United States Environmental Office of Water EPA-822-R-05-006
Protection Agency Office of Science and December 2005
Technology 4304T
Aquatic Life Ambient
Water Quality Criteria
Diazinon
FINAL
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EPA-822-R-05-006
Aquatic Life Ambient Water Quality Criteria
Diazinon
(CAS Registry Number 333-41-5)
FINAL
December 2005
U.S. Environmental Protection Agency
Office of Water
Office of Science and Technology
Washington, DC
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NOTICE
This document has been reviewed in accordance with U.S. EPA policy and approved for
publication. Mention of trade names or commercial products does not constitute endorsement or
recommendation for use.
This document can be downloaded from EPA's website at:
http://www.epa.gov/waterscience/criteria/aqlife.html
in
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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 which 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 on consideration of
comments received from independent peer reviewers and the public. 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 health or ecological
effects. Criteria presented in this document are such scientific assessments. If water quality
criteria associated with specific waterbody uses are adopted by a state or tribe as water quality
standards under section 303, they become enforceable maximum acceptable pollutant
concentrations in ambient waters within that state or tribe. Water quality criteria adopted in state
or tribal water quality standards could have the same numerical values as criteria developed
under section 304. However, in many situations states or tribes might want to adjust water
quality criteria developed under section 304 to reflect local environmental conditions and
exposure patterns. Alternatively, states or tribes 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 or tribal water quality standards that criteria
become regulatory. Guidelines to assist the states and tribes in modifying the criteria presented
in this document are contained in the Water Quality Standards Handbook (U.S. EPA 1994). The
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 final document is guidance only. It does not establish or affect legal rights or
obligations. It does not establish a binding norm and cannot 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.
Ephraim King, Director
Office of Science and Technology
IV
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ACKNOWLEDGMENTS
Document Authors
Larry T. Brooke
University of Wisconsin-Superior
Superior, WI
Gregory J. Smith
Great Lakes Environmental Center
Columbus, OH
Heidi Bell
Rick Stevens
Tala Henry
Walter Berry
Cindy Roberts
Robert Spehar
Thomas Steeger
Charles Stephan
Glen Thursby
U.S. EPA Document Coordinators
Office of Water
Office of Water
U.S. EPA Technical Reviewers
Office of Water
Office of Research and Development
Office of Research and Development
Office of Research and Development
Office of Prevention, Pesticides and Toxic Substances
Office of Research and Development
Office of Research and Development
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TABLE OF CONTENTS
NOTICE Hi
FOREWORD iv
ACKNOWLEDGMENTS v
FIGURES vii
TABLES vii
1. INTRODUCTION 1
1.1. Physical-Chemical Properties 1
1.2. Diazinon in the Environment 2
1.3. Toxicity of Diazinon 4
1.4. Derivation of Aquatic Life Ambient Water Quality Criteria 5
2. ACUTE TOXICITY TO AQUATIC ANIMALS 6
2.1. Freshwater 6
2.2. Saltwater 7
3. CHRONIC TOXICITY TO AQUATIC ANIMALS 9
3.1. Freshwater 9
3.2. Saltwater 11
3.3. Acute-Chronic Ratios 11
4. TOXICITY TO AQUATIC PLANTS 13
5. BIOACCUMULATION 14
6. OTHER DATA 15
6.1. Freshwater 15
6.2. Saltwater 20
6.3. Olfactory Effects of Diazinon in Aquatic Organisms 21
7. UNUSED DATA 23
8. SUMMARY 26
8.1. Freshwater Data 26
8.2. Saltwater Data 26
8.3. Plant Data 27
8.4. Bioaccumulation Data 27
9. NATIONAL CRITERIA 28
9.1. Freshwater 28
9.2. Saltwater 28
10. IMPLEMENTATION 29
11. REFERENCES 60
VI
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FIGURES
Page
Figure 1. Summary of Ranked Diazinon GMAVs (Freshwater) 30
Figure 2. Summary of Ranked Diazinon GMAVs (Saltwater) 31
Figure 3. Chronic Toxicity of Diazinon to Aquatic Animals 32
TABLES
Table 1. Acute Toxicity of Diazinon to Aquatic Animals 33
Table 2. Chronic Toxicity of Diazinon to Aquatic Animals 40
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios 42
Table 4. Toxicity of Diazinon to Aquatic Plants 46
Table 5. Bioaccumulation of Diazinon by Aquatic Organisms 47
Table 6. Other Data on Effects of Diazinon on Aquatic Organisms 48
vn
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1. INTRODUCTION
1.1. Physical-Chemical Properties
Diazinon [Chemical Abstract Service registry number 333-41-5; O,O-diethyl O-(6-methyl-
2-{l-methylethyl}-4-pirimidinyl) phosphorothioate] is a broad spectrum insecticide effective
against adult and juvenile forms of flying insects, crawling insects, acarians and spiders (WHO
1998). Specific uses include the control of pest insects such as cutworms, wireworms, and
maggots in soil (Farm Chemicals Handbook 2000) and ectoparasites on sheep (Virtue and
Clayton 1997). It is also effective against many pests of fruits, vegetables, tobacco, forage, field
crops, range, pasture, grasslands and ornamentals. Additional diazinon uses in urban areas
include dormant sprays on fruit trees, professional landscape and maintenance, and structural
pest control (Bailey et al. 2000). Until recently, most diazinon was used in and around the home
and in other non-agricultural settings including treatment of lawns, gardens, and ornamentals,
and indoor crack and crevice treatment. After December 31, 2004, it became unlawful to sell
outdoor, non-agricultural diazinon products in the United States (i.e., all residential uses of the
insecticide diazinon have been cancelled). However, it is lawful to use diazinon for non-
residential agricultural or other uses in accordance with product labeling and precautions
approved by EPA under the Federal Insecticide, Fungicide and Rodenticide Act.
Diazinon is an organophosphorus compound with the empirical formula of Ci2H2iN2O3PS,
a molecular weight of 304.35 g/mole and has a log octanol/water partition coefficient (log Kow)
of 3.40 (Hunter et al. 1985; WHO 1998). In its purest form diazinon is a colorless oil with a
density greater than water (1.116-1.118 g/mL at 20°C) and is soluble in water at 20°C to 0.006
percent (40 mg/L, Farm Chemicals Handbook 2000; 40.5 mg/L, Kanazawa 1983b; 60 mg/L,
WHO 1998). The technical product is a pale to dark brown liquid of at least 90 percent purity
and has a faint ester-like odor. Diazinon decomposes above 120°C (Verschueren 1983, WHO
1998), is susceptible to oxidation above 100°C, is stable in neutral media, but slowly hydrolyzes
in alkaline media and more rapidly in acidic media (WHO 1998). If stored properly, diazinon
has a shelf-life of at least three years (SOLARIS Consumer Affairs for Ortho products, P.O. Box
5008, San Ramos, CA 94583, 1998).
Commercial formulations of diazinon previously contained the impurity sulfotepp
(O,O,O,O-tetraethyl dithiopyrophosphate), but current diazinon formulations produced by
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Makhteshim - Agan of North America do not contain sulfotepp (personal communication,
Makhteshim - Agan of North America, 2004). Historically, sulfotepp was found at levels
ranging from 0.20 to 0.71 percent of the diazinon concentrations (Meier et al. 1979). Allender
and Britt (1994) conducted a screening program throughout Australia to determine the degree of
breakdown products in diazinon formulations. Of the 169 samples evaluated, eight contained the
degradates, O,S-TEPP and S,S-TEPP. The presence of the sulfotepp degradates was directly
correlated with the presence of water in the container. Sulfotepp is more stable than diazinon
and therefore should persist longer in the environment. It should be noted that sulfotepp is also
used alone as a pesticide, marketed under the trade names ASP-47 and Bladafun by the Bayer
Corporation for fumigation control in greenhouse crops and mushrooms (Agrochemicals
Handbook 1991).
1.2. Diazinon in the Environment
Diazinon has been detected in freshwater (Bailey et al. 2000; Domagalski et al. 1997; Land
and Brown 1996; Lowden et al. 1969; McConnell et al. 1998; Ritter et al. 1974).
Organophosphorus pesticides, including diazinon, were found in almost all samples of seawater,
but not in net plankton from the harbor of Osaka City, Japan (Kawai et al. 1984). Kawai et al.
(1984) reported diazinon was applied from June to August to rice paddy fields resulting in
concentrations in the Osaka City harbor greater than 0.1 ug/L.
Diazinon has been detected in point source (e.g., wastewater treatment plant effluents)
discharges (Villarosa et al. 1994). U.S. EPA's National Effluent Toxicity Assessment Center
investigated the occurrence of diazinon in 28 different publicly owned treatment works (POTW)
effluents located across the country in 1988. Detectable levels were found in samples from 17 of
the 28 facilities, primarily those located in southern states (Norberg-King et al. 1989). The
authors concluded that the diazinon levels found in several effluents were sufficiently high to be
a contributing factor to the toxicity observed to Ceriodaphnia dubia. The acute and chronic
toxicity of other POTW effluents to C. dubia has also been attributed, in part, to diazinon
(Amato et al. 1992; Bailey et al. 1997; Burkhard and Jensen 1993; Guinn et al. 1995).
Diazinon has also been detected in storm water runoff (non-point source) in urban and
agricultural areas (Bailey et al. 1997, 2000; Domagalski et al. 1997; Kratzer 1999; McConnell et
al. 1998; NCTCOG 1993; Waller et al. 1995). Domagalski et al. (1997) observed that in the
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western valley streams of the San Joaquin River, California, diazinon concentrations peaked
within hours of a rainfall event and decreased thereafter. Diazinon was also detected in air
samples over the Mississippi River from St. Paul to New Orleans, most likely related to use on
cropland within 40 km of the river (Majewski et al. 1998). Rainfall runoff of pesticides with
water solubility exceeding 10 mg/L, such as diazinon, can cause toxic additions to freshwater
ecosystems (Wauchope 1978). A study by Ritter et al. (1974) showed that the highest
concentration of diazinon measured in field runoff (82 ug/L), occurred after a storm event and
corresponded to 0.1% of the total amount of diazinon applied to the experimental watershed.
The mobility of diazinon in soil is influenced by the organic matter (OM) and carbonate
content of the soil (WHO 1998). Arienzo et al. (1994a,b) found that diazinon is slightly mobile
in soils with a low or medium (< 2 percent) OM content and immobile in those with high OM
content (> 2 percent). The sorption of diazinon to OM was enhanced when a sandy loam soil
was modified with different exogenous organic materials containing humic-like substances
relative to unmodified sandy loam soil (Iglesias-Jimenez et al. 1997).
Martinez-Toledo et al. (1993) found that the presence of 10 to 300 ug/g of diazinon in soil
increased the total number of bacteria and the population of denitrifying bacteria. However,
aerobic dinitrogen fixing bacteria numbers and dinitrogen fixation rate decreased initially (3
days) at diazinon concentrations of 100 to 300 ug/g before recovering to control levels.
Nitrifying bacteria and fungal soil populations were not affected by concentrations of 10 to 300
ug/g diazinon in soil.
The fate of diazinon in the aquatic environment is thought to be regulated by two main
processes - chemical hydrolysis and microbial degradation. Both processes are influenced by the
conditions of pH, temperature and the organic content of the water. Diazinon is stable at pH 7.0
and can persist in the environment for as long as six months. Ku et al. (1998b) found that
cleavage of the phosphorous-oxygen bond was the critical step in the hydrolysis of diazinon.
Diazinon half-life due to hydrolysis was 43.3 days in well water at pH 7.4 to 7.7 and 16°C
(Morgan 1976) and 171 days at pH 7.3 and 21°C (Mansour et al. 1999). Diazinon, unlike other
organophosphorus insecticides, hydrolyzes under both acidic and alkaline pH conditions (Gomaa
et al. 1969). In the laboratory at 20°C the half-life was determined to be 12, 4436 and 146 hr at
pH 3.1, 7.4 and 10.4, respectively (Faust and Gomaa 1972). Parkhurst et al. (1981) measured a
degradation rate of two percent per day and a half-life of 39 days in diazinon treated river water
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at summer temperatures. The breakdown of diazinon in soils of flooded rice fields occurs at
similar rates as in water and is described in a review by Sethunathan (1973).
A less dominant process influencing the fate of diazinon in aquatic systems is
photodegradation. Scheunert et al. (1993) found that when diazinon solutions were irradiated
with UV light of different wave lengths, photodegradation was greater in river or lake water than
in distilled water. Medina et al. (1999) compared the half-life of diazinon in filtered Limon
River samples under light and dark conditions and found that sunlight exposed samples had a
shorter half-life (ti/2 = 31.13 days) than samples held in the dark (ti/2 = 37.19 days).
An important factor regulating the rate of microbial decomposition of diazinon is adaptation
of microbes to the chemical. Microbes exposed repeatedly to diazinon had a markedly increased
capacity to degrade diazinon compared to microbes exposed once to diazinon (Sethunathan and
MacRae 1969; Sethunathan and Pathak 1972; Forrest et al. 1981).
1.3. Toxicity of Diazinon
A primary mode of toxicity of organophosphorus insecticides is inhibition of
cholinesterases present in the nervous system. Like most organophosphorous pesticides,
oxidative desulfuration of diazinon to diazoxon results in greater anticholinesterase activity (Hill
1995). Margot and Gysin (1957) have reported that the cholinesterase inhibiting activity of
diazoxon is about 4,000 times greater than that of the parent diazinon. Diazoxon has been
identified as a metabolite of diazinon in the liver microsomes of channel catfish, Ictalurus
punctatus, and bluegill, Lepomis macrochirus (Hogan and Knowles 1972). Insect enzymes
efficiently convert diazinon to the toxic oxygen homolog, diazoxon (Albert 1981). Crustacea
very likely have similar ability to metabolize organophosphates. Insects and Crustacea are
generally more sensitive to organophosphorous insecticides than vertebrates, presumably due to
less efficient detoxification of diazoxon by the invertebrates.
Diazinon, on prolonged storage, may become more toxic due to transformation products.
Monosulfotepp was shown to be 14,000 times more potent than diazinon in a test of enzyme
inhibition (Singmaster 1990). The use of an improperly stored diazinon formulation in which
diazinon had transformed into the more toxic products sulfotepp and monothiono-tepp, was cited
by Soliman et al. (1982) as the most probable cause of two acute human poisoning cases in
Egypt. Sulfotepp has been reported to be 58 times more toxic to fathead minnows (Pimephales
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promelas), 75 times more toxic to bluegill (Lepomis macrochirus) and rainbow trout
(Oncorhynchus mykiss), and 8.7 times more toxic to a cladoceran (Daphnia magna) than
diazinon (Meier et al. 1979). The authors speculated that some of the toxicity attributed to
diazinon is likely due to sulfotepp, which is no longer in commercial formulations of diazinon.
1.4. Derivation of Aquatic Life Ambient Water Quality Criteria
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), hereafter
referred to as the Guidelines, is necessary to fully understand the text, tables, and calculations
presented in this criteria document. Results of intermediate calculations are presented to four
significant figures to prevent round-off error in subsequent calculations, not to reflect the
precision of the value. Final criteria values are presented to two significant figures.
The latest comprehensive literature search for information used in developing this document
was conducted in November 1999. An additional literature search, limited to identifying
information regarding diazinon effects on olfaction, was conducted in 2004. Data in the files of
the U.S. EPA's Office of Pesticide Programs concerning the effects of diazinon on aquatic
organisms have also been evaluated in deriving the aquatic life criteria for diazinon.
Whenever adequately justified, a national criterion may be replaced by a site-specific
criterion (U.S. EPA 1983), which may include not only site-specific criterion concentrations
(U.S. EPA 1994), but also site-specific averaging periods and frequencies of allowed excursions
(U.S. EPA 1991).
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2. ACUTE TOXICITY TO AQUATIC ANIMALS
2.1. Freshwater
The acute toxicity of diazinon to freshwater animals has been determined for 13
invertebrate species, 10 fish species and one amphibian species (Table 1). Acute toxicity values
ranged from 0.25 ug/L for the cladoceran, Ceriodaphnia dubia (Norberg-King 1987), to 11,640
ug/L for planaria, Dugesia tigrina (Phipps 1988). The most sensitive organisms tested were
invertebrates in the Class Crustacea. The cladoceran, C. dubia., had the lowest Genus Mean
Acute Value (GMAV) which was calculated from 14 tests (0.3773 ug/L; Table 3), ten of which
were conducted by the U.S. EPA's Office of Research and Development (Norberg-King 1987;
Ankley et al. 1991). Results from these 14 tests were relatively consistent (acute values ranged
from 0.25 to 0.59 ug/L) considering that different water sources were used and organism age at
test initiation ranged from < 6 hr-old to < 48 hr-old. C. dubia data were included in Table 1
when the organisms received food during the exposure, but these data were not used to calculate
the Species Mean Acute Value (SMAV), as per the Guidelines (Stephan et al. 1985). Three
other cladoceran species (Daphniapulex, Daphnia magna, and Simocephalus serrulatus) were
tested and their sensitivity to diazinon found to be similar to that of C. dubia with ECSOs ranging
from 0.65 to 1.8 ug/L. The toxicity of diazinon to three species of amphipods (Gammarus
faciatus, Gammaruspseudolimneaus, and Hyallela aztecd) was tested, and the 96-hr LCSOs
ranged from 2.04 to 16.82 ug/L. Toxicity test data were available for two insect species. LCSOs
of 10.7 ug/L for the midge, Chironomus tentans, and 25 ug/L for the stonefly, Pteronarcys
californica, were reported. These data show that insect sensitivity to diazinon toxicity is in the
same range as amphipods.
The least sensitive species tested with diazinon was also an invertebrate. The planarian,
Dugesia tigrina, had the highest observed diazinon 96-hr LC50 of 11,640 ug/L. Other
invertebrate species exhibiting relatively low sensitivity to diazinon included the snail, Gillia
altilis (96-hr LC50 of 11,000 ug/L), the oligochaete worm, Lumbriculus variegatus (individual
test 96-hr LC50 values of 9,980 and 6,160 ug/L, and SMAV of 7,841 ug/L) and the apple snail,
Pomaceapaludosa (individual test 96-hr LC50 values of 2,950, 3,270 and 3,390 ug/L and
SMAV of 3,198 ug/L).
The only amphibian toxicity test available was for the green frog, Rana clamitans. The frog
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embryos were exposed to three concentrations of diazinon (0.5, 5.0 and 50 ug/L). The 96-hr
LC50 was reported as > 50 ug/L (Harris et al. 1998).
Freshwater fish species that were tested showed moderate sensitivity to diazinon. SMAVs
ranged from 425.8 ug/L for the rainbow trout, Oncorhynchus mykiss, to 9,000 ug/L for the
goldfish, Carassius auratus (Table 1). Diazinon toxicity to rainbow trout was evaluated in five
tests with LC50 values ranging from 90 ug/L (Cope 1965b; Ciba-Geigy 1976; Johnson and
Finley 1980; Mayer and Ellersieck 1986) to 3,200 ug/L (Bathe et al. 1975a). The cutthroat trout,
Oncorhynchus clarki, was generally less sensitive (SMAV = 2,166 ug/L) to diazinon than
rainbow trout (SMAV = 425.8 ug/L). Certain species of warmwater fish, flagfish (Jordanella
floridae\ fathead minnow (Pimephalespromelas\ goldfish (Carassius auratus), and zebrafish
(Danio rerio; formerly Brachydanio rerio) are less sensitive to diazinon than the coldwater
species, rainbow trout, brook trout (Salvelimisfontinalis), and lake trout (Salvelinus namaycush).
Two exceptions include the warmwater bluegill, which is more sensitive to diazinon than the
coldwater fish species, and the coldwater cutthroat trout, which is less sensitive than the
warmwater flagfish. For the four most sensitive genera, all crustaceans, the GMAVs differed by
a factor of 15.5 (Table 3 and Figure 1). Based on available data for freshwater organisms, as
summarized in Table 1, the freshwater Final Acute Value (FAV) is 0.3397 ug/L.
2.2. Saltwater
The acute toxicity of diazinon to saltwater animals has been determined for 7 invertebrate
species and 2 fish species (Table 1). SMAVs ranged from 2.57 ug/L for the copepod, Acartia
tonsa (Khattat and Farley 1976), to > 9,600 ug/L for embryos of the sea urchin, Arbacia
punctulata (Thursby and Berry 1988), which is a difference among species of >3,735-fold.
Acute values for the mysid, Americamysis bahia (formerly Mysidopsis bahid), determined from a
renewal, unmeasured test (8.5 ug/L) were approximately two-fold higher than those determined
from a flow-through measured test (4.82 ug/L). Acute toxicity test data available for other
saltwater invertebrates include an annelid worm (Neanthes arenaceodentata), an amphipod
(Ampelisca abditd), and two species of shrimp, grass shrimp (Palaemonetespugio) and pink
shrimp (Penaeus duoraruni) (Table 1). The saltwater fish, inland silverside (Menidia beryllina),
was relatively insensitive to diazinon with a LC50 of 1,170 ug/L. The remaining fish species,
the sheepshead minnow (Cyprinodon variegatus), had an LC50 value of 1,400 ug diazinon/L,
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and is the only saltwater fish with a corresponding chronic value. Acute values for the four most
sensitive genera, all invertebrates, differed by only a factor of 2.6 (Table 3 and Figure 2). Based
on available data for saltwater organisms, as summarized in Table 1, the saltwater Final Acute
Value (FAV) is 1.637ug/L.
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3. CHRONIC TOXICITY TO AQUATIC ANIMALS
3.1. Freshwater
The chronic toxicity of diazinon was determined for 4 freshwater species, 3 fish and 1
invertebrate (Table 2). A life-cycle test consisting of a 7-day exposure period was conducted
with C. dubia (Norberg-King 1987). Diluted mineral reconstituted water was used to culture and
expose the organisms. All organisms survived in the control and the three lowest diazinon
exposures (0.063, 0.109, and 0.220 ug/L). There also was no effect on reproduction in the three
lowest diazinon exposures. No organisms survived at diazinon concentrations > 0.520 ug/L.
The chronic value for C. dubia was 0.3382 ug/L. Dividing the acute value derived from ten 48-
hr acute tests (0.3760 ug/L; Table 1) conducted in the same laboratory with the same dilution
water (Norberg-King 1987; Ankley et al. 1991) by the chronic value (0.3382 ug/L; Table 2)
results in an Acute-Chronic Ratio (ACR) of 1.112 for C. dubia (Table 2).
Allison and Hermanutz (1977) conducted a partial life-cycle test with brook trout,
Salvelinusfontinalis. The test began with yearlings, which were exposed for 173 days to
measured concentrations ranging from 0.55 to 9.6 ug/L. Each replicate was thinned to two males
and four females, and exposure continued during spawning for an additional two months, during
which time eggs were collected and viability (% hatch) determined. Larvae were thinned to 25
per chamber and exposure continued for 122 additional days. Average measured concentrations
during egg viability and larval growth periods ranged from 0.8 to 11.1 ug/L. After 173 days,
survival of parental stock was significantly reduced at 9.6 ug/L, but not at 4.8 ug/L. However,
some deformities were seen and the instantaneous growth rate was reduced by 4.8 ug/L diazinon.
The authors state that high within-treatment variance in egg viability prevented any accurate
analysis of egg production, egg viability or hatch, but there were viable eggs produced at every
concentration. Brook trout progeny from the 122 day larval exposure showed some measurable
effects after 30 days. At 122 days post-hatch, fish in all exposure concentrations had average
weights significantly less than the control fish. The chronic value for this species is < 0.8 ug/L,
which is the lowest exposure concentration for the progeny in which growth effects were
observed. Dividing the acute value (723.0 ug/L; Table 1) calculated from three 96-hr acute tests
(Allison and Hermanutz 1977) by the chronic value (< 0.8 ug/L; Table 2) results in an ACR of >
903.8 for brook trout (Table 2).
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Norberg-King (1989) exposed fathead minnow embryos and the resulting larvae to diazinon
for 32 days in an early-life stage test. At test termination, wet weight and survival offish
exposed to only the highest exposure concentration (285 ug/L) were significantly different from
that of the control fish. Total length was significantly affected at concentrations > 60 ug/L and
dry weight was significantly reduced at 37.8 ug/L, but not at 16.5 ug/L. Based on reduced dry
weight, the chronic value for the test was 24.97 ug/L. Dividing the acute value (9,350 ug/L;
Table 1), determined by another group of researchers (University of Wisconsin-Superior 1988) at
the same laboratory using the same water supply and the same genetic stock offish, by the
chronic value (24.97 ug/L; Table 2) results in an ACR of 374.4 for fathead minnow (Table 2).
In another test, fathead minnow embryos (< 24-hr old) and the resulting larvae were
exposed to diazinon for a total of 32 days (Jarvinen and Tanner 1982). Results of the early-life
stage test were reduced survival at diazinon concentrations > 290 ug/L and reduced weight
(10.1% reduction) at 90 ug/L, but no weight difference from the control fish at 50 ug/L. Based
on reduced weight, the chronic value for the test was 67.08 ug/L. Dividing the acute value
(6,900 ug/L), determined from a flow-through test in which toxicant concentration was measured
(Jarvinen and Tanner 1982; Table 1), by the chronic value (67.08 ug/L; Table 2) results in an
ACR of 102.9 for fathead minnow. Calculating the geometric mean of the two ACRs for fathead
minnow (374.4 and 102.9) results in a species mean acute-chronic ratio (SMACR) of 196.3 for
the fathead minnow (Table 2).
The flagfish, Jordanellafloridae, was expsosed to diazinon in a life-cycle test (Allison
1977). The study began with one-day-old larvae and continued through spawning, which
occurred at about 60 days, and then continued with the fish progeny for 35 days post-hatch. The
only significant effect on the parental stock was a reduction (23.3%) in the average wet weight of
the male fish after 61 days of exposure to 88 ug/L diazinon. This effect is based on only two fish
per replicate because the fish were culled to two males and five females per treatment (from 30
fish per treatment at start of test) prior to spawning. Weight of the female fish was not
significantly different from controls at any exposure concentration although there was a 21.4%
reduction in the average weight of female fish exposed to 88 ug/L diazinon. There was a
significant reduction in percent hatch at diazinon concentrations of 88 ug/L. Average weight at
35 days post-hatch was significantly reduced in the two lower diazinon exposure groups (14 and
26 ug/L), but not in the two higher diazinon exposure groups (54 and 88 ug/L), hence, a dose-
10
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dependent effect on this endpoint was not observed. The chronic value for flagfish, based on
hatch success, is the geometric mean of 54 ug/L (NOEC) and 88 ug/L (LOEC), or 68.93 ug/L.
Dividing the acute value (1,643 ug/L; Table 1), which is the geometric mean of results from two
tests conducted in the same water supply and using fish from the same culture as used in the
chronic test (Allison and Hermanutz 1977), by the chronic value (68.93 ug/L; Table 2) results in
an ACR of 23.84 for the flagfish (Table 2).
3.2. Saltwater
The chronic toxicity of diazinon to saltwater organisms has been determined in a life-cycle
test with the mysid, A. bahia, and a partial life-cycle test with the sheepshead minnow (Table 2).
The mysid test (Nimmo et al. 1981) was of 22 days duration, and the authors' original data was
used to recalculate the chronic limits (Berry 1989). There was no statistical difference in
survival observed at any of the concentrations tested (0.54, 1.2, 2.1, 4.4 ug/L). The number of
young per female was not significantly reduced relative to controls at diazinon concentrations <
2.1 ug/L. There were no young produced by females exposed to the highest concentration tested
(4.4 ug/L). Based on reproduction, the chronic value for the mysid is the geometric mean of the
chronic limits, 2.1 and 4.4 ug/L, or 3.040 ug/L. Dividing the acute value (4.82 ug/L; Table 1),
determined by the same authors (Nimmo et al. 1981), by the chronic value (3.040 ug/L) results in
an ACR of 1.586 for the mysid, A. bahia (Table 2).
Sheepshead minnow, Cyprinodon variegates., reproduction was significantly reduced in all
diazinon exposure concentrations during a partial life-cycle test (Goodman et al. 1979). The
number of eggs spawned per female in the 0.47, 0.98, 1.8, 3.5 and 6.5 ug/L (average measured)
diazinon concentrations were 69, 50, 50, 55 and 45 percent of control fish, respectively. Neither
survival nor growth was affected by diazinon exposures < 6.5 ug/L. Based on reduction of eggs
spawned, the chronic value for sheepshead minnow is < 0.47 ug/L (Table 2). Dividing the acute
value (1,400 ug/L; Table 1) determined by the same authors (Goodman et al. 1979) by the
chronic value (< 0.47 ug/L) results in an ACR of > 2,979 for sheepshead minnow.
3.3. Acute-Chronic Ratios
Chronic toxicity tests have been conducted on six aquatic species and chronic values ranged
from 0.3882 ug/L for Ceriodaphnia, C. dubia, to 68.93 ug/L for flagfish (Table 2). The chronic
11
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values for brook trout (< 0.8 ug/L) and sheepshead minnow (< 0.47 ug/L) cannot be determined
accurately because all concentrations tested affected reproduction and growth. Acute-chronic
ratios for acutely sensitive crustacean invertebrates were 1.586 for mysids and 1.112 for C. dubia
(Table 2). In contrast, ratios are markedly higher for relatively acutely insensitive fishes: 23.84
for flagfish, 102.9 and 374.4 for fathead minnow (Pimephales promelas), > 903.8 for brook trout
(Salvelinus fontinalis), and > 2,979 for sheepshead minnow.
The Guidelines (Stephan et al. 1985) specify that if the species mean acute-chronic ratio
(SMACR) seems to increase or decrease as the SMAV increases, the Final Acute-Chronic Ratio
(FACR) should be calculated as the geometric mean of the ACRs for species whose SMAVs are
close to the FAV. It does appear that ACR values are lower for species acutely sensitive to
diazinon and higher for acutely insensitive species (Table 3). Therefore, only the acutely
sensitive C. dubia and A. bahia ACRs were used to calculate the FACR of 1.328. The
Guidelines also stipulate that if the most appropriate SMACRs are less than 2.0, acclimation has
probably occurred during the chronic test and the FACR should be assumed to be 2.0. The low
ACRs for C. dubia and A bahia support the finding that diazinon toxicity is rapid for these
sensitive invertebrates and extended periods of exposure do not increase toxicity for these
sensitive species. Thus, the FACR for diazinon is 2.0. The Final Chronic Values (FCV) for
freshwater and saltwater are 0.1699 and 0.8185 ug/L, respectively (FAVs divided by 2.0). Use
of an FACR of 2.0 results in the same value for the Criteria Maximum Concentration (CMC;
acute criterion) and the Criteria Continuous Concentration (CCC; chronic criterion).
It appears from available data that the freshwater Final Chronic Value will protect the tested
freshwater species against adverse effects due to diazinon (Figure 3). Growth of offspring of
exposed brook trout, a recreationally important freshwater fish species, was statistically
significantly reduced by 40% at the lowest tested concentration of 0.8 ug/L, which is a factor of
4.7 times the CCC. However, the chronic value for this study is a less than value and it is
uncertain how close to the freshwater CCC adverse effects may occur. Reproduction of the
saltwater sheepshead minnow was statistically significantly reduced by 31% at the lowest tested
concentration of 0.47 ug/L, which is below the saltwater CCC. Therefore, where exposure to
diazinon at or near CCC levels may occur to this or similar saltwater fish species, states and
tribes may want to consider site-specific criteria derivations for diazinon.
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4. TOXICITY TO AQUATIC PLANTS
Acceptable data on the effects of diazinon to freshwater algae (nonvascular plant) are
available for one species (Table 4), but no acceptable data are available regarding the toxicity to
freshwater vascular plants. Hughes (1988) exposed the green alga, Selenastrum capricormitum,
for seven days in a static test. A 7-day EC50 of 6,400 ug/L (measured concentration) was
determined based on reduced cell numbers. No saltwater tests with plants are suitable, according
to the Guidelines, for inclusion in this section. Some additional freshwater and saltwater plant
toxicity information is included with "Other Data." Based on a single aquatic plant test, the
Final Plant Value for diazinon is 6,400 ug/L.
13
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5. BIOACCUMULATION
Three freshwater species offish, rainbow trout (Oncorhynchus mykiss), carp (Cyprinus
carpio) and guppy (Poecilia reticulatd), were exposed to diazinon for 14 days and the whole
body tissue concentrations were determined (Seguchi and Asaka 1981; Keizer et al. 1993).
Diazinon accumulated rapidly in the fish and reached steady-state in approximately three days.
The bioconcentration factor (BCF) for rainbow trout and carp exposed to 15 ug diazinon/L was
62 and 120, respectively (Table 5). The half-life for diazinon in these fish was less than seven
days. The BCF for guppy exposed to 350 ug diazinon/L was 188 (Keizer et al. 1993).
In a 108-day saltwater exposure, uptake of diazinon by the sheepshead minnow was rapid,
reaching steady state within 4 days (Goodman, et al. 1979). Whole body (less brain)
bioconcentration factors for fish exposed to 1.8, 3.5 and 6.5 ug/L were 147, 147 and 213,
respectively (Table 5).
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6. OTHER DATA
6.1. Freshwater
Additional data on lethal and sublethal effects of diazinon on freshwater species are
presented in Table 6. Sewage microbes (Bauer et al. 1981) and actinomycete bacteria
(Sethunathan and MacRae 1969) appear to be unaffected or have growth enhancement at
diazinon concentrations near water saturation.
Sensitivity to diazinon varies greatly among green plants and diatoms tested. The green
algal (non-vascular plant) species, Chlorella ellipsoidea and Chlamydomonas sp., were affected
only at concentrations of 100,000 ug/L. The green algae Scenedesmus quadricauda was not
affected at 1,000 ug/L (Stadnyk and Campbell 1971), but a mixture of green alga and diatoms
had reduced growth at < 10 ug/L (Butler et al. 1975a). Exposure of the vascular plant, duckweed
(Wolffiapapulifera), to diazinon for 11 days resulted in 100 percent mortality at 100,000 ug/L
saturation and deformities at 10,000 ug/L (Worthley and Schott 1971).
Various species of protozoans and invertebrates have been tested and found to have
relatively low sensitivity to diazinon compared to crustacean and vertebrate species. Adverse
affects were reported for protozoans at approximately 3,000 ug/L (Evtugyn et al. 1997). The
rotifer, Brachionus calyciflorus, was found to be substantially less sensitive than cladocerans and
insects to diazinon with respect to survival (24-hr LC50 = 29,220 ug/L), filtration and ingestion
rates (50 percent reduction at 14,000 ug/L), reproduction (decreased reproduction at < 5,000
ug/L), and median time to lethal effects (LT50 values ranged from 2.5 to 4 days for 14,000 and
5,000 ug/L, respectively) (Fernandez-Casalderrey 1992a,b,c,d). Juchelka and Snell (1994)
estimated a 48-hr no effect concentration (NOEC) for ingestion rate of 20,000 ug/L and Snell
and Moffat (1992) calculated a NOEC for reproduction of 8,000 ug/L for B. calyciflorus.
Charter]ee and Konar (1984) determined a 96-hr LC50 of 2,220 ug/L for the tubificid worm,
Branchiura sowerbyi. Rogge and Drewes (1993) determined that 20,000 ug/L diazinon was
lethal to the oligocheate worm, Lumbriculis variegatus, in 4 hours. A snail species (Physa
acutd) had a 48-hr LC50 of 4,800 ug/L (Hashimoto and Nishiuchi 1981) which is near the upper
end of the range offish 96-hr LCSOs.
Dortland (1980) conducted a series of tests with the cladoceran, Daphnia magna, and found
in one exposure that 0.2 ug/L did not affect the organisms during the 21-day exposure, but 0.3
15
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ug/L reduced reproduction and mobility. In four other 21-day tests in which the D. magna were
fed, ECSOs ranged from 0.22 to 0.8 ug/L. In 21-day renewal tests with/), magna, Fernandez-
Casalderrey et al. (1995) determined survival NOEC and LOEC of 0.15 ug/L and 0.18 ug
diazinon/L (unmeasured concentrations), respectively. The mean total young per female (which
was slightly less than that required by the ASTM test method) and mean brood size were both
significantly reduced at the lowest exposure concentration (0.15 ug/L) when compared to the
controls. A 24-hr LC50 of 0.86 ug/L for D. magna (unfed during test) was reported by the same
authors. Sanchez et al. (1998, 1999 and 2000) reported chronic effects of diazinon toD. magna
in a series of tests to evaluate the toxicity of this pesticide over several generations. Test
solutions (which were reported mistakenly as ng/L instead of ug/L), were measured initially, but
not thereafter during each test. Although test solutions were renewed daily, dissolved oxygen
concentrations were not reported. The lowest test concentration (0.05 ug/L) significantly
reduced survival, growth and the number of young per female of the parental generation (Fo)
(Sanchez et al. 1998). The progeny (first and third broods), which were transferred to clean
water in separate 21-day tests (Sanchez et al. 1999), showed similar responses to that of control
animals, indicating that diazinon was being eliminated after parental exposure. However,
adverse effects to progeny (first and third broods) that were continually exposed to the same test
solutions as the parental generation for an additional 21-days were observed at the lowest tested
concentration (0.05 ug/L) (Sanchez et al. 2000). A test in which D. magna were exposed to an
insecticidal soap formulation of diazinon yielded similar results with a 48-hr LC50 of 0.74 ug/L
and a 96-hr LC50 of 0.21 ug/L (Nishiuchi and Hashimoto 1967 and Hashimoto and Nishiuchi
1981).
Amphipods are generally very sensitive to diazinon toxicity. Collyard et al. (1994)
compared the sensitivity of different H. azteca age groups to diazinon. The eight different age
groups (0-2 to 24-26 days old at test initiation) had very similar 96-hr LC50 values that ranged
from 3.8 to 6.2 ug/L. Werner and Nagel (1997) tested adultHyallela azteca and reported an
LC50 of 19 ug/L for this life stage.
Mosquito larvae appear to be about as sensitive to diazinon as cladocerans and amphipods.
Yasuno and Kerdpibule (1967) exposed mosquito larvae (4th instar), Culexpipiensfatigans, to
diazinon for 24 hr and measured LCSOs ranging from 1.8 to 5.7 ug/L. Chen et al (1971) reported
24-hr LCSOs of 61-350 ug/L for younger life stages (3^-4* instar) of the same species. Klassen
16
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et al (1965) found the mosquito species, A. eqyptii, to be less sensitive (24-hr LC50 = 350 ug/L)
than Culexpipiens fatigans. Caddisfly larvae exposed to diazinon for 6 hr had highly variable
LCSOs, ranging from 500 to 2,500 ug/L for Hydropsyche morosa and > 500 u/L for H. recurvata
(Fredeen 1972). The EC50 for a species of stonefly, Pteronarcys californicus, exposed to
diazinon for 48 hr was reported as 74 ug/L (Cope 1965a).
Rainbow trout fingerlings were exposed to diazinon concentration of 8, 40 and 200 ug/L
(unmeasured) under flow-through conditions for 28 days (Bresch 1991). Survival and growth of
rainbow trout in the three treatment groups after 28 days were not statistically (p > 0.05)
different from the control group. The chronic value for rainbow trout in this test was > 200 ug/L
diazinon. Rainbow trout were also exposed to an insecticidal soap formulation of diazinon for
96 hr (Mitchell 1985) and an unspecified form of diazinon for 48 hr (Cope et al 1965a), and the
LCSOs determined were 20 ug/L and 170 ug/L, respectively. Cutthroat trout of two sizes were
exposed to an unspecified formulation of diazinon for 96 hr and LCSOs of 3,850 ug/L for the
smaller fish and 2,760 ug/L for the larger fish determined (Swedberg 1973). The LCSOs for
rainbow trout and cuttthroat trout were consistent with the values used in Table 1 for the same
species. Brown trout, Salmo trutta lacustris, were also relatively sensitive to diazinon having a
96-hr LC50 value of 602 ug/L for an unspecified formulation of diazinon (Swedberg 1973).
Carp and goldfish are relatively tolerant of diazinon in acute exposures with 48-72 hr LCSOs
ranging from 1420 ug/L (carp) to 5100 (goldfish) ug/L (Table 6). Diazinon (technical grade)
was toxic to newly hatched fathead minnow larvae at seven- and twelve-days exposure (Table 6),
but the sensitivity increased as the exposure was continued to 32-days (Table 1) (Norberg-King
1989). The more sensitive timepoint was used in calculating the criteria.
Jarvinen and Tanner (1982) exposed fathead minnows to an encapsulated formulation of
diazinon in acute and chronic exposures. The encapsulated formulation was less acutely toxic
(5,100 and 6,100 ug/L; Table 6) than the technical grade (2,100 and 4,300 ug/L; Table 1)
following 96-hr exposures. Exposure of embryo-larval stage fathead minnows for 32 days to the
encapsulated formulation resulted in a chronic value of 55.14 ug/L. Dividing the acute value by
the chronic value results in an ACR for the encapsulated formulation of 101.6, which is
comparable to the ACR of 102.9 for the technical grade chemical (Table 2). Ciba-Geigy (1976)
reported 96-hr LCSOs of 8,000 ug/L and 150 ug/L for catfish (Ictalurus sp.) and Ide (Leucisuc
idus) respectively, exposed to diazinon as an emulsifiable concentrate (60%).
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Flagfish, J.floridae, have been exposed in a 21-day pulsed dose exposure with diazinon
followed by a period without the chemical to observe effects (Allison 1977). Exposure of the
parental stock beginning at hatch and lasting 21 days resulted in decreased egg production by the
females at concentrations > 290 ug/L. Exposure to diazinon for 21 days just prior to spawning
resulted in decreased parental survival at concentrations > 250 ug/L, but there were no effects on
reproduction at the 250 and 450 ug/L exposure concentrations. Exposure of adults to diazinon
for 21 days once spawning had initiated resulted in decreased survival of the parents at the
highest exposure concentration (1,170 ug/L) and reduced survival of larval progeny at 1,170
ug/L.
Chen et al. (1971) exposed the guppy, P. reticulata, to diazinon and measured 24-hr LCSOs
of 3,700 and 3,800 ug/L. These values were in agreement with the work of Ciba-Geigy (1976)
which measured a 96-hr LC50 of 3,000 ug/L for the same fish species. Ohayo-Mitoko and
Deneer (1993) estimated a lethal body burden of 2,495 ug diazinon/L for the guppy. Relative to
some other fish species, the guppy appears to be more tolerant of diazinon than trout species but
less tolerant than tested cyprinid species (fathead minnow and goldfish).
Bluegill, L. macrochims, was tested by two research groups with widely different results
(Table 6). The results of Cope (1965a) indicate that the bluegill is a relatively sensitive species
(48-hr EC50 = 30 ug/L), whereas the work of Li and Chen (1981) indicate intermediate
sensitivity (48-hr LC50 = 1,493 ug/L) relative to other fish species.
Bresch (1991) evaluated the toxicity of diazinon to zebrafish in an early life-stage test.
Zebrafish were exposed to diazinon from egg stage (approximately 2-3 hr after spawning)
through juvenile stage to diazinon concentrations of 8, 40 and 200 [j, g/L (unmeasured) for 42
days under flow-through conditions. Survival and growth in the three treatment groups were not
statistically different (p > 0.05) from the controls. Thus, the zebrafish chronic value was > 200
ug/L.
Bioconcentration factors were determined for various aquatic species with a value of 4.9 for
the crayfish, Procambarus clarkii (Kanazawa 1978), 17.5 for the guppy (Kanazawa 1978), 28 for
oriental weatherfish, Misgurnus anguillicaudatus (Seguchi and Asaka 1981), 62 for rainbow
trout (Seguchi and Asaka 1981), and for carp 20.9 (Tsuda et al. 1990), 65.1 (Kanazawa 1978)
and 120 (Seguchi and Asaka 1981).
Outdoor experimental channels at EPA's Monitcello Ecological Research Station
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(Mississippi River water) were used by Arthur et al. (1983) to evaluate the effects of diazinon on
macroinvertebrates. One channel served as a control and two other channels as low and high
treatments. The low and high treatment channels were continuously treated to achieve either 0.3
or 3 ug/L nominal diazinon concentrations for 12 weeks, then increased to 6 and 12 ug/L
nominal diazinon concentrations for four weeks, and finally the high treatment channel was
increased to 30 ug/L and the low treatment channel allowed to returned to ambient conditions.
Only the first 12 week dosing regime achieved nominal diazinon levels as indicated by analytical
measurements. During the latter two dosing regimes the channel water did not reach the
intended concentrations. No consistent interchannel differences were observed in total
macroinvertebrate abundance or in species diversity indices. Hyalella was the most sensitive
species in the test, exhibiting substantially higher (5 to 8 times) drift rates in the 0.3 ug/L
diazinon treated channel relative to the control channel, and had sharply reduced population
levels at diazinon concentrations of 5 ug/L. Macroinvertebrate tolerance to diazinon treatment
was observed as: flatworms, physid snails, isopods and chironomids (most tolerant); leeches and
the amphipod Crangonyx (less tolerant); the amphipod Hyalella, mayflies, caddisflies and
damselflies (least tolerant).
An aquatic pulsed exposure microcosm study was conducted with technical grade diazinon
by Giddings et al. (1996). The objectives of the study were to measure the effects of a range of
diazinon exposure regimes to many taxonomic groups under simulated field conditions and to
determine the relationship between the level of diazinon exposure and the magnitude of
ecological response. Eighteen fiberglass tanks, each 3.2 m in diameter and 1.5 m in depth, were
established with sediment and water (11.2 m3) from natural ponds and stocked with 40 juvenile
bluegill sunfish (L. macrochirus). Diazinon was applied in aqueous solution three times at 7-day
intervals. Eight loading rates were used, with two microcosms at each load rate plus two
controls. The amount of diazinon added during each application corresponded to nominal
concentrations ranging from 2.0 ug/L to 500 ug/L. The most sensitive ecological components of
the microcosms were zooplankton (Cladocera) and chironomid insects (Pentaneurini and
Ceratopogonidae), which were reduced at all treatment levels. Effects on many zooplankton and
macroinvertebrate taxa occurred at diazinon concentrations (time-weighted averages) of 9.2 ug/L
and higher. Total fish biomass was reduced at 22 ug/L and higher, and fish survival was reduced
at 54 ug/L and higher. Odonates, some dipterans, and plants were not adversely affected by
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diazinon at 443 ug/L, the highest concentration tested. Microcosm results were consistent with
laboratory toxicity data for some taxa (e.g., cladocerans, Ephemeroptera, and bluegill sunfish),
but differed substantially for others (e.g., rotifers, Chironomini, and odonates). The NOEC for
the microcosms study (70-d time-weighted average) was reported as 4.3 ug/L.
6.2. Saltwater
Other data on the lethal and sublethal effects of diazinon on saltwater species (Table 6) did
not indicate greater sensitivities than data represented in Tables 1 and 2. Saltwater algae appear
to be less sensitive to diazinon than most aquatic animals. Photosynthesis of natural
phytoplankton was essentially unaffected by a 4-hr exposure to 1,000 ug/L diazinon (Butler
1963). There was no effect of diazinon at 1,000 ug/L on sexual reproduction of the red alga,
Champia parvula (Thursby and Tagliabue 1988). A 24-hr exposure of the red alga, Chondrus
crispus, to 10,000 ug/L diazinon had no effect on the growth of the alga in a subsequent 18-day
grow-out period (Shacklock and Croft 1981). Rotifers, Brachionisplicatilis, were also not
acutely sensitive to diazinon (Thursby and Berry 1988; Guzzella et al 1997). No effect on
growth of eastern oysters, Crassostrea virginica, was observed following a 96-hr exposure to
1,000 ug/L diazinon (Butler 1963), however, an LC50 of 1,115 ug/L was reported by Williams
(1989). Shacklock and Croft (1981) reported that two days after a 3-hr exposure to 1,000 ug/L
diazinon, mortality of the saltwater snail, Lacuna vincta, test organisms was 88% whereas
mortality of the amphipod, Gammarus oceanicus, and the isopod, Idotea baltica, was 100%.
Longer exposure (48-hr) of the adult amphipods, Ampelisca aldita and Rheopoxynius abronius,
resulted in LC50 values of 10 and 9.2 ug/L, respectively. The brown shrimp, Penaeus aztecus,
had a 24-hr EC50 of 44 ug/L (Butler 1963) and a 48-hr EC50 of 28 ug/L (Mayer 1987).
Similarly, an acute (48-hr) EC50 of 28 ug/L has been reported for for grass shrimp,
Palaemonetespugio (Mayer 1987). The 24- and 48-hr LCSOs for the white mullet, Mugil
curema, were both 250 ug/L (Butler 1963) and the 48-hr LC50 for striped mullet, Mugil
cephalus., was 150 ug/L (Mayer 1987). In the partial life-cycle test conducted with sheepshead
minnow by Goodman et al. (1979), acetylcholinesterase activity in fish exposed to 0.47 ug/L
diazinon were consistently less than control fish activity and averaged 71% inhibition in the fish
exposed to 6.5 ug/L diazinon. A BCF of 56 was reported for Eastern oyster exposed to diazinon
for 5 days (Williams 1989).
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6.3. Olfactory Effects of Diazinon in Aquatic Organisms
Olfaction (the sense of smell) is important to aquatic organisms, especially fish, because
feeding, defense, schooling, spawning and migration are significantly influenced by olfactory
cues (Kara et al. 1976). A well known example of the importance of olfaction in aquatic
organisms is the ability of salmon and other migratory fish to follow scents in the water to find
natal streams after an extended stay in the distant ocean.
Several studies have been conducted to explore whether certain chemicals may alter
detection of olfactory cues by damaging organelles, interacting with membrane receptor sites, or
masking biologically important chemical signals. A laboratory technique for measuring
peripheral olfactory function in fish is the use of electric field potential recordings (Baatrup et al.
1990, Winberg et al. 1992). The amplitude of the EOG reflects the summed electrical response
of olfactory receptor neurons as they bind to molecules in the surrounding environment. Short-
term exposure of the olfactory epithelium of mature male Atlantic salmon (Salmo salaf) parr to >
1.0 ug/L of diazinon reduced the olfactory electrophysiological response to pheromonally-
mediated endocrine system (prostaglandin F2a) as measured by their olfactory epithelium EOG
electrical response (Moore and Waring 1996, 1998; Moore and Lower 2001).
The majority of studies associated with olfactory effects do not report effects on olfactory
organs or physiology directly, but rather evaluate the effects of chemicals on the behavior offish
that are associated with olfactory cures, including preference/avoidance reactions, feeding and
swimming responses. Chu and Lau (1994) studied the effect of diazinon on the behavioral
response of the shrimp Metapenaeus ensis to a known amino acid attractant. They found that
exposure to 0.1 ug/L diazinon significantly reduced the shrimp's ability to find and grasp the
food source. Scholz et al. (2000) found that the diazinon significantly disrupts olfactory-
mediated anti-predator responses and homing behavior of chinook salmon (Oncorhynchus
tshawytscha) at 1.0 and 10.0 ug/L, respectively. Swimming behavior and visually guided food
capture were not affected at diazinon concentrations as high as 10.0 ug/L.
In several other laboratory studies, researchers have attempted to link affects on
biochemical and physiological responses (e.g., receptor cell loss, neuron degeneration or
depressed EOG/neurotransmission) with abnormal fish behavior including disruption of
preference/avoidance reactions, depressed feeding and erratic swimming (Beyers and Farmer
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2001; Hansen et al. 1999; Saglio et al. 2001). Beauvais et al. (2000) exposed larval rainbow
trout (Oncorhynchus mykiss) for 96 hours to 250 ug/L diazinon and observed significant AChE
inhibition accompanied by decreased swimming speed, demonstrating association between
diazinon-induced AChE inhibition and a specific behavioral effect in fish.
Based on these short-term laboratory exposure results, many authors have speculated that
since fish feeding, defense, schooling, spawning and migration are significantly influenced by
olfactory cues, disruption of this sensory function would place the organism at a competitive
disadvantage in the natural environment. However, an important aspect of the findings to date is
that the effects are, for the most part, reversible. Once the animal is removed from the chemical
exposure, recovery was observed for the vast majority of the chemicals evaluated. In addition,
some studies showed that over an extended exposure period, the fish adapted to the chemical-
induced change by partially regenerating lost cells or damaged neurons leading to partial
recovery of normal olfactory function.
In the absence of confirmatory field exposure studies, whether effects of chemicals on the
olfactory system structures or function of aquatic organisms result in adverse outcomes cannot
be substantiated (no articles were obtained that evaluated this issue). The primary unanswered
question is whether temporary damage to olfactory structures or loss of olfactory function affect
homing, migratory patterns, feeding activity of exposed organisms in the wild, and more
importantly, whether these behavioral changes affect the ability of the exposed population to
reproduce, grow and ultimately survive in the wild. The impact of sublethal effects on the long-
term survival of an exposed aquatic population is difficult to determine from laboratory studies.
Long-term, field and laboratory studies are needed to provide the weight of evidence necessary
to use such endpoints in risk assessment and criteria derivation. However, it should be noted that
the freshwater and saltwater criteria recommended in this document are below the concentrations
reported to affect a variety of olfactory endpoints in several salmonid species.
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7. UNUSED DATA
Data from some studies were not used in this document, as they did not meet the criteria for
inclusion as specified in the Guidelines (Stephan et al. 1985). The reader is referred to the
Guidelines for further information regarding these criteria.
Studies were Conducted with Species that are Not Resident in North America
Alabaster (1969)
Alam and Maughan (1993)
Alametal. (1995)
Anees (1974, 1976, 1978)
Arab etal. (1990)
Asakaetal. (1980)
Bajpai and Perti (1969)
Boumaiza et al. (1979)
Ceronetal. (1996a,b)
Chu and Lau (1994)
El-Elaimy etal. (1990)
Ferrando etal. (1991)
Hammetal. (1998)
Hidakaetal. (1984)
Hirayama and Tamanoi (1980)
Hirose and Kawakami (1977)
Hirose and Kitsukama (1976)
Hirose etal. (1979)
Iqbaletal. (1992)
Kabir and Ahmed (1979)
Kabir and Begum (1978)
Kanazawa (1975, 1980, 1981a,b,
1983a)
Khalaf-Allah(1999)
Kikuchietal. (1992)
Kimura and Keegan (1966)
Kobayashietal. (1993)
Miahetal. (1995)
Morale et al. (1998)
Niforos and Lim (1998)
Nishiuchi and Yoshida (1972)
Rompas etal. (1989)
Sakr and Gabr( 1992)
Sakretal. (1991)
Sancho etal. (1992a,b, 1993a,b,
1994)
Setakana and Tan (1991)
Shigehisa and Shiraishi (1998)
Sinhaetal. (1987)
Stevens (1991, 1992)
Stevens and Warren (1992)
Tsudaetal. (1989, 1992, 1995a,b,
1997a,b)
Uno etal. (1997)
VanderGeestetal. (1999)
Yasutomi and Takahashi (1987)
Data were Compiled from Other Sources
Bay etal. (1993)
Connolly (1985)
Dyer etal. (1997)
Eisler (1986)
Garten and Trabalka (1983)
Kaiser etal. (1997)
Kanazawa (1982)
Kenaga (1979, 1982)
Robinson (1999)
Roex et al. (2000)
Steenetal. (1999)
Van derGeest etal. (1997)
Vighi and Calamari (1987)
Vittozzi and DeAngelis (1991)
Yoshiokaetal. (1986)
Zaroogian et al. (1985a)
23
-------
Diazinon was a Component of a Drilling Mud, Effluent, Mixture, Sediment or Sludge
Alam and Maughan (1992) Glass et al. (1995) Matsuo and Tamura (1970)
Amato et al. (1992) Gruber and Munn (1998) Mazidji et al. (1990)
Bailey et al. (1996, 2000) Hashimoto et al. (1982) Mulla et al. (1963)
Bathe et al. (1975a,b) Hatakeyama et al. (1997) Nishiuchi (1977)
Bishop et al. (1999) Hendriks et al. (1998) Pan and Dutta (1998)
Burchfield and Storrs (1954) Hilsenhoff (1959) Rettich (1979)
Burkhard and Jenson (1993) Kikuchi et al. (1996) Singh (1973)
Deanovic et al. (1996, 1997) Kuivila and Foe (1995) Steinberg et al. (1992)
Dennis et al. (1979a,b) LaBrecque et al. (1956) Tripathi (1992)
DeVlaming et al. (2000) Larsen et al. (1998) Tsuda et al. (1997a,b)
Doggett and Rhodes (1991) Lehotay et al. (1998) Verma et al. (1982)
Duursma and Hanafi (1975) McLeay and Hall (1999) Werner et al. (2000)
Foe (1995) Macek (1975) Wong (1997)
Foe et al. (1998) Malone and Blaylock (1970) Wong and Chang (1988)
Results of tests conducted with brine shrimp, Artemia sp. (e.g. Kuwabara et al. 1980),
were not used because these species are from a unique saltwater environment.
Results were not used when either the test procedures, test material, or dilution water was
not adequately described (e.g., Adlung 1957; Ansari et al. 1987; Butler et al. 1975a,b;
Charter] ee 1975; Hashimoto and Fukami 1969; Hatakeyama and Sugaya 1989; Kaur and Toor
1980; Murray and Guthrie 1980; Oh et al. 1991; Qadri and Anjum 1982).
Results of some laboratory tests were not used because the tests were conducted in
distilled or deionized water without addition of appropriate salts or were conducted in
chlorinated or "tap" water (e.g., Mulla et al. 1962; Rettich 1977; Yasuno et al. 1965), or the
concentration of a water-miscible solvent used to prepare the test solution exceeded 0.5 mL/L
(Beauvais et al. 2000). Hirakoso 1968; Lee et al. 1993; Jamnback and Frempong-Boadu 1966;
Klassen et al. 1965; Kok 1972; Lilly et al. 1969; Mulla 1963; Nishiuchi and Asano 1979;
O'Kelley and Deason 1976; Steinberg et al. 1993 were not used because the results were not
adequately described or could not be interpreted.
Tests conducted without controls, with unacceptable control survival, or with too few test
organisms were not used (e.g., Applegate et al. 1957; Devillers et al. 1985; Federle and Collins
1976; Allison and Hermanutz 1977). Data of Norland et al. (1974) were not used because they
24
-------
were derived using organisms preconditioned to organophosphorus chemicals.
Experimental Model was Plasma, Enzymes, Tissue, or Cell Cultures
Anjum and Siddiqui (1990) Fujii and Asaka (1982) Qadri and Dutta( 1995)
Ansari and Kumar (1988) Garrood et al. (1990) Sastry and Malik (1982a,b)
Ariyoshi et al. (1990) Hiltibran (1974) Sastry and Sharma (1980,
Burbank and Snell (1994) Keizer et al. (1995) 1981)
Christensen and Tucker (1976) Kraus (1985) Vigfusson et al. (1983)
Dutta et al. (1992a,b, 1993, Mitsuhashi et al. (1970) Weiss (1959, 1961)
1994,1997) Moore and Waring (1996) Weiss and Gakstater (1964)
Dyer et al. (1993) Olson and Christensen (1980) Whitmore and Hodges (1978)
BCFs and BAFs from laboratory tests were not used when the tests were static or when
the concentration of diazinon in the test solution was not adequately measured or varied too
much (e.g., Khattat and Farley 1976). Toxicity data were not used if they were generated with
a photoluminescence assay utilizing lyophilized marine bacteria that had been rehydrated (e.g.,
Curtis et al. 1982). Reports of the concentration of diazinon in wild aquatic organisms (e.g.,
Clark et al. 1984) were not used to calculate BAFs when either the number of measurements of
the concentration in water was too small or the range of the measured concentrations in water
was too large. BCFs obtained from microcosm or model ecosystem studies were not used
when the concentration of diazinon in water decreased with time (e.g., Miller et al. 1966).
25
-------
8. SUMMARY
8.1. Freshwater Data
The acute toxicity of diazinon to freshwater organisms was determined for 13 invertebrate
species from 11 genera, 10 fish species from 8 genera, and one amphibian species (Figure 1
and Table 3). Nine of the invertebrate species (seven crustaceans and two insects) were the
most sensitive organisms tested (SMAV = 0.38 to 25 ug/L) and one invertebrate species
(planarian) was the most tolerant species tested (SMAV = 11,640 ug/L). Freshwater fish and
the amphibian (green frog) were intermediate in sensitivity to the two groups of invertebrates.
Rainbow trout (Oncorhynchus mykiss) was the most sensitive (SMAV = 425.8 ug/L) and
goldfish (Carassius auratus) was the most tolerant fish tested (SMAV = 9,000 ug/L). No
relationships have been demonstrated between diazinon toxicity and water quality
characteristics such as hardness. The freshwater Final Acute Value is 0.3397 ug/L.
The chronic toxicity of diazinon to freshwater organisms was determined for four species
(Figure 3 and Table 2). Chronic values ranged from 0.3382 to 68.93 ug/L (Table 2), and the
Acute-Chronic Ratios (ACRs) ranged from 1.112 for Ceriodaphnia dubia to > 903.8 for brook
trout (Salvelinus fontinalis) (Table 3). The Final Acute-Chronic Ratio for diazinon was
derived using two ACRs for tested species with acute values near the FAV (C. dubia and A.
bahid) because the ACRs decreased with SMAVs. The calculated FACR was less than 2.0,
indicating that the organisms may have become acclimated to diazinon during the study.
Therefore, the FACR value was changed to 2.0 (Stephan et al. 1985). Thus, the freshwater
Final Chronic Value (FCV) for diazinon is 0.1699 ug/L (FAV - FACR, or 0.3397 ug/L - 2.0 =
0.1699 ug/L).
8.2. Saltwater Data
The acute toxicity of diazinon to saltwater organisms was determined for 7 invertebrate
species from 7 genera and 2 fish species from 2 genera (Figure 2 and Table 3). Five of the
invertebrates were crustaceans and the most sensitive species tested (SMAV = 2.57 to 21 ug/L)
and two species (an annelid and an echinoderm) were the most tolerant species tested (SMAVs
> 2,880 and > 9,600 ug/L, respectively). The two saltwater fish species tested were
intermediate in sensitivity with acute values of 1,170 and 1,400 ug/L. No relationships have
been demonstrated between diazinon toxicity and water quality characteristics such as salinity.
26
-------
The saltwater Final Acute Value is 1.637 ug/L.
Chronic values were determined for two species of saltwater organisms (Figure 3 and
Table 2). The mysid, Americamysis bahia, and the sheepshead minnow, Cyprinodon
variegatus, had chronic values of 3.040 and < 0.47 ug/L, respectively (Table 2). ACRs for
these speces were 1.586 for the mysid and > 2,979 for the sheepshead minnow (Table 3). The
Final Acute-Chronic Ratio for diazinon was derived using two ACRs for tested species with
acute values near the FAV (C. dubia and A. bahia) because the ACRs decreased with SMAVs.
The calculated FACR was less than 2.0, indicating that the organisms may have become
acclimated to diazinon during the study. Therefore, the FACR value was changed to 2.0
(Stephan et al. 1985). Thus, the saltwater Final Chronic Value (FCV) for diazinon is 0.8185
ug/L (FAV -H FACR, or 1.637 ug/L - 2.0 = 0.8185 ug/L).
8.3. Plant Data
Only one acceptable test with a freshwater algal species (Selenastrum capricornutum) was
available, whereas no acceptable toxicity data are available for freshwater vascular plants. No
saltwater tests with aquatic plants were suitable for consideration when estimating the Final
Plant Value. Therefore, based on the single test with the freshwater algae, the Final Plant
Value is 6,400
8.4. Bioaccumulation Data
Bioaccumulation of diazinon was measured in three species of freshwater fish and steady-
state concentrations were reached in about three days. Bioconcentration factors of 62, 120 and
188 were determined for rainbow trout, carp (Cyprinus carpio) and guppy (Poecilia
reticulata\ respectively. The tissue half-life of diazinon was less than seven days.
Bioaccumulation of diazinon was determined in one saltwater species. The sheepshead
minnow was exposed for 108 days to three concentrations of diazinon. The mean
bioconcentration factor, based on the BCF for the three concentrations, was 169.
27
-------
9. NATIONAL CRITERIA
9.1. Freshwater
The procedures described in the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses" (Stephan et al. 1985)
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 one-hour average
concentration does not exceed 0.17 ug/L more than once every three years on the average and
if the four-day average concentration of diazinon does not exceed 0.17 ug/L more than once
every three years on the average.
Growth of offspring of exposed brook trout, a recreationally important freshwater fish
species, was statistically significantly reduced by 40% at the lowest tested concentration of 0.8
Ug/L, which is a factor of 4.7 times the CCC. However, the chronic value for this study is a
less than value and it is uncertain how close to the freshwater CCC adverse effects may occur.
9.2. Saltwater
The procedures described in the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses" (Stephan et al. 1985)
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 one-hour average
concentration does not exceed 0.82 ug/L more than once every three years on the average and
if the four-day average concentration of diazinon does not exceed 0.82 ug/L more than once
every three years on the average.
Reproduction of the saltwater sheepshead minnow was statistically significantly
reduced by 31% at the lowest tested concentration of 0.47 ug/L, which is below the saltwater
CCC. Therefore, where exposure to diazinon at or near CCC levels may occur to this or
similar saltwater fish species, states and tribes may want to consider site-specific criteria
derivations for diazinon. Because sensitive saltwater animals appear to have a narrow range of
acute susceptibilities to diazinon, this criterion will probably be as protective as intended only
when the magnitude and/or duration of excursions are appropriately small.
28
-------
10. IMPLEMENTATION
As discussed in the Water Quality Standards Regulation (U.S. EPA 1983) and the
Foreword to this document, a water quality criterion for aquatic life has regulatory impact only
after it has been adopted in a state or tribal water quality standard. Such a standard specifies a
criterion for a pollutant that is consistent with a particular designated use. With the
concurrence of the U.S. EPA, states and tribes designate one or more uses for each body of
water or segment thereof and adopt criteria that are consistent with the use(s) (U.S. EPA 1994,
1987). In each standard a state or tribe may adopt the national criterion, if one exists, or, if
adequately justified, a site-specific criterion (if the site is an entire state, the site-specific
criterion is also a state-specific criterion).
Site-specific criteria may include not only site-specific criterion concentrations (U.S. EPA
1994), but also site-specific, and possibly pollutant-specific, durations of averaging periods and
frequencies of allowed excursions (U.S. EPA 1991). The averaging periods of "one hour" and
"four days" were selected by the U.S. EPA on the basis of data concerning how rapidly some
aquatic species react to increases in the concentrations of some pollutants, and "three years" is
the Agency's best scientific judgment of the average amount of time aquatic ecosystems
should be provided between excursions (Stephan et al. 1985; U.S. EPA 1991). However,
various species and ecosystems react and recover at greatly different rates. Therefore, if
adequate justification is provided, site-specific and/or pollutant-specific concentrations,
durations, and frequencies may be higher or lower than those given in national water quality
criteria for aquatic life.
Use of criteria, which have been adopted into state or tribal water quality standards, for
developing water quality-based permit limits requires selection of an appropriate wasteload
allocation model. Although dynamic models are preferred for the application of these criteria
(U.S. EPA 1991), limited data or other considerations might require the use of a steady-state
model (U.S. EPA 1986). Guidance on mixing zones and the design of monitoring programs is
also available (U.S. EPA 1987, 1991).
29
-------
— 10N
c
_g
ro 1000
8 100
c
O
o 10
o
£ 1
LU n
0.1 -
N
re
0.01
Figure 1. Summary of Ranked Diazinon GMAVs
Freshwater
a n
Freshwater Final Acute Value = 0.3397 ug/L Diazinon
Criteria Maximum Concentration =0.1699 ug/L Diazinon
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7
Genus Mean Acute Values
(Cumulative Fraction)
0.8 0.9 1.0
• Fish
D Invertebrates
A Amphibians
30
-------
Figure 2. Summary of Ranked Diazinon GMAVs
Saltwater
_J
c
.0
s
^^J
^p*
c
0)
o
o
o
,|_>
o
£
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LU
c
0
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re
Q
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1000 -E
:
100 -E
2
-
-
10 -E
-
:
1 -
-
"
0.1 -
D
D
•
D
D
D
D °
Saltwater Final Acute Value = 1.637 ug/L Diazinon
Criteria Maximum Concentration = 0.8185 ug/L Diazinon
i i i i i i i i i i
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
Genus Mean Acute Values
(Cumulative Fraction)
• Fish
D Invertebrates
31
-------
Figure 3. Chronic Toxicity of Diazinon to Aquatic Animals
_J
"ro
^^
0)
o
0
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•+->
o
£
LU
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o
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.5
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A Saltwater Final Chronic Value =0.8185 ug/L Diazinon
Freshwater Final Chronic Value = 0.1699 ug/L Diazinon
1 1 1 1 1 1 1 1 1 1
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
Genus Mean Chronic Values
(Cumulative Fraction)
D Freshwater Invertebrates
• Freshwater Fish
A Saltwater Invertebrates
A Saltwater Fish
32
-------
Table 1. Acute Toxicity of Diazinon to Aquatic Animals
Species
Method"
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(us/L)
Species Mean
Acute Value0
(ug/L) Reference
FRESHWATER SPECIES
Planaria,
Dugesia tigrina
Oligochaete worm,
Lumbriculus
variegates
Oligochaete worm,
Lumbriculus
variegates
Snail (2.4 g),
Gillia altilis
Apple snail (1-day),
Pomacea paludosa
Apple snail (7 -days),
Pomacea paludosa
Apple snail (7 -days),
Pomacea paludosa
Cladoceran
(<24 hr),
Ceriodaphnia dubia
Cladoceran
(<24 hr),
Ceriodaphnia dubia
Cladoceran
(<24 hr),
Ceriodaphnia dubia
Cladoceran
(<24 hr),
Ceriodaphnia dubia
Cladoceran
(<24 hr),
Ceriodaphnia dubia
Cladoceran
(<6 hr),
Ceriodaphnia dubia
Cladoceran
(<48 hr),
S,M
S,M
S,U
S,U
F,M
F, M
F, M
S,U
s,u
s,u
s,u
s,u
S,M
s,u
Technical
(85%)
Technical
(85%)
Technical
(95%)
Technical
(89%)
Technical
(87%)
Technical
(87%)
Technical
(87%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
46.5-47.5
46-48
42-47
22-35
130.5
219
173.5
40
45
40-48
~
40
40
-
11.640
9,980
6.160
11,000
2.950
3.270
3.390
0.57^
0.66^
0.57^
>1.0d'e
>0.6d'e
0.66 "^
0.35
11,640 Phipps 1988
Phipps 1988
7,841 Ankleyand
Collyard 1995
11,000 Robertson and
Mazzella 1989
Call 1993
Call 1993
3,198 Call 1993
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Ceriodaphnia dubia
33
-------
Table 1. (continued)
Species Method3
Cladoceran S, U
(<48 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<6 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<24 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<48 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<48 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<48 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<48 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<48 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<48 hr),
Ceriodaphnia dubia
Cladoceran S, M
(<24 hr),
Ceriodaphnia dubia
Cladoceran S, M
(<24 hr),
Ceriodaphnia dubia
Cladoceran S, M
(<24 hr),
Ceriodaphnia dubia
Cladoceran S, M
(<24 hr),
Ceriodaphnia dubia
Cladoceran S, U
(<20 hr),
Daphnia magna
Chemicalb
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(85%)
Technical
(95%)
Analytical
(99%)
Analytical
(99%)
Analytical
(99%)
Analytical
(99%)
Technical
Hardness LC50
(mg/L as or EC50
CaCO3) (ug/L)
0.35
0.25
0.33
0.35
0.59
0.43
0.35
0.36
40-48 0.5
80-100 0.58
80-100 0.48
80-100 0.26
80-100 0.29
50 0.96
Species Mean
Acute Value0
(ug/L) Reference
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Norberg-King
1987
Ankley et al.
1991
Bailey etal. 1997
Bailey etal. 1997
Bailey etal. 1997
0.3773 Bailey etal. 1997
Vilkas 1976
34
-------
Table 1. (continued)
Species Method3
Cladoceran S, U
(<24 hr),
Daphnia magna
Cladoceran S, U
(<48 hr),
Daphnia magna
Cladoceran S, U
(first instar),
Daphnia pulex
Cladoceran S, U
(first instar),
Daphnia pulex
Cladoceran S, U
(<48 hr),
Daphnia pulex
Cladoceran S, U
(first instar),
Simocephalus
serrulatus
Cladoceran S, U
(first instar),
Simocephalus
serrulatus
Amphipod (mature), S, U
Gammarus fasciatus
Amphipod (mature), R, M
Gammarus
pseudolimnaeus
Amphipod S, U
(7-14 days),
Hyalella azteca
Stonefly S, U
(larva 30-35 mm),
Chemicalb
Analytical
Technical
(95%)
Technical
(89%)
Technical
(89%)
Technical
(95%)
Technical
(89%)
Technical
(89%)
Technical
(89%)
Analytical
(100%)
Technical
(95%)
Technical
(89%)
Hardness LC50
(mg/L as or EC50
CaCO3) (ug/L)
200 1.5
40-48 0.8
47 0.90
47 0.8
40-48 0.65
47 1.8
47 1A
44 2.04
62.5 16.82
42-47 6.51
47 25
Species Mean
Acute Value0
(ug/L) Reference
Dortland 1980
1.048 Ankleyetal.
1991
Cope 1965a;
Sanders and Cope
1966
Johnson and
Finley 1980;
Mayer and
Ellersieck 1986
0.7764 Ankley et al.
1991
Cope 1965a;
Sanders and Cope
1966; Mayer and
Ellersieck 1986
1.587 Sanders and Cope
1966; Johnson
and Finley 1980;
Mayer and
Ellersieck 1986
2.04 Johnson and
Finley 1980;
Mayer and
Ellersieck 1986
16.82 Hall and
Anderson 2004
6.51 Ankley and
Collyard 1995
25 Cope 1965a;
Sanders and Cope
Pteronarcys
californica
1968; Johnson
and Finley 1980;
Mayer and
Ellersieck 1986
35
-------
Table 1. (continued)
Species Method3
Midge S, U
(third instar),
Chironomus tentans
Cutthroat trout S, U
(2.0 g),
Oncorhynchus clarki
Cutthroat trout S, U
(2.0 g),
Oncorhynchus clarki
Rainbow trout S, U
(3.7 cm),
Oncorhynchus
mykiss
Rainbow trout S, U
(1.20 g),
Oncorhynchus
mykiss
Rainbow trout S, U
(25-50 g),
Oncorhynchus
mykiss
Rainbow trout, S, U
Oncorhynchus
mykiss
Rainbow trout, S, U
Oncorhynchus
mykiss
Brook trout (1 yr), F, M
Salvelinus fontinalis
Brook trout (1 yr), F, M
Salvelinus fontinalis
Brook trout (1 yr), F, M
Salvelinus fontinalis
Lake trout (3. 20 g), S,U
Salvelinus
namaycush
Zebrafish (0.4 g), R, M
Danio rerio
Chemicalb
Technical
(95%)
Technical
(92%)
Technical
(92%)
Technical
Technical
(89%)
Technical
Technical
Reagent
Technical
(92.5%)
Technical
(92.5%)
Technical
(92.5%)
Technical
(92%)
Technical
(98%)
Hardness LC50
(mg/L as or EC50
CaCO3) (ug/L)
42-47 10.7
162 1,700
44 2,760
400
44 90
3.200
90
192 1.350
45 800
45 450
45 1.050
162 602
8.000
Species Mean
Acute Value0
(ug/L) Reference
10.7
2,166
425.8
723.0
602
Ankley and
Collyard 1995
Johnson and
Finley 1980;
Mayer and
Ellersieck 1986
Mayer and
Ellersieck 1986
Bellies 1965
Cope 1965a;
Johnson and
Finley 1980;
Mayer and
Ellersieck 1986
Bathe etal. 1975a
Ciba-Giegy 1976
Meier etal. 1979;
Dennis etal. 1980
Allison and
Hermanutz 1977
Allison and
Hermanutz 1977
Allison and
Hermanutz 1977
Johnson and
Finley 1980;
Mayer and
Ellerseick 1986
Keizeretal. 1991
36
-------
Table 1. (continued)
Species
Fathead minnow,
Pimephales promelas
Fathead minnow
(newly hatched
larva),
Pimephales promelas
Fathead minnow
(newly hatched
larva),
Pimephales promelas
Fathead minnow
(juvenile),
Pimephales promelas
Fathead minnow
(juvenile),
Pimephales promelas
Fathead minnow
(juvenile),
Pimephales promelas
Fathead minnow
(newly hatched
larva),
Pimephales promelas
Fathead minnow
(juvenile),
Pimephales promelas
Goldfish
(2.5-6.0 cm),
Carassius auratus
Flagfish (6 wk),
Jordanella floridae
Flagfish (7 wk),
Jordanella floridae
Guppy (0.6 g),
Poecilia reticulata
Bluegill
(2.5-5.0 cm),
Lepomis macrochirus
Bluegill (0.87 g),
Lepomis macrochirus
Method3
S,U
S,M
S,M
F, M
F, M
F,M
F, M
F,M
S,U
F,M
F,M
R,M
S,U
Hardness
(mg/L as
Chemicalb CaCO3)
Reagent 192
Technical 45.8
(87.1%)
(fresh stock
solution)
Technical 45.8
(87.1%)
(aged stock
solution)
Technical 45
(92.5%)
Technical 45
(92.5%)
Technical 45
(92.5%)
Technical 45
(87.1%)
Technical 43.6
(87.1%)
Technical
(91%)
Technical 45
(92.5%)
Technical 45
(92.5%)
Technical
(98%)
Technical
LC50
or EC50
(ug/L)
10,300e
4,300 e
2,100e
6,600
6.800
10,000
6.900
9.350
9.000
1.500
1,800
800
136e
Species Mean
Acute Value0
(ug/L) Reference
Meier etal. 1979;
Dennis etal. 1980
Jarvinen and
Tanner 1982
Jarvinen and
Tanner 1982
Allison and
Hermanutz 1977
Allison and
Hermanutz 1977
Allison and
Hermanutz 1977
Jarvinen and
Tanner 1982
7804 University of
Wisconsin-
Superior 1988
9,000 Bellies 1965
Allison and
Hermanutz 1977
1,643 Allison and
Hermanutz 1977
800 Keizer etal. 1991
Bellies 1965
s,u
Technical
22e
Cope 1965b
37
-------
Table 1. (continued)
Species
Bluegill,
Lepomis macrochims
Bluegill (0.8 g),
Lepomis macrochims
Bluegill (1. 00 g),
Lepomis macrochims
Bluegill (1 yr),
Lepomis macrochims
Bluegill (1 yr.),
Lepomis macrochims
Green frog
(stage 8),
Rana clamitans
Species
Method3
S,U
s,u
s,u
F, M
F, M
R,U
Method"
Chemicalb
Technical
Reagent
Technical
(92%)
Technical
(92.5%)
Technical
(92.5%)
Technical
Chemicalb
Hardness
(mg/L as
CaCO3)
-
192
44
45
45
Salinity
(g/kg)
LC50
or EC50
(ug/L)
22 e
120 e
168.0 e
480
440
>50
LC50
or EC50
(ug/L)
Species Mean
Acute Value0
(ug/L) Reference
Ciba-Geigy 1976
Meier etal. 1979;
Dennis etal. 1980
Johnson and
Finley 1980;
Mayer and
Ellersieck 1986
Allison and
Hermanutz 1977
459.6 Allison and
Hermanutz 1977
>50 Harris etal. 1998
Species Mean
Acute Value0
(ug/L) Reference
SALTWATER SPECIES
Annelid worm
(juvenile),
Neanthes
arenaceodentata
Copepod (adult),
Acartia tonsa
Mysid (juvenile),
Americamysis bahia
Mysid (juvenile),
Americamysis bahia
Mysid (juvenile),
Americamysis bahia
Amphipod (juvenile),
Ampelisca abdita
Pink shrimp (larval),
Penaeus duoramm
Grass shrimp
(larval),
R,U
S,M
R,U
s,u
F, M
R,U
s,u
R,U
(96%)
Technical
(97.6%)
(96%)
Technical
Diazinon
(96%)
Technical
(96%)
30
20
29
25
17
30
25
30
>2.880
2.57
8.5 e
8.5 e
4.82
6.6
21
2.8
>2,880 Thursby & Berry
1988
2.57 Khattat & Farley
1976
Thursby & Berry
1988
Cripe 1994
4.82 Nimmoetal. 1981
6.6 Thursby & Berry
1988
21 Cripe 1994
2.8 Thursby & Berry
1988
Palaemonetes pugio
38
-------
Table 1. (continued)
Sea urchin
(embryo/larval),
Arbacia punctulata
Sheepshead minnow
(juvenile),
Cyprinodon
variegatus
Inland silverside
(juvenile),
Menidia beryllina
Method3
S,U
F, M
R,U
Chemicalb
(96%)
(92.6%)
(96%)
LC50 Species Mean
Salinity or EC50 Acute Value0
(g/kg) (ug/L) (ug/L) Reference
31 >9,600 >9,600 Thursby & Berry
1988
23 1,400 1,400 Goodman etal.
1979; Mayer 1987
30 1,170 1,170 Thursby & Berry
1988
a S = static; R = renewal; F = flow-through; M = measured; U = unmeasured.
b Percent purity is given in parenthesis when available.
0 Species Mean Acute Value was calculated from the underlined number(s) in the preceeding column.
d Animals were fed during the exposure.
e Results were not used in the calculation of the Species Mean Acute Value due to availability of data from more
sensitive test conditions.
39
-------
Table 2. Chronic Toxicity of Diazinon to Aquatic Animals
Species Test"
Cladoceran LC
(<6-hr. old), (7-day)
Ceriodaphnia
dubia
Brook trout PLC
(yearling),
Salvelinus
fontinalis
Fathead minnow ELS
(embryo-larva),
Pimephales
promelas
Fathead minnow ELS
(embryo-larva),
Pimephales
promelas
Flagfish LC
(1-day old),
Jordanella floridae
Mysid (juvenile), LC
Americamysis
bahia
Sheepshead PLC
minnow (juvenile),
Cyprinodon
variegatus
Hardness Chronic
(mg/L as Limits
Chemicalb CaCO3) fus/L)
FRESHWATER SPECIES
Technical 40 0.220-0.520
(85%)
Technical 45 0-0.8
(92.5%)
Technical 44-49 16.5-37.8
(88.2%)
Technical 45.8 50-90
(87.1%)
54-88
SALTWATER SPECIES
30-31C 2.1-4.4
Technical 16.5C 0-0.47
(92.6%)
Chronic
Value
(us/L) Reference
0.3382 Norberg-King 1987
< 0.8 Allison and
Hermanutz 1977
24.97 Norberg-King 1989
67.08 Jarvinen and Tanner
1982
68.93 Allison 1977
3.040 Nimmoetal. 1981
< 0.47 Goodman et al.
1979
a PLC = partial life-cycle; ELS = early life-stage; LC = life cycle.
b Percent purity is listed in parentheses when available.
c Salinity (g/kg).
40
-------
Table 2. (continued)
Acute-Chronic Ratio
Species
Cladoceran,
Ceriodaphnia dubia
Mysid,
Americamysis bahia
Flagfish,
Jordanella floridae
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Brook trout,
Salvelinus fontinalis
Sheepshead minnow,
Cyprinodon variegatus
Hardness
(mg/L as
CaCO3)
40
1?c
45
44-49
45.8
45
16.5C
Acute
Value
(U2/L)
0.3760
4.82
1,643
9,350
6,900
723.0
1,400
Chronic Value
(U2/L) Ratio
0.3382 1.112
3.040 1.586
68.93 23.84
24.97 374.4
67.08 102.9
<0.8 >903.8
0.47 >2,979
Mean
Ratio
1.112
1.586
23.84
-
196.3
>903.8
>2,979
Salinity (g/kg).
41
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
Rank"
20
19
18
17
16
15
14
13
12
11
10
9
Genus Mean
Acute Value
(U2/U
11,640
11,000
9,000
8,000
7,841
7804
3,198
1,643
960.4
800
659.7
459.6
Species
FRESHWATER
Planaria,
Dugesia tigrina
Snail,
Gillia altilis
Goldfish,
Carassius auratus
Zebrafish,
Danio rerio
Oligachaete worm,
Lumbricus variegatus
Fathead minnow,
Pimephales promelas
Snail,
Pomacea paludosa
Flagfish,
Jordanella floridae
Cutthroat trout,
Oncorhynchus clarki
Rainbow trout,
Oncorhynchus mykiss
Guppy,
Poecilia reticulata
Brook trout,
Salvelinus fontinalis
Lake trout,
Salvelinus namaycush
Bluegill,
Species Mean Species Mea
Acute Value Acute-Chror
(u2/L)b Ratioc'd
SPECIES
11,640
11,000
9,000
8,000
7,841
7804 196.3
3,198
1,643 23.84
2,166
425.8
800
723 >903.8
602
459.6
Lepomis macrochirus
42
-------
Table 3. (continued)
Genus Mean
Acute Value
Rank3 (us/L)
8 >50
7 25
6 10.7
5 6.51
4 5.858
3 1.587
2 0.9020
1 0.3773
Species
Green frog
Rana clamitans
Stonefly,
Pteronarcys
californica
Midge,
Chironomus tentans
Amphipod,
Hyalella azteca
Amphipod,
Gammarus fasciatus
Amphipod,
Gammarus
pseudolimnaeus
Cladoceran,
Simocephalus
serrulatus
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran,
Ceriodaphnia dubia
Species Mean
Acute Value
>50
25
10.7
6.51
2.04
16.82
1.587
1.048
0.7764
0.3773
Species Mean
Acute-Chronic
Ratioc'd
1.112
43
-------
Table 3. (continued)
SALTWATER SPECIES
9
8
7
6
5
4
3
2
1
>9,600
>2,880
1,400
1,170
21
6.6
4.82
2.8
2.57
Sea urchin,
Arbacia punctulata
Annelid worm,
Neanthes
arenaceodentata
Sheepshead minnow,
Cyprinodon variegatus
Inland silverside,
Menidia beryllina
Pink shrimp,
Penaeus duorarum
Amphipod,
Ampelisca abdita
Mysid,
Americamysis bahia
Grass shrimp
Palaemonetes pugio
Copepod,
Acartia tonsa
>9,600
>2,880
1,400
1,170
21
6.6
4.82
2.8
2.57
-
-
>2,979
-
-
-
1.586
-
-
a Ranked from most sensitive to most resistant based on Genus Mean Acute Values.
b From Table 1.
c From Table 2.
d The Species Mean Acute-Chronic Values underlined and in bold font were used to calculate
the Final Acute-Chronic Ratio.
44
-------
Table 3. (continued)
Freshwater
Final Acute Value = 0.3397 ug/L
Criterion Maximum Concentration = 0.3397 ug/L + 2 = 0.1699 ug/L
Final Acute-Chronic Ratio = 2.0 (see text)
Final Chronic Value = 0.3397 ug/L - 2.0 = 0.1699 ug/L
Saltwater
Final Acute Value = 1.637 ug/L
Criterion Maximum Concentration = 1.637 ug/L -H 2 = 0.8185 ug/L
Final Acute-Chronic Ratio = 2.0 (see text)
Final Chronic Value = 1.637 ug/L - 2.0 = 0.8185 ug/L
45
-------
Table 4. Toxicity of Diazinon to Aquatic Plants
Hardness
(mg/L as Duration Concentration
Species CaCO3) (days) Effect (ug/L) Reference
FRESHWATER SPECIES
Green algae, - 7 EC50 6,400 Hughes
Selenastrum (cell 1988
capricornutum numbers)
46
-------
Table 5. Bioaccumulation of Diazinon by Aquatic Organisms
Species
Cone, in
Water Duration Percent BCF or Normalized
dig/L)a (days) Tissue Lipid BAFb BCF or BAFC Reference
FRESHWATER SPECIES
Rainbow trout 15
(16 g),
Oncorhynchus
mykiss
Carp (8 g), 15
Cyprinus
carpio
Guppy, 350
Poecilia
reticulata
Sheepshead 1.8
minnow,
Cyprinodon
variegatus
Sheepshead 3.5
minnow,
Cyprinodon
variegatus
Sheepshead 6.5
minnow,
Cyprinodon
variegatus
14 Whole - 62
body
14 Whole - 120
body
14 Whole - 188
body
SALTWATER SPECIES
108 Whole - 147
body
(less brain)
108 Whole - 147
body
(less brain)
108 Whole - 213
body
(less brain)
Seguchi and
Asaka 1981
Seguchi and
Asaka
1981
Keizer et al.
1993
Goodman et
al. 1979
Goodman et
al. 1979
Goodman et
al. 1979
a Measured concentration of diazinon.
b Bioconcentration factors (BCFs) and bioaccumulation factors (BAFs) are based on measured
concentrations of diazinon in water and in tissue.
c When possible, the factors were normalized to 1% lipids by dividing the BCFs and BAFs by
the percent lipids.
47
-------
Table 6. Other Data on Effects of Diazinon on Aquatic Organisms
Species
Sewage
microbes
Actinomycete
bacteria
Green alga,
Chlorella
ellipsoidea
Green alga,
Chlamydomonas
sp.
Green alga,
Scenedesmus
quadricauda
Mixture of green
alga and diatoms
Euglenoid,
Euglena elastica
Duckweed,
Wolffia
papulifera
Duckweed,
Wolffia
papulifera
Protozan,
Paramecium
caudatum
Rotifer,
Brachionus
calyciflorus
Rotifer
(16-18 hr),
Brachionus
calyciflorus
Rotifer (<2 hr),
Brachionus
calyciflorus
Chemical"
Regent
Technical
-
-
-
(99.9%)
-
(97%)
(97%)
-
Technical
(92%)
Technical
(92%)
Technical
(92%)
Hardness
(mg/L as
CaCO3) Duration
FRESHWATER
22 hr
20 days
72 hr
72 hr
10 days
14 days
72 lu-
ll days
1 1 days
Ihr
80-100 24 hr
80-100 5 hr
80-100 10 days
Effect
SPECIES
No reduction of
oxygen
consumption
Stimulated
growth
Decreased ATP
content
Decreased ATP
content
No decrease in
cell number,
biomass, or
photosynthesis
Decreased growth
Decreased ATP
content
Lethal
Teratogenic
effects
LC50
LC50
Reduced (50%)
filtration and
ingestion ratios
Decreased
reproduction
Concentration
Ol2/L)
40,000
40,000
100,000
100,000
1,000
<10
100,000
100,000
10,000
~3,000
29,220
14,000
<5,000
Reference
Bauer etal. 1981
Sethunathan and
MacRae 1969
Clegg and
Koevenig 1974
Clegg and
Koevenig 1974
Stadnyk and
Campbell 1971
Butler et al.
1975a
Clegg and
Koevenig 1974
Worthley and
Schott 1971
Worthley and
Schott 1971
Evtugyn et al.
1997
Fernandez-
Casalderrey et
al. 1992a
Fernandez-
Casalderrey et
al. 1992b
Fernandez-
Casalderrey et
al. 1992c
48
-------
Table 6. (continued)
Species
Chemical"
Hardness
(mg/L as
CaCO3) Duration Effect
Concentration
(ug/L) Reference
Rotifer (<2 hr),
Brachionus
calyciflorus
Rotifer (<2 hr),
Brachionus
calyciflorus
Rotifer (<2 hr),
Brachionus
calyciflorus
Rotifer (<2 hr),
Brachionus
calyciflorus
Rotifer (<2 hr),
Brachionus
calyciflorus
Oligochaete
worm,
Lumbriculus
variegatus
Tubificid worm,
Branchiura
sowerbyi
Snail,
(Physa acuta)
Cladoceran
Daphnia magna
Cladoceran
(adult),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Technical
(99%)
Technical
(99%)
Technical
(99%)
"
"
"
-
-
Analytical
(95%)
Analytical
(99%)
Analytical
(99%)
Analytical
(99%)
80-100 4.04 days LT50
80-100 4.66 days LT50
80-100 2.49 days LT50
80-100 48 hr NOEC
Reproduction
80-100 48 hr NOEC Ingestion
4 hr Lethal
96 hr LC50
48 hr LC50
202 50 hr EC50
24 hr Adhesion of algal
particles on 2nd
antennae and
immobilization
200 21 days Reduced
reproduction and
mobility
200 21 days No reduction in
reproduction or
mobility
200 21 days EC50
(immobilization)
200 21 days EC50
(immobilization)
5,000
7,000
14,000
8,000
20,000
20,000
2,220
4,800
4.3
1
0.3
0.2
0.22
0.24
Fernandez-
Casalderry et al.
1992d
Fernandez-
Casalderrey et
al. 1992d
Fernandez-
Casalderry et al.
1992d
Snell and Moffat
1992
Juchelka and
Snell 1994
Rogge and
Drewes 1993
Chatterjee and
Konar 1984
Hashimoto and
Nishiuchi 1981
Anderson 1959
Stratton and
Corke 1981
Dortland 1980
Dortland 1980
Dortland 1980
Dortland 1980
49
-------
Table 6. (continued)
Species
Chemical"
Hardness
(mg/L as
CaCO3) Duration
Effect
Concentration
(ug/L) Reference
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran
(adult),
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran (<24
hr),
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnia pulex
Analytical
(99%)
Analytical
(99%)
Insecticidal
soap
Insecticidal
soap
Technical
Technical
Technical
(92%)
Technical
(92%)
Technical
(92%)
Technical
(92%)
Technical
(92%)
Technical
(96.1%)
Optimum
-
-
200 21 days
200 21 days
48 hr
96hr
3hr
3hr
5hr
250 21 days
250 21 days
250 21 days
250 24 hr
182 21 days
160-180 30 min
3hr
3hr
EC50
(immobilization)
EC50
(immobilization)
LC50
LC50
LC50
LC50
Reduced (50%)
filtration rate
NOEC survival
LOEC survival
LOEC
reproduction
LC50
Reduced survival,
growth and
reproduction
IC50
LC50
LC50
0.7 Dortland 1980
0.8 Dortland 1980
0.74 Mitchell 1985
0.21 Mitchell 1985
7.8 Nishiuchi and
Hashimoto 1967
80 Hashimoto and
Nishiuchi 1981
0.47 Fernandez-
Casalderrey et
al. 1994
0.15 Fernandez-
Casalderrey et
al. 1995
0.18 Fernandez-
Casalderrey et
al. 1995
0.15 Fernandez-
Casalderrey et
al. 1995
0.86 Fernandez-
Casalderrey et
al. 1995
0.05 Sanchez et al.
1998, 1999,
2000
0.45 Fort etal. 1996
80 Hashimoto and
Nishiuchi 1981
7.8 Nishiuchi and
Hashimoto 1967
50
-------
Table 6. (continued)
Species
Hardness
(mg/L as
Chemical" CaCO3) Duration Effect
Concentration
(ug/L) Reference
Cladoceran
(adult),
Moina
macrocopa
Cladoceran,
Moina
macrocopa
Copepod,
Cyclops vividis
Amphipod
(adult),
Hyalella azteca
Amphipod
(0-2 days),
Hyalella azteca
Amphipod
(2-4 days),
Hyalella azteca
Amphipod
(6-8 days),
Hyalella azteca
Amphipod
(8-10 days),
Hyalella azteca
Amphipod
(12-14 days),
Hyalella azteca
Amphipod
(16-18 days),
Hyalella azteca
Amphipod
(20-22 days),
Hyalella azteca
Amphipod
(24-26 days),
Hyalella azteca
Crayfish,
Procambams
clarkii
Stonefly
(nymph),
Pteronarcys
californicus
Technical - 3 hr LC50
Technical - 3 hr LC50
96 hr LC50
Technical 160-180 48 hr LC50
Technical 40 96 hr LC50
Technical 40 96 hr LC50
Technical 40 96 hr LC50
Technical 40 96 hr LC50
Technical 40 96 hr LC50
Technical 40 96 hr LC50
Technical 40 96 hr LC50
Technical 40 96 hr LC50
7 days BCF = 4.9
48 hr EC50
26
50
2,600
19 (measured)
6.2
4.2
4.3
4.4
3.8
4.4
4.6
4.6
10
74
Nishiuchi and
Hashimoto 1967
Hashimoto and
Nishiuchi 1981
Chatterjee and
Konar 1984
Werner and
Nagel 1997
Collyard et al.
1994
Collyard et al.
1994
Collyard et al.
1994
Collyard et al.
1994
Collyard et al.
1994
Collyard et al.
1994
Collyard et al.
1994
Collyard et al.
1994
Kanazawa 1978
Cope 1965a
51
-------
Table 6. (continued)
Species
Caddisfly
(larva),
Hydropsyche
morosa
Caddisfly
(larva),
Hydropsyche
morosa
Caddisfly
(larva),
Hydropsyche
recurvata
Caddisfly
(larva),
Hydropsyche
recurvata
Mosquito
(4th instar),
Aedes aegypti
Mosquito
(3rd-4th instar),
Culexpipiens
fatigans
Mosquito
(3rd-4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Hardness
(mg/L as
Chemical" CaCO3) Duration Effect
6hr LC50
6 hr LC50
6 hr LC50
6 hr LC50
Technical - 24 hr LC50
Technical - 24 hr LC50
Technical - 24 hr LC50
Technical - 24 hr LC50
Technical - 24 hr LC50
Technical - 24 hr LC50
Technical - 24 hr LC50
Concentration
(ug/L) Reference
2,500 Fredeen 1972
500 Fredeen 1972
>500 Freeden 1972
>500 Freeden 1972
350 Klassenetal.
1965
61 Chen etal. 1971
80 Chen etal. 1971
3.5 Yasuno and
Kerdpibule 1967
5.7 Yasuno and
Kerdpibule 1967
2.2 Yasuno and
Kerdpibule 1967
5.2 Yasuno and
Kerdpibule 1967
52
-------
Table 6. (continued)
Species
Mosquito
(4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Mosquito
(4th instar),
Culexpipiens
fatigans
Midge
(1st instar),
Chironomus
riparius
Midge
(4th instar),
Chironomus
riparius
Salmonidae
Brown Trout
(3.22g),
Salma trutta
lacustris
Cutthroat trout
(0.52 g),
Oncorhynchus
clarki
Chemical"
Technical
Technical
Technical
Technical
Technical
Technical
Analytical
(99.7%)
Analytical
(99.7%)
Emulsible
concentrate
(60%)
Hardness
(mg/L as
CaCO3) Duration
24hr
24hr
24hr
24 hr
24 hr
24 hr
96 hr
96 hr
96 hr
96 hr
96 hr
Effect
LC50
LC50
LC50
LC50
LC50
LC50
LC50 (fed)
LC50 (fed)
LC50
LC50
LC50
Concentration
(ug/L) Reference
4.6 Yasuno and
Kerdpibule 1967
4.5 Yasuno and
Kerdpibule 1967
1.9 Yasuno and
Kerdpibule 1967
1.8 Yasuno and
Kerdpibule 1967
5.4 Yasuno and
Kerdpibule 1967
3.5 Yasuno and
Kerdpibule 1967
23 Stuijfzand et al.
2000
167 Stuijfzand et al.
2000
;,000 Ciba-Geigy
1976
602
Swedberg 1973
3,850 Swedberg 1973
53
-------
Table 6. (continued)
Hardness
(mg/L as
Concentration
Species
Cutthroat trout
(2.02 g),
Oncorhynchus
clarki
Rainbow trout
(fiy),
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Rainbow trout
(16 g),
Oncorhynchus
mykiss
Rainbow trout,
Oncorhynchus
mykiss
Goldfish
(4.01 cm),
Carassius
auratus
Carp,
Cyprinus carpio
Carp (4.2 cm),
Cyprinus carpio
Carp (6.0 cm),
Cyprinus carpio
Carp (8 g),
Cyprinus carpio
Carp (1. 1-1.4 g),
Cyprinus carpio
Carp (24-35 g),
Cyprinus carpio
Fathead minnow
(larva),
Pimephales
promelas
Chemical" CaCO3) Duration Effect
96 hr LC50
Insecticidal - 96 hr LC50
soap
48 hr EC50
Synthesized - 14 days BCF = 62
Analytical 360 28 days NOEC
Technical - 48 hr LC50
7 days BCF = 65.1
Technical - 72 hr LC50
Technical - 48 hr LC50
Synthesized - 14 days BCF = 120
72 hr LC50
Reagent - 7 days BCF = 20.9
(98%)
Technical 44-49 7 days No reduction in
(88.2%) growth or
survival
(us/L) Reference
2,760 Swedberg 1973
20 Mitchell 1985
170 Cope 1965a
15 Seguchi and
Asaka 1981
200 Bresch 1991
5,100 Nishiuchi and
Hashimoto
1967;
Hashimoto and
Nishiuchi 1981
10 Kanazawa 1978
2,000 Nishiuchi and
Asano 1981
3,200 Nishiuchi and
Hashimoto
1967;
Hashimoto and
Nishiuchi 1981;
Nishiuchi and
Asano 1981
18 Seguchi and
Asaka 1981
1,420 DuttandGuha
1988
2.4 Tsudaetal. 1990
277 Norberg-King
1989
54
-------
Table 6. (continued)
Species
Chemical"
Hardness
(mg/L as
CaCO3) Duration
Effect
Concentration
(ug/L) Reference
Fathead minnow
(larva),
Pimephales
promelas
Fathead minnow
(larva),
Pimephales
promelas
Fathead minnow
(embryo-larva),
Pimephales
promelas
Fathead minnow
(newly hatched
larvae),
Pimephales
promelas
Fathead minnow
(newly hatched
larvae),
Pimephales
promelas
Fathead minnow
(embryo-larva),
Pimephales
promelas
Fathead minnow
(embryo-larva),
Pimephales
promelas
Catfish
let alums sp.
Ide
Leucisuc idus
Flagfish
(larva-juvenile),
Jordanella
floridae
Flagfish
(juvenile-adult),
Jordanella
floridae
Technical
(88.2%)
Technical
(88.2%)
Technical
(88.2%)
Encapsulated
formulation
(fresh stock)
Encapsulated
formulation
(11 week-old
stock)
Encapsulated
formulation
Encapsulated
formulation
Emulsifiable
concentrate
(60%)
Emulsifiable
concentrate
(60%)
-
~
44-49 7 days
44-49 7 days
44-49 12 days
45.8 96 hr
45.8 96 hr
45.8 32 days
45.8 32 days
96 hr
96 hr
21 -day
pulsed
dose
+ recovery
21 -day
pulsed
dose
+ recovery
Reduction in dry
weight
Reduction in dry
weight
No reduction in
growth or
survival
LC50
LC50
No effect on
weight
Significant
reduction in
weight
LC50
LC50
Decreased egg
production
Decreased
parental survival
277
347
285
6,100
5,100
40
76
8,000
150
290
250
Norberg-Kin;
1989
Norberg-Kin;
1989
Norberg-Kinj
1989
Jarvinen and
Tanner 1982
Jarvinen and
Tanner 1982
Jarvinen and
Tanner 1982
Jarvinen and
Tanner 1982
Ciba-Geigy
1976
Ciba-Geigy
1976
Allison 1977
Allison 1977
55
-------
Table 6. (continued)
Species
Chemical"
Hardness
(mg/L as
CaCO3) Duration Effect
Concentration
(ug/L) Reference
Flagfish (adult-
spawning),
Jordanella
floridae
Oriental Technical
weatherfish,
Misqurnus
anguillicaudatus
Oriental Synthesized
weatherfish
(2.6 g),
Misgurnus
anguillicaudatus
Guppy (7 wk), Technical
Poecilia
reticulata
Guppy (7 wk), Technical
Poecilia
reticulata
Guppy (7 wk), Technical
Poecilia
reticulata
Guppy, Emulsifiable
Poecilia concentrate
reticulata (60%)
Guppy,
Poecilia
reticulata
Guppy Technical
(2-3 mon), (99%)
Poecilia
reticulata
Guppy
(2-3 mon),
Poecilia
reticulata
Guppy
(2-3 mon),
Poecilia
reticulata
Bluegill,
Lepomis
macrochirus
21 -day
pulsed
dose
+ recovery
48 hr
14 days
24 hr
24 hr
30 min
96 hr
7 days
100 3 days
75 24 hr
75 7 days
48 hr
Decreased
survival of
parents and larvae
LC50
BCF = 28
LC50
LC50
Loss of
equilibrium
LC50
BCF =17.5
Lethal body
burden
Lethal body
burden
(@ 4,330 ug/L
exposure)
Lethal body
burden (@ 2,420
ug/L exposure)
EC50
1,170
500
14
3,700
3,800
7,000
3,000
10
2,495
2.1 (umol/g)
1.8 (umol/g)
30
Allison 1977
Hashimoto and
Nishiuchi 1981
Seguchi and
Asaka 1981
Chenetal. 1971
Chenetal. 1971
Chenetal. 1971
Ciba-Geigy
1976
Kanazawa 1978
Ohayo-Mitoko
andDeneer 1993
Deneer et al.
1999
Deneer et al.
1999
Cope 1965a
56
-------
Table 6. (continued)
Hardness
(mg/L as
Concentration
Species
Bluegill,
Lepomis
macrochirus
Zebrafish,
Brachydanio
rerio
Tilapia,
Tilapia sp.
Mozambique
tilapia (5-9 g),
Tilapia
mossambica
Mozambique
tilapia
(3.56g),
Tilapia
mossambica
Mozambique
tilapia (1.4 g),
Tilapia
mossambica
Experimental
stream
community
Experimental
stream
community
Experimental
pond community
Experimental
pond community
Experimental
pond community
Experimental
pond community
Chemical"
Basudin
(93%)
ELS
-
Technical
Technical
(92.5%)
Technical
(92.5%)
Technical
(88%)
Technical
(88%)
Technical
(88%)
Technical
(88%)
CaCO3) Duration
48 hr
Analytical 360
48 hr
96 hr
72 hr
170-195 84 days
170-195 112 days
70-150 70 days
70-150 70 days
70-150 70 days
70-150 70 days
Effect
LC50
200->200
LC50
LC100
LC50
LC50
Increased drift
rates for Hyalella
Reduced Hyalella
populations
NOEC for
phytoplankton
and periphyton
chlorophyll;
macrophyte
biomass
LOEC for
Cladocera,
Pentaneurcini,
Ceratopogonidae
abundance
LOEC for
zooplankton and
macroinvertebrate
taxonomic
richness
Reduced bluegill
sunfish biomass
(us/L) Reference
1,493 Li and Chen
1981
>200 Bresch 1991
1,492 Li and Chen
1981
15,850 Mustafa etal.
1982
2,280 Chatterjee and
Konar 1984
2,880 Dutt and Guha
1988
0.3 Arthur et al.
1983
5 Arthur et al.
1983
443 Giddings et al.
1996
2.4 Giddings et al.
1996
9.2 Giddings et al.
1996
22 Giddings et al.
1996
57
-------
Table 6. (continued)
Species
Experimental
pond community
Species
Natural
phytoplankton
Red alga,
Champia
parvula
Red alga,
Chondms
crispus
Rotifer,
Brachionus
plicatilis
Rotifer,
Brachionus
plicatilis
Snail,
Lacuna vincta
Snail,
Lacuna vincta
Eastern oyster,
Crassostrea
virginica
Eastern oyster
(5-10 cm
height),
Crassostrea
virginica
Eastern oyster
(6-10 cm
height),
Crassostrea
virginica
Chemical"
Technical
(88%)
Chemical"
-
(96%)
(12.5%)
(96%)
Standard
(95%)
(12.5%)
(12.5%)
~
Technical
and WC-
labeled
Technical
and WC-
labeled
Hardness
(mg/L as
CaCO3) Duration
70-150 70 days
Salinity
(g/kg) Duration
SALTWATER
4hr
48 hr
exposure
24 hr
exposure
18 day
holding
24 hr
24 hr
3hr
exposure,
48 hr
holding
3hr
exposure,
48 hr
holding
96 hr
96 hr
5 days
Effect
Reduced bluegill
sunfish survival
Effect
SPECIES
6.8% decrease in
photosynthesis
No effect on
sexual
reproduction
No effect on
growth
LC50
EC50
88% mortality
75% mortality
No decrease in
shell growth
LC50 shell
growth
BCF = 56
Concentration
Olg/L)
54
Concentration
(us/L)
1,000
1,000
10,000
55,100
28,000
1,000
10,000
1,000
1,115
100
Reference
Giddings et al.
1996
Reference
Butler 1963
Thursby &
Tagliabue 1988
Shaddock &
Croft 1981
Thursby & Berry
1988
Guzzella et al.
1997
Shacklock &
Croft 1981
Shacklock &
Croft 1981
Butler 1963;
Mayer 1987
Williams 1989
Williams 1989
58
-------
Table 6. (continued)
Salinity
Concentration
Species
Amphipod
(adult),
Ampelisea aldita
Amphipod,
Gammams
oceanicus
Amphipod
(adult),
Rhepoxynius
abronius
Isopod,
Idotea baltica
Brown shrimp,
Penaeus aztecus
Brown shrimp,
Penaeus aztecus
Grass shrimp,
Palaemonetes
pugio
White mullet,
Mugil curema
Striped mullet,
Mugil cephalus
Sheepshead
minnow,
Cyprinodon
variegatus
Chemical"
Technical
(12.5%)
Technical
(12.5%)
-
Technical
95.1% pure
Technical
95.1% pure
-
Technical
95.1% pure
92.6% pure
(g/kg) Duration
25 48 hr
3hr
exposure
31 24 hr
3hr
exposure
24hr
48 hr
48 hr
24 & 48 hr
48 hr
108 days
Effect
LC50
100% mortality
LC50
100% mortality
EC50
EC50
EC50
LC50
LC50
Decrease in
acetylcholin-
esterase activity
(ug/L)
10
1,000
9.2
1,000
44
28
28
250
150
0.47
Reference
Werner & Nagel
1997
Shacklock &
Croft 1981
Werner & Nagel
1997
Shacklock &
Croft 1981
Butler 1963
Mayer 1987
Mayer 1987
Butler 1963
Mayer 1987
Goodman et al.
1979; Mayer
1987
a Percent purity is listed in parentheses when available.
59
-------
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