemlgonus crysoleucas
ClMMlesI*
Reagent
(99|)
Reagent
(99*)
Reagent
(991)
Reagent
(991)
Techn leal
-
Techn leal
Technical
Technical
Duration
64 hr
-
8 hr
114 hr
140 hr
144 hr
48 hr
48 hr
48 hr
48 hr
48 hr
Effect
BCF
LC50
Reduced
percent hatch
BCF
LC50
LC50
LC50
LC50
LC50
61
77
75
to
88.5
102.5
301.5
192.5
1,700
3.500
3,200
1,895
2,800
Reference
Spacle 1976; Spacle et al.
1981
Spacle 1976; Spacle et al.
1981
Spacle 1976; Spacle et al.
1981
Spacle 1976; Spacle et al.
1981
Nlshluchl and Hashimoto
1967,1969
Ludemann and Neumann I960 a
Nlshluchl and Hashimoto
1967,1969
Mlnche* and Ferguson 1970
Mlnchew and Ferguson 1970
Golden shiner,
Notemlqonus crysoleucas
24 hr
LC50
931
Gibson 1971
-------
Table*.
Vw
Species
Chemical* Duration Effect
Re«elt
Blueglll.
Lepo»ls •acrochlrus
24 hr
LC50
Reference
Fathead minnow
(DDT-susceptlble),
Plmephales promelas
Fathead minnow
(DDT-reslstant).
Plmephales promelas
Mosqultoflsh,
Gambusla afflnls
Mosqu 1 tof 1 sh (1 5-30 mg) ,
Gambosla afflnls
Mosqultoflsh (adult)
(DDT-raslstant),
Gambusla afflnls
Mosqultoflsh (adult)
(DDT-susceptlble),
Gambusla afflnls
Guppy,
Poecllla retlculata
Guppy (7 wk old) ,
Poecllla retlculata
Green sun fish
(DDT-susceptlble),
Lepcnls cyanellus
Green sun fish
(ODT-reslstant),
Lepomls cyanellus
Green sunflsh,
Lepomls cyanellus
Technical
Technical
Technical
Analytical
Analytical
Analytical
(991)
Technical
Technical
Technical
-
48 hr
48 hr
24 hr
24 hr
48 hr
48 hr
72 hr
24 hr
48 hr
46 hr
24 hr
^^^•^•VIMBB
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
^••••••MBMB
48
199
140
1,400
390
950
350
610
29
80
45
207
275
155
Culley and Ferguson 1969
Cul ley and Ferguson 1969
Ahmed and Nash 1 no 1977
Krleger end Lee 1973
Chambers and Yarbough 1974
Chambers and Yarbough 1974
Nagasawa et a). 1968
Chen et al. 1971
Mlnchew and Ferguson 1970
Mlnchew and Ferguson 1970
Gibson 1971
141
Gibson 1971
-------
Table 6. (co*tl*»ed)
Species
Blueglll,
Lepomls macrochlrus
Chemical*
Reagent
(99*1
Ourmtlon
12 hr
18 hr
24 hr
29 hr
46 hr
70 hr
72 hr
Effect
BCF
R«Mlt
Largemouth bass,
Mlcropterus saIsoldes
Frog (tadpole),
Rene catesbetane
Natural phytoplankton
communities
Eastern oyster (Juvenile),
Crassostree vlrglnlca
Eastern oyster (juvenile),
Crassostrea vlrglnlca
Eastery oyster (juvenile
to adult),
Crassostrea vlrglnlca
Eastern oyster (larva),
Crassostrea vlrglnlca
Grass shrimp (Juvenile),
Palaemonetes puglo
Grass shrimp,
Pelaemonetes puglo
(99.6*)
(99.6*)
(99.6*1
(99.6*)
24 hr Change In operculi
rhythm
96 hr BCF
SALTWATER SPECIES
4 hr
96 hr
96 hr
336 days
12 days
48 hr
9.9* decrease In
population growth
EC50
(shall deposition)
22* reduction In
she 11 deposition
No significant
effects on growth
78* reduction In
average length
BC50 (Mortality and
loss of aqull Ibrlum)
80.5
145
173
175.3
253.0
311
462
160
50.1
1,000
850
1,000
0.8
1,000
2.8
Specie 1976; Spacle et al,
1981
(99.6*) 24-72 hr
Increased predatlon 0.1-0.5
by gulf Kllllflsh,
Fundulus grand Is
Morgan 1976
Hall and Kolba 1980
Butler 1964
Butler 1963
Butler 1964; Lowe et al
1970; U.S. Bureau of
Commercial Fisheries 1966
Lowe et al. 1971
Oavls and Hldu 1969
U.S. Bureau of Commercial
Fisheries 1967
Farr 1977
-------
Table 6. (coatinee*)
Specie* Chemical*
Brown shrimp (adult), (99.61)
Penaeus aztecus
Pink shrimp (juvenile), (99.61)
Penaeus duorarum
Fiddler crab, (95%}
Uca pug 1 later
Fiddler creb, (95*)
Uca puqllator
Sheepshead minnow (Juvenile), (99.61)
Cyprlnodon varlegatus
Sheepshead minnow (juvenile), (99.61)
Cyprlnodon varlegatus
Sheepshead minnow (adult),
Cyprlnodon varlegatus
Sheepshead minnow (adult),
Cyprlnodon varlegatus
Sheepshead minnow (adult),
Cyprlnodon varlegatus
Sheepshead minnow (adult),
Cyprlnodon varlegatus
Sheepshead minnow (adult),
Cyprlnodon varlegatus
Deration
48 hr
48 hr
2-3 wk
2-3 wk
48 hr
48 hr
2 hr
24 hr
48 hr
72 hr
120 hr
Effect
BC50 (mortal Ity and
loss of equilibrium)
EC50 (mortality and
loss of equll Ibrlum)
No effect on 1 Imb
regeneration or time
to molt
1001 mortal Ity
LC50
LC50
40-60* mortality;
brain AChE activity
reduced >82%
40-60* mortality;
brain AChE activity
reduced >82*
40-60* mortality;
brain AChE activity
reduced ±82*
40-60* mortal Ity;
brain AChE activity
reduced >B2%
Greatest reduction
(78-82*) In normal
Reselt
1
0.24
10
100
60
36
5,000
2,000
100
10
5
Reference
Butler 1964; U.S. Bureau
of Commercial Fisheries
1966
Lowe et al. 1970; U.S.
Bureau of Commercial
Fisheries 1967
Nets and Mantel 1976
Nels and Mantel 1976
Butler 1964
U.S. Bureau of Commercial
Fisheries 1966
Coppage 1972
Coppage 1972
Coppage 1972
Coppage 1972
Coppage 1972
brain AChE activity
obtained without
causing death
-------
Table 6.
Mummlchog (adult),
Fundulus heteroclltus
Mummlchog (embryo),
Fundulus heteroclltus
Chemical*
(91)1)
(95$)
Result
Longhose kllllflsh (Juvenile), (99.6$)
Fundulus slmllls
Plnflsh (65-125 mm). Technical
Lagodon rhomboldas
Spot (Juvenile), (99.61)
Lalostomus xanthurus
Spot (69-150 MI), Technical
Lalostomus xanthurus
Striped mullet (Juvenile) (99.6$)
Mug11 cephalus
Laughing gull (chick),
Larus artrlcllla
Laughing gull (adult),
Larus artrlcllla
Deration Effect
2 wk Significant reduction 10
In fin regeneration
3 days 50$ Incidence of 10,000
circulatory failure
48 hr LC50 15
24 hr 40-60$ mortality; 10
brain AChE activity
reduced 90$
48 hr LC50 18
24 hr 40-60$ mortality; 10
brain AChE activity
reduced 88$
48 hr LC50 100
Field 75-90$ Inhibition of
collections brain ChE In dead
chicks contaminated
with parathlon
Field 57-89$ Inhibition of
collections brain ChE In dead
adults contaminated
with parathlon
Reference
Wels and Mais 1973
We Is and We Is 1974
Lowe et al. 1970
Cop page and Matthews 1974
U.S. Bureau of Commercial
Fisheries 1966
Coppage and Matthews 1974
U.S. Bureau of Commercial
Fisheries 1967
White et al. 1979
White at al. 1979
* Percent purity Is given In parentheses when available.
•" If the concentrations were not measured and the published results were not reported to be adjusted for purity, the
published results ware multiplied by the purity If It was reported to be less than 97$.
* Organisms collected at sites potentially contaminated by pesticides.
-------
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-------
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