Draft
11/6/85
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
PARATHION
NOTE: This draft contains only freshwater data. The saltwater data
will be incorporated later. The freshwater CCC is likely
to change when the saltwater data are incorporated.
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH. MINNESOTA
NARRAGANSETT, RHODE ISLAND
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NOTICES
This document has been reviewed by the Criteria and Standards Division,
Office of Water Regulations and Standards, U.S. Environmental Protection
Agency, and approved for publication.
Mention of trade names or 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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ACKNOWLEDGMENTS
Loren J. Larson
(freshwater author)
University of Wisconsin-Superior
Superior, Wisconsin
Jeff Hyland
(saltwater author)
Environmental Research Laboratory
Narragansett, Rhode Island
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
David J. Hansen
(saltwater coordinator)
Environmental Research Laboratory
Narragansett, Rhode Island
Clerical Support:
Terry L. Highland
Shelley A. Heintz
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CONTENTS
Page
Foreword iii
Acknowledgments iv
Tables vi
Introduction 1
Acute Toxicity to Aquatic Animals
Chronic Toxicity to Aquatic Animals
Bioaccumulation
Other Data
Unused Data
Summary
National Criteria
References
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TABLES
Page
1. Acute Toxicity of Parathion to Aquatic Animals
2. Chronic Toxicity of Parathion To Aquatic Animals
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios
4. Toxicity of Parathion to Aquatic Plants
5. Bioaccumulation of Parathion by Aquatic Organisms
6. Other Data on Effects of Parathion on Aquatic Organisms . . .
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Introduction*
Parathion** is one of several organophosphorus compounds developed to
replace organochlorine pesticides. Its use is primarily as a domestic
and agricultural insecticide. Its direct use in aquatic environments is
most often in conjunction with mosquito abatement projects as a larvicide.
The major commercial formulation of parathion is an emulsifiable
concentrate, within which the percentage of active ingredient can vary
considerably. This results in a large percentage of often unspecified
ingredients, many used as carriers, in the commercial formulation. These
ingredients are considered inert. Although no studies have compared relative
toxicities of technical grade parathion and its emulsifiable concentrate,
other organophosphorus insecticides (e.g., chlorpyrifos) have been shown
to differ significantly in this regard. For this reason, the effect of
the inert ingredients can not be discounted.
Numerical water criteria are derived herein solely for the chemical
parathion. Although some data obtained from studies using formulations
are discussed, only data derived from toxicity tests utilizing technical
grade parathion are used in deriving criteria.
The toxic effect of parathion is the result of metabolic conversion
to its oxygen analogue, parathion-oxon, and its subsequent inhibitive
interaction with various enzyme systems (e.g., cholinesterases, carboxylases,
acetylcholinesterases, mitochondrial oxidative phosphorylation). Its
* 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.
** Parathion refers to QfQ-diethyl 0-p-nitrophenyl phosphorothionate, and
is synonymous with(ethyl parathion.
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activity with acetylcholinesterase (AChE) is generally accepted to be its
most critical toxic effect. AChE inhibition results in accumulation of
the neurotransmitter, acetylcholine, in synapes, disrupting normal neural
transmission. Although in fish even substantial reductions in brain AChE
activity have not always been fatal, the effect of this condition on
normal activity (e.g., feeding, reproduction, predator-prey relationships.
etc.) in nature is not known. Parathion has also been demonstrated to
produce teratogenic effects in fish embryos (Solomon 1977; Solomon and
Weis 1979; Tomita and Matsuda 1961).
Although less persistent than organochlorine compounds, parathion
has a great affinity for organic complexes, and is quickly sorbed to
sediments and suspended material. Miller et al. (1967) observed a rapid
decrease in water concentration after parathion application and attributed
it to degradation. It is more likely that sorbtion processes contributed
greatly to this observation. Its persistence is dependent on chemical
hydrolysis (Faust 1972, 1975; Gomaa and Faust 1971) and biodegradation
(Amed and Casida 1958: Mackiewicz et al. 1969; Zuckerman et al. 1970).
Working with natural lake sediments, Graetz et al. (1970) reported that
the portion of parathion degradation attributable to abiological means
was negligible. Movement and persistence of parathion has been described
in a natural pond (Mulla et al. 1986; Nicholson et al. 1962) and in a model
stream (Laplanche et al. 1981). Several studies report parathion residues
in water (Braun and Frank 1980; Dick 1982; Harris and Miles 1975; Greve
et al. 1972; Rannan and Job 1979; Sethunathan et al. 1977) and in biota
(Chovelon et al. 1984; Haddadin and Alawi 1974; Hesselberg and Johnson
1972; Perry et al. 1983).
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All concentrations herein are expressed as parathion, not as the
material tested. 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 exceedences (U.S. EPA 1985). The latest literature
search for information for this document was conducted in February, 1985;
some newer information was also used.
Acute Toxicity to Aquatic Animals
Data used in calculation of freshwater criteria for parathion are
found on Table 1. Thirty-five species are represented, including 13 fish.
10 insects, and 9 crustaceans. Organisms representing a range of ecological
and habitat types are included.
Ranked Genus Mean Acute Values (Table 3) for the twenty-eight genera
range from 0.47 Mg/L for a cladoceran to 5,230 Mg/L for two tubifid
worm species. Invertebrates are represented by the 15 most sensitive
genera. Of the remaining 20 genera, only 4 are invertebrates, and this
includes 2 tubifid worms which appear to be greatly more resistant to
parathion than any other organism reported on.
The most striking disparity of values within a species on Table 1 is
for the crayfish, Orconectes nais. Early instar lifestages are 375 times
more susceptible to parathion intoxication than adults (LC50 = 0.04 and
15. pg/L, respectively). Considering only this early instar, -Orconectes
nais is the most sensitive species reported on. No other values for
early instar decapods are available to suggest whether this relationship
is valid beyond this species.
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Relative toxicity to parathion (Table 3) may be influenced by
taxonomic differences, making invertebrates more susceptible. This
relationship could also be an artifact of size differences, with smaller
organisms, supposedly with higher metabolisms, being more susceptible.
There is a general increase in size with increased ranking on Table 3.
It appears that centrarchids are more susceptible to parathion than
salmonids, although this may be influenced by salmonids being cultured at
a lower temperature. Banas and Sprague (1981) report no effect on LC50
in rainbow trout acclimated to low levels of parathion.
Final Acute Value is calculated to be 0.5489 |Jg/L, resulting in
a Criterion Maximum Concentration for parathion of 0.2745 Mg/L. With the
exception of early instar crayfish, Orconectes nais, this value should be
adequately protective of all organisms reported on.
Chronic Toxicity to Aquatic Animals
Data used to determine Final Chronic Value for parathion are found
on Table 2. Information is available from a single study, reported in
two sources (Spacie 1976; Spacie et al. 1981). Although this study
reports chronic toxicity in three aquatic invertebrates and three fish.
because of experimental problems (primarily high control mortality), only
chronic values for the fathead minnow and the bluegill are used in
calculation of the Final Acute-Chronic Ratio and Final Chronic Value.
Much chronic data from this study reports LC50 data only and it is not
known whether this is the most sensitive parameter relating to chronic
intoxication. Many of these values occur on Table 5. No appropriate data
on chronic toxicity to parathion is available for arthropods.
Chronic exposure in bluegill larvae produced no statistically
significant effect on growth (in length) at 30, 60, and 90 days. There
4
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was also no statistically significant effect on number of eggs spawned,
percent hatch, and survival of larvae at 7, 14, 21, and 30 days.
In brook trout embryos LC50 was 75.0 pg/L (duration not stated)
after correction for control mortality, when considering percent hatch of
19 day old embryos. This is 4.2% of the 96 hr LC50 for the species. At
10. pg/L, percent hatch was reduced but surviving embryos were normal.
At greater than 32 Mg/L, developmental abnormalities were common.
Fathead minnows were reported to be significantly affected by chronic
exposure to parathion at 9.0 *Jg/L, with a chronic value of 6.3 ;Jg/L. Acute-
Chronic Ratio for fathead minnows is 79.4. Chronic value in bluegills is
0.24 Mg/L with an Acute-Chronic Ratio of 2125 (Table 2). Both fish were
cultured at approximately equal temperature. Acute toxicity to parathion
appeared to be greater in centrarchids (Table 1), therefore, the large
Acute-Chronic Ratio in bluegills may be indicative of high sensitivity
within this taxon.
Geometric mean of the two Acute-Chronic Ratios results in a Final
Acute-Chronic Ratio of 410.8. Division of the Final Acute Value (Table
3) by this factor results in a Final Chronic Value of 0.0013 jJg/L. This
parathion concentration is below the sensitivity limit of most analytic
methods. Chronic toxicity data for a freshater arthropod were not available,
therefore were not used in these calculations.
Toxicity to Aquatic Plants
No data is available on the relative toxicity of varying concentrations
of parathion to freshwater aquatic plants. A single study (Cole and
Plapp 1974) reported the effect of various initial cell concentrations (1
to 1000 |jg algae/ml) at a single parathion level (1000 pg/L) in terms of
growth and photosynthesis in a green alga. Chlorella pyrenoidosa (Table 5).
5
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They reported increased growth inhibition with lower cell concentrations.
With a single parathion dose, specific photosynthesis was greater in
treated cultures, although with multiple doses photosynthesis was strongly
inhibited with greatest effect at lowest cell concentrations.
Bioaccumulation
All available bioaccumulation data comes from a single study, reported in
two sources (Spacie 1976, Spacie et al. 1981). Bioaccumulation factors (BAF)
are reported in four fishes. Factors for brook trout, fathead minnows and
bluegills are found in Table 4. Addition factors, not appropriate for inclu-
sion in Table 4, are available for brown trout, brook trout, and bluegills
(Table 5).
In brook trout,"average BAF at 180 days is 392, and at 260 days is
105.9. From Table 5, 4.75 day, 5.8 day, and 6.0 day BAFs are reported to
be 102.5, 301.5, and 192.5, respectively, indicating rapid uptake of
parathion. but unstable residue levels.
At 260 days, BAF for fathead minnows averages 111.4, with a range of
32.9 to 201.4. At 64 hours, BAF in brown trout averaged 69 (Table 5). A
single bluegill produced a BAF of 27 in 560 days; at 46, 70, and 72 hrs.
factors of 253, 311, and 462 were reported (Table 5).
There is considerable variation in BAF data. This most likely is the
result of rapid metabolism of parathion in fish or other metabolic factors.
No U.S. FDA action level has been set for parathion, therefore no
Final Residue Value is calculated.
Other Data
Other data on the effects of parathion on aquatic organisms are
found on Table 5. The majority of entries are LC50 values for durations
other than 96 hours.
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A 24 hour LC50 for a non-resident snail is the only toxicity data
available for the family Mollusca. This species was very resistant, with
an LC50 of 8090 Mg/L. For a cladoceran, Daphnia magna, 0.34 pg/L
resulted in a 50Z reproductive impairment (Spacie 1978; Specie et al
1981). In six coleopteran species, Ahmed (1977) observed a range in 24
hr LC50s from 1.8 |jg/L to 40 pg/L.
Because of its wide use as a mosquito larvicide, many studies have
tested mosquito larva. Standard methods commonly adhered to using mosquito
larvae prescribe a 24 hour test duration, making most mosquito larvae
studies inappropriate for consideration in deriving numerical criteria.
The three Aedes species in Table 5 have a mean LC50 of 14.8 pg/L,
Anopheles species 24 hour LCSOs average 5.9 pg/L, and this value for
Culex species is 3.1 jJg/L.
Several studies have reported associated effects of parathion exposure.
Kynard (1974) observed avoidance of parathion by mosquitofish in the
laboratory, although the significance of this finding under natural
conditions is unknown. Weiss (1961) reports on fish brain AChE as
inhibition in several freshwater species. Effects on locomotor behavior
in goldfish, bluegills, and largemouth bass are 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.
Interaction of parathion toxicity has to be examined with 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).
Ludemann and Herzel (1973) report changes in ambient parathion concentrations
under static conditions with and without aeration, and with and without
fish. Without fish or aeration, parathion level dropped 22% in 96 hours.
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When fish were added, levels dropped 54% in 96 hours. With both fish and
aeration, 67Z reduction was observed. Other studies on the persistence
of parathion in water include Mulla (1963) and Dortland (1980).
Several studies evaluated the effectiveness of biomonitoring of
effluents using trout in detecting pollutants including parathion (Jung
1973; Morgan 1976; Van Hoof 1980). Morgan (1977) was able to detect
parathion concentrations at 15Z of the fishes 48 hour LC50. Mount and
Boyle (1969) examined the use of blood parathion residues to diagnose
causes of fish kills.
A field study by Ghetti and Gorbi (1985) reported the effects of a
simulated parathion spill in a stream. Field studies by Gasith and Perry
(1980, 1982) and Grzendz et al. (1962) reported community effects of parathion
application to a pond. Warnick et al. (1966) noted increases in water con-
centrations of organochlorine compounds correlated with parathion application
in a natural pond. They postulated the source of these compounds to be the
release from decomposing tissues of intoxified organisms.
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., Bellavere and Gorbi 1984; Dortland 1980; Gupta
et al. 1979; Hashiomoto and Nishiuchi 1981; Nishiuchi and Hashimoto 1967;
Nishiuchi and Yoshida 1972; Panwar et al. 1976; Siva Prasada et al. 1983)
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 1968). 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).
8
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Anderson (1959), Henderson et al. (1959), LeBlanc (1984), Ramke
(1969), Sato and Kubo (1965), Surber (1948), and Tarzwell (1959a, b) only
present data that have been published elsewhere. Juhnke and Ludetnann
(1978) and Gutierrez et al. (1977) present only results. Gaufin et al.
(1961) and Ludemann and Neumann (1961) cite no LC50 data. Some studies
were not used because of inadequate description of method (e.g., Mulla 1980)
or materials (e.g., Gillies et al. 1974; Hart and Womeldorf 1977; Lahav
and Sarig 1969; Leva11en and Wilder 1962: Micks and Rougeau 1977; Moore
1970; Wilder 1977; 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; Hasimoto
and Fukami 1969; Loeb and Kelly 1963 and Murphy et al. 1968).
Chambers (1976); Dortiand (1978); Dortland et al. (1976): Estenik
and Collins (1979): Goldsmith et al. (1976); Hiltibran (1974, 1982);
Huddart (1978); Ludke et al. (1972); McDonald and Fingerman (1979);
Nollenberger (1982); Nollenberger et al. (1981); Weiss (1959); Weiss and
Gakstatter (1964, 1965): Whitmore and Hodges (1978); and Yahalomi and
Perry (1981) only exposed enzymes or cell cultures or conducted other
biochemical or histological studies.
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; Carlson 1978;
Goldsmith and Carlson 1979; Lewallen 1959, 1962; Lichtenstein et al.
1966; and Yasuno et al. 1965).
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
9
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Gaufin et al. 1965; Hilsenhoff 1959: Labrecque et al. 1956; Mohamed and Gupta
1984: Pawar et al. 1982; Singh and Singh 1981, Sreenivasen and Swaninathan
1967; Srivastava et al. 1977, Venna et al. 1981). Field studies on
parathion which did not measure concentrations 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) .
Microcosm studies were not used (e.g., Dortland 1980; Francis et al.
1980: Miller et ai. 1966; Yu 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).
A bioconcentration study by Schmidt and Weidhaas (1961) was not used because
radio-labeled parathion was not adequately identified as the source of
residue radioactivity.
Summary
The acute values for thirty-five species in twenty-nine genera range
from 0.47 pg/L for a cladoceran to 5230 Mg/L for two species of tubifid
worm. The early instar of a crayfish, Orconectes nais was the most
sensitive organism reported with an acute value of 0.04 Mg/L- Invertebrates
appear to be more sensitive, although this could be related to their
smaller size. Centrarchids are more sensitive than salmonids, although
differences in culture temperature could effect this relationship.
10
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Chronic toxicity values are available for two fish species, bluegills
and fathead minnows, with chronic values of 0.24 pg/L and 6.3 pg/L,
respectively. Final Acute-Chronic Ratio was 410.8. Final Chronic Value
is calculated to be 0.0013 yg/L> which is below detection limits.
No information is available on the toxicity of parathion to freshwater
aquatic plants. Bioconcentration factors are reported in four fish
species. Average BCF for the data set is 186.7. Wide variation occurs
in BCF data possibly due to metabolism of parathion by fish.
National Criteria
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms
and Their Uses" indicate that, except possibly where a locally important
species is very sensitive, freshwater aquatic organisms and their uses
should not be affected unacceptably if the four-day average concentration
of parathion does not exceed(s0.0013 pg/L^more than once every three years
on the average or if the one-hour average concentration does not exceed
(_0.2745 (Jg/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" indicate that, except possibly where a locally important
species is very sensitive, saltwater aquatic organisms and their uses
should not be affected unacceptably if the four-day average concentration
of parathion does not exceed AAA (Jg/L more than once every three years on
the average and if the one-hour average concentration does not exceed yyy
Mg/L more than once every three years on the average.
The allowed excursion frequency of thee years is based on the Agency's
best scientific judgment of the average amount of time it will take an
11
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aquatic ecosystem to recover from a pollution event in which exposure to
parathion exceeds the criterion. The resilience of ecosystems and their
ability to recover differ greatly, however, and site-specific criteria
may be established if adequate justification is provided.
The use of criteria in designing waste treatment facilities requires
selection of an appropriate wasteload allocation model. Dynamic models
are preferred for the application of these criteria. Limited data or
other factors may make their use impractical, in which case one must rely
on a steady-state model. The Agency recommends interim use of 1Q10 for
Criterion Maximum Concentration (CMC) design flow and 7Q10 for the
Criterion Continuous Concentration (CCC) design flow in steady-state
models. These matters are discussed in more detail in the Technical
Support Document for Water Quality-Based Toxics Control (U.S. EPA 1985)
and the Design Flow Manual (U.S. EPA 1986).
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Table 1. Acute Toxic Ity of Parathlon to Aquatic Animals
Species
Method*
Chemical
LC50 Species Mean
or EC50 Acute Value
(wg/L) (Mq/L)
Reference
FRESHWATER SPECIES
Tub! field worm,
Llmnodrl lus sp.
Tubl field worm.
Tub If ex sp.
Cladoceran (<24 hr),
Daphnla magna
Cladoceran, «24 hr) ,
Daphnla magna
Cladoceran «24 hr) ,
Oaphnla magna
Cladoceran (1st Instar),
Daphnla pulex
Cladoceran (1st Instar),
Slmocephalus serrulatus
1 sopod ,
Asellus brevlcaudus
1 sopoda ( mature) ,
Asellus brevlcaudus
Amphlpod (Immature),
Gammarus fasclatus
Amphlpod (Immature),
Gammarus fasclatus
Amphlpod (Immature),
Gammarus fasclatus
Amphlpod (Immature)
s, u
s, u
F, M
S, M
S, U
S, U
S, U
S, U
S, U
F, M
F, M
F, M
F, M
Analytical
Analytical
Reagent
Reagent
Analyt leal
Techn leal
Technical
Techn leal
Technical
Reagent
Reagent
Reagent
Reagent
5,230f 5,230
5,230t 5,230
1.00
t.27
1.3'" ,.3
0.60ftt 0.60
0.47tft 0.47
600
2,130 1,130.5
0.43
0..62
0,26
0.25
Whltten and Goodnight
1966
Whltten and Goodnight
1966
Spacle 1976; Spacle
et al. 1981
Spacle 1976; Spacle
et al. 1981
Dortland 1980
Johnson and Fin ley
1980
Johnson and Fin ley
1980
Sanders 1972
Johnson and Flnley
1980
Spacle 1976; Spacle
et al. 1981
Spacle 1976; Spacle
et al. 1981
Spacle 1976; Spacle
et al. 1981
Spacle 1976; Spacle
Gammarus fasclatus
et al. 1981
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Table 1. (continued)
Species
Amph 1 pod ( mature) ,
Gammarus fasclatus
Amph 1 pod (mature),
Gammarus fasclatus
Amph 1 pod (mature),
Gammarus lacustrls
Prawn ,
Palaemonetes kadlakensls
Prawn (mature),
Palaemonetes kadlakensls
Crayfish (early Instar),
Orconectes nals
Crayfish (mature),
Orconectes nals
Crayfish (mature) ,
Procambarus sp.
Mayfly,
Cloeon dlpterum
Mayfly (Juvenile),
Hexagon la bill neata
Damsel fly (juvenile),
1 schnura ventl calls
Damsel fly,
Lestes congener
Stonef ly,
Pteronarcel la badla
Stonefly (naiad).
Method*
S, U
f. u
S, U
S, U
F, U
S, U
S, U
S, U
S, U
S, U
S, U
R, U
S, U
S, U
S, U
S, U
S, U
Chemical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
Analytical
Technical
Technical
Technical
Technical
Techn leal
LC50 Species Mean
or EC50 Acute Value
(»g/U (n9/L)
2.1
4.5
1.3 2.3
3.5 3.5
5.0
1.5 2.7
0.04
15 0.77
<250 <250
2.5
2.6
1.7 2.2
15 15
0.64 0.64
3 3
4.2 4.2
32
Reference
Sanders 1972
Johnson and Flnley
1980; Sanders 1972
Johnson and Flnley
1980; Sanders 1969
Sanders 1972
Johnson and Fin ley
1980; Sanders 1972
Johnson and Flnley
1980; Sanders 1972
Sanders 1972
Johnson and Flnley
1980
Dortland 1980
Johnson and Flnley
1980
Johnson and Flnley
1980
Federle and Col 1 Ins
1976
Johnson and Flnley
Sanders and Cope 191
Jensen and Gaufln 1<
Pteronarcys callfornlca
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Table t. (continued)
LC50 Species Mean
or EC50 Acute Value
Species Method*
Stonefly (2nd year class),
Pteronarcy s ca 1 1 torn 1 ca
Stonefly (naiad),
Acroneurla pad flea
Stonefly (2nd year class),
Claassenla sabulosa
Crawling water beetle
(adult),
Pel tody tes spp.
Chtronomld (4th Instar),
Chlronomus tentans
Cutthroat trout (0.3 g) ,
Salmo clarkl
Rainbow trout (1.0 g) ,
Salmo galrdnerj
Brown trout (16-19 cm),
Salmo trutta
Brook trout (juvenile),
Salve) Inus fontlnalls
Lake trout (0.7 g) ,
Salvellnus namaycush
Goldfish (Juvenile),
Car ass (us auratus
Goldfish (0.9 g).
Car ass 1 us auratus
Fathead minnow (adult),
Plmephales promelas
Fathead minnow (adult).
s,
s,
s,
s,
F.
s,
s,
F,
F,
s,
s,
s.
s,
F,
U
u
U
u
M
U
u
M
M
U
U
U
M
M
Chen leal
Technical
Technical
Technical
Technical
Reagent
Technical
Technical
Reagent
Reagent
Technical
Technical
Technical
Reagent
Reagent
<(,q/L) (vg/L)
5.4 13.1
2.9 2.9
1.5 1.5
7 7
31.0
1,560 1,560
1,430 1,430
1,510 1,510
1,76CI»«
1 ,920 1 ,920
2,700
1,830 2,223
1,600
500
Reference
Johnson and Fin ley 1980;
Sanders and Cope 1969
Jensen and Gaufln 1964
Johnson and Flnley 1980;
Sanders and Cope 1969
Federle and Collins 1976
Spacle 1976; Spacle
et al. 1981
Johnson and Flnley 1980
Johnson and Flnley 1980
Spacle 1976; Spacle
et al. 1981
Spacle 1976; Spacle
et al. 1981
Johnson and Flnley 1980
Pickering et al. 1962
Johnson and Flnley 1980
Spacle 1976; Spacle
et al. 1981
Spacle 1976; Spacle
Plmephales promelas
et al. 1981
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Table t. (continued)
Species Method*
Fathead minnow (1.8-4.0 cm),
Plmephales promelas
Fathead minnow,
Plmephnles promelas
Fathead minnow (1-1.5 g) ,
Plmephales promelas
Fathead minnow (1-1.5 g) ,
Plmephales promelas
Fathead minnow (1-1.5 g) ,
Plmephales promelas
Fathead minnow (1-1.5 g) ,
Plmephales promelas
Fathead minnow (juvenile),
Plmephales promelas
Fathead minnow (0.8 g) ,
Plmephales promelas
Channel catfish (1.4 g) ,
Ictalurus punctatus
Mosqultof Ish (1.1 g) ,
Gambusla of fin Is
Guppy ("6 mo) ,
Poecl 1 la retlculata
Green sunflsh (1.1 q) ,
Lepomls cyanellus
Blueglll (Juvenile),
Lepomls macrochlrus
Blueglll (juvenile).
F,
F,
s,
s.
s.
s.
s,
s.
s,
s.
s,
s,
F,
s.
M
M
U
U
U
U
U
U
U
U
U
U
M
U
Chemical
Analytical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
Reagent
Technical
LC50 Species Mean
or EC50 Acute Value
(MCJ/D (»a/L)
1,410
1,410
1,400
1 ,600
2,800
3,700
1,300
2,350 1,410
2,650 2,650
320 320
56 56
930 930
510
95
Reference
Solon et al. 1969
Solon and Nalr 1970
Henderson and Pickering
1958
Henderson and Pickering
1958
Henderson and Pickering
1958
Henderson and Pickering
1958
Pickering et al. 1962
Johnson and Fin ley 1980
Johnson and Flnley 1980
Johnson and Flnley 1980
Pickering et al . 1962
Johnson and Flnley 1980
Spacle 1976; Spacle
et al. 1981
Pickering et al. 1962
tepomls macrochlrus
-------
Table 1. (continued)
Species
Blueglll (1.0 g),
Lepomls macrochlrus
Blueglll (1.5 g) ,
Lepomls macrochlrus
Blueglll (1.5 g) ,
Lepomls macrochlrus
Largemouth bass (0.7 g) ,
Mlcropterus sal mo Ides
Western chorus frog (1 wk) ,
Pseudacrls trlserlata
Method* Chemical
S, U Technical
S, U Technical
S, U Technical
S, U Technical
S, U Technical
* S • static; R » renewal; F • flow-through; U
** Normalized by author for 5< mortality In the
* Average LC50 when cultured with Tublfex sp.
LC50 Species Mean
or EC50 Acute Value
(ng/L) (»g/L)
400
710
710 372
620 620
1 ,000 1 ,000
= unmeasured; M = measured.
control.
Reference
Fin ley and Johnson 1980
Henderson and Pickering
1958
Henderson and Pickering
1958
Johnson and Fin ley 1980
Sanders 1970
' Average LC50 when cultured with Llmnodrllus sp.
m 48 hr EC50.
-------
Table 2. Chronic Toxic Ity of Parathlon to Aquatic Anlmls
Species Test*
Fathead minnow, LC
Plmephales promelas
Blueglll, LC
Lepomls macrochlrus
* LC « life-cycle or partial llfe-cycl
Species
Fathead minnow,
Limits Chronic Value
Chemical (|ig/L) (ng/L)
FRESHWATER SPECIES
Reagent 4.4-9.0 6.3
Reagent 0.17-0.34 0.24
e
Acute-Chronic Ratio
Acute Value Chronic Value
500 6.3
Reference
Spacle 1976;
et al. 1981
Spacle 1976;
et al. 1981
Ratio
79.4
Spacle
Spac 1 e
Plmephales promelas
Blueglll.
Lepomls macrochlrus
510
0.24
2,125
-------
Table 3. Ranked Genus Mean Acute Values vlth Species Mean Acute-Chronic Ratios
tank*
29
28
27
26
25
24
23
22
21
20
Genus Mem
Acute Value
(.0/L)
5,230
5,230
2,650
2,223
1,838
1,499
1,131
1,000
998
689
Species
FRESHWATER SPECIES
Tub) field worm,
Tub If ex sp.
Tub1 field worm,
Llmnodrl lus sp.
Channel catfish,
Ictalurus punctatus
Goldfish,
Carasslus auratus
Lake trout,
Salvellnus namaycush
Brook trout,
Salvellnus fontlnalls
Cutthroat trout,
Sal mo clarkl
Brown trout.
Sal mo trutta
Rainbow trout,
Salmo qalrdner!
Isopod,
Asellus brevlcaudus
Western chorus frog,
Pseudacrls trlserlata
Fathead minnow,
Plmephales promelas
Green sun fish,
Lepomls cyanellus
Blueglll,
Species Mean
Acute Value
WD*»
5,230
5,230
2,650
2,223
1,920
1,760
1,560
1,510
1,430
1,131
1,000
998
930
510
Species Mean
Acute-Chronic
Ratio"*
79.4
2,125
Lepomls macrochlrus
-------
Table 3. (continued)
Rank*
19
18
17
16
15
14
13
12
11
10
9
8
7
Genus Mean
Acute Value
(iiq/L)
620
320
<250
56
31.0
15
13.1
7.0
4.2
3.0
2.9
2.8
2.7
Species
Largemouth bass,
Mlcropterus sal mo Ides
Mosqultof Ish,
Gambusla at fin Is
Crayfish,
Procambarus sp.
Guppy,
Poecl 1 la retlculata
Midge,
Chlronomus tentans
Mayfly,
Hexagenla blllneata
Stonef ly,
Pteronarcys call for nlca
Beetle,
Pel tody tes spp.
Stonef ly,
Pteronarcel la bad I a
Damsel fly,
Lestes congener
Stonef ly,
Acroneurla paclflca
Amph ! pod ,
Gammarus lacustrls
Amph 1 pod,
Gammarus fasclatus
Prawn ,
Species Mean
Acute Value
(iiq/L)M
620
320
<250
56
31.1
15
13.1
7.0
4.2
3.0
2.9
3.5
2.3
2.7
Species Mean
Acute-Chronic
Ratio***
-
Palaemonetes kadlakensls
-------
Table 3. (continued)
Rank*
6
5
4
3
2
1
Genus Mean
Acute Value
(»q/L)
2.2
1.5
0.77
0.77
0.64
0.47
Species
Mayfly,
Cloeon dlpterum
Stonefly,
Claassenla sabulosa
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla pulex
Crayfish,
Orconectes nals
Damsel fly,
Ischnura vent) calls
Cladoceran,
Slmocephalus serrulatus
Species Mean
Acute Value
(iia/L)**
2.2
1.5
1.0
0.60
0.77
0.64
0.47
Species Mean
Acute-Chronic
Ratio*"
-
* Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
** From Table 1.
*"* From Table 2.
Fresh water
Final Acute Value = 0.5489 Mq/L
Criterion Maximum Concentration = (0.5489 n9/L) 12= 0.2745 ug/L
Final Acute-Chronic Ratio = 410.8
Final Chronic Value * (0.5489 Mg/L) / 410.8 = 0.0013 ug/L
-------
Table 4. Bloaccumulatllon of Parathlon by Aquatic Organ I SMS
Species
Brook trout,
Salvellnus fontlnalIs
Chemical
Reagent
Fathead minnow,
Plmephales promelas
BIueg i 11,
Lepomls macrochlrus
Reagent
Concentration
In Water (ng/L)
FRESHWATER
0.44
0.53
1.26
1.45
2.76
2.86
4.24
5.53
8.30
8.72
0.6
0.6
1.4
2.6
4.0
6.7
0.15
4.2
9.0
15.5
21.7
49.0
Duration
(days)
SPECIES
260
180
260
Tissue
Muscle
Reagent
4.00
540
Whole
body
Muscle
BCF or BAF
124
86
31
43
99
91
86
88
232
179
258
312
299
439
471
573
93.3
169.4
104.6
32.9
66.8
201.4
27
Reference
Spacle 1976; Spade
et at. 1981
Spacle 1976; Spacle
et al. 1981
Spacle 1976; Spacle
et al. 1981
-------
Table 5. Other Data on the Effects of Parathlon on Aquatic Organisms
Species
Alga,
Chloral la pyrenoldosa
Alga,
Chloral la pyrenoldosa
CD late
Colpldlum campy 1 urn
Worm,
.Tub If ex tub If ex
Snail,
B 1 ompha 1 ar 1 a 9 1 abr ata
Cladoceran,
Daphnla magna
Cladoceran (<24 hr old).
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran (adult),
Daphnla pulex
Cladoceran (adult).
Molna macrocopa
1 sopod ,
Asel lus aquatlcus
Chemical Duration
Technical 7 hr
Technical 7 hr
43 hr
18 hr
18-36 hr
24 hr
24 hr
26 hr
Reagent 7 days
14 days
21 days
21 days
Technical 3 hr
Technical 3 hr
24 hr (exp.)
72 hr (rec.)
Effect
Change In growth
I.OOO'pg algae/ml*
IOO*Mg algae/ml*
10* Mg algae/ml*
I'pg algae/ml*
Result
(mg/L)
9\%
84*
74*
47*
Reference
Cole and Plapp 1974
Change In photosynthesis
1,000'Mg algae/ml*
100*pg algae/ml*
10*Mg algae/ml*
I'tig algae/ml*
MAD»»
Onset of symptoms
Onset of death
LC50
LC50
LC50
EC50
RI50
LC50
LC50
LC50
156*
118*
147*
181*
10,000
10,000
100,000
8,090
4
0.8
0.39
0.31
0.16
0.34
0.8
8.1
55«»»
Cole and Plapp 1974
Dive et al. 1980
Ludemann and Neumann I960c
Ghettl and Gorbl 1985
Ghettl and Gorbl 1985
Frear and Boyd 1967
Spade 1976; Spacle et al.
1981
Nlshluchl and Hashimoto
1967, 1969
Nlshluchl and Hashimoto
1967, 1969
Ludemann and Neumann 1960c
-------
Table 5. (continued)
Species
Prawn,
Palaemonetes kadlakensls
Mayfly (larva),
Baetls rhodanl
Beetle ( larva),
Hydrophllus triangular Is
Beetle (adult),
Hygrotus sp.
Beetle (adult),
Laccophllls declplens
Beetle (adult),
Thermonectus baslllarls
Beetle (adult),
Trop 1 sternus 1 atera 1 1 s
Beetle ( larva) ,
Trop 1 sternus 1 atera 1 1 s
Water bug (adult),
Belostoma spp.
Caddlsfly ( larva),
Hydropsyche pellucldula
Mosquito (4th Instar),
Aedes aegyptl
Mosquito ( larva) ,
Aedes nlgromacul Is
.Chemical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
Technical
32 -P labeled
Technical
Duration
24 hr
65 mln
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
24 hr
110 mln
24 hr
24 hr
Effect
LC50
LT50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LT50
LC50
LC50
Result
(mg/L)
Reference
7.1. Naqvl and Ferguson 1970
11.81
7.4}
6.6f
1,000 Ghettl and Gorbl 1985
17 Ahmed 1977
28 Ahmed 1977
12 Ahmed 1977
1.8 Ahmed 1977
32 Ahmed 1977
40 Ahmed 1977
60 Ahmed 1977
1,000 Ghettl and Gorbl 1985
4.8 Schmidt and Weldhaas 1961
Mosquito (4th Instar),
Aedes nlgromaculIs
Technical
24 hr
LC50
40
35
3.5
27
68
Mulla et al. 1970
Mulla et al. 1978
-------
Table 5. (continued)
Species Chemical Duration Effect
Mosquito (4th Instar), 32-P labeled 24 hr LC50
Aedes taenlorhynchus
Mosquito (4th Instar), Technical 24 hr LC50
Anopheles freebornl
Mosquito (larva), Technical 24 hr LC50
Anopheles freebornl
Mosquito (4th Instar), 32-P labeled 24 hr LC50
Anopheles quadr Imacu latus
Mosquito (4th Instar), Technical 24 hr LC50
Culex plplens
Mosquito (4th Instar), Technical 24 hr LC50
Culex plplens
Mosquito (3rd-4th Instar), Technical 24 hr LC50
Culex plplens
Result
dog/L) Reference
3.6 Schmidt and Weldhaas 1961
9.7 Womeldorf et al . 1970
4.5
3.7
6.3
6.2
7.2
7.6
5.7
6.1
2.9
2.6
2.4
9.7
8.6
4.9
15.0
8.0
11.0
6.0
4.0
10.0
11.0
2.2
2.6
0.7 Ahmed 1977
6.0 Schmidt and Weldhaas 1961
4.5 Mulla et al. 1962
4.5 Mulla et al. 1964
0.45 Chen et al . 1971
5.0
-------
Table 5. (continued)
Species
Mosquito (larva),
Culex tarsal Is
Midge (larva),
Chlronomus plumosus
Midge (4th Instar),
Chlronomus rlparlus
Midge (2nd and 4th Instar), Reagent
Chlronomus tentans
Brown trout.
Salmo trutta
Brook trout,
SalvelInus fontlnalIs
Goldfish (t.O g>,
Cyprlnus auratus
Carp (3.9 g),
Cyprlnus carp Io
Carp (I.I g),
Cyprlnus carplo
Golden shiner,
(DDT-susceptlble),
Notemlgonus crysoleucas
Golden shiner
(DDT-reslstant),
Notemlgonus crysoleucas
Golden shiner,
Notemlgonus crysoleucas
Chemical
Technical
-
Technical
Reagent
Reagent
Reagent
Technical
-
Technical
Technical
Duration
24 hr
24 hr
24 hr
1 day
2 day
5 day
8 day
14 day
64 hr
8 hr
114 hr
140 hr
144 hr
48 hr
48 hr
48 hr
48 hr
Effect
LC50
LC50
LC50
LC50
BAF
BAF
LC50
LC50
LC50
LC50
Result
(«g/D
Technical
48 hr
24 hr
LC50
LC50
Reference
5.8 Ahmed 1977
39
660
135
7.3
2.2
2.6
61
77
88.5
102.5
301.5
192.5
1,700
3,500
3,200
1,895
2,800
931
Ludemann and Neumann 1960b
2.5 Estenlk and Collins 1979
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 1960a
Nlshluchl and Hashimoto
1967, 1969
MlacheM and Ferguson 1970
Mlachew and Ferguson 1970
Gibson 1971
-------
Table 5. (continued)
Species
Fathead minnow
(DDT-susceptlble),
Plmephales promelas
Fathead minnow
(DDT-reslstant),
Plmephales promelas
MosqultofIsh,
Gambusla afflnls
MosqultofIsh (15-30 mg).
Gambusla afflnls
MosqultofIsh (adult)
(DDT-reslstant),
Gambusla afflnls
Mosqultof Ish (adult)
(DDT-susceptlble),
Gambusla afflnls
Guppy,
PoeclI la retlculata
Guppy (7 wk old),
PoeclI la retlculata
Green sunfish
(DDT-susceptlble),
Lepomls cyanelI us
Green sunfish
(DDT-reslstant),
Lepomls cyanelI us
Green sun fish,
Lepomls cyanelI us
Blueglll,
Lepomls macrochlrus
Chemical Duration Effect
Technical 48 hr LC50
Technical 48 hr
Technical
Analytical
Analytical
Technical
Technical
Technical
24 hr
24 hr
48 hr
Analytical 48 hr
72 hr
24 hr
48 hr
48 hr
24 hr
24 hr
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Result
(ng/L)
48
199
140
1,400
390
950
350
610
29
80
45
207
Reference
Culley and Ferguson 1969
Culley and Ferguson 1969
Ahmed and Wash I no 1977
Krleger and Lee 1973
Chambers and Yarbough 1974
Chambers and Yarbough 1974
Nagasawa et al. 1968
Chen et al. 1971
Mlnchew and Ferguson 1970
275 Mlnchew and Ferguson 1970
155 Gibson 1971
141 Gibson 1971
-------
Table 5. (continued)
Species
Bluegll 1,
Lepomls macrochlrus
Largemouth bass,
Mlcropterus sal mo Ides
Toad (larva),
Bufo bufo
Chemical Duration
Reagent 12 hr
18 hr
24 hr
29 hr
46 hr
70 hr
72 hr
24 hr
48 hr
Result
Effect
-------
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