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DRAFT EPA
DRAFT AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA
DIAZINON
Prepared by
University of Wisconsin-Superior
Superior, Wisconsin 54880
andGreat Lakes Environmental Center
Traverse City, Michigan 49686
Prepared forU.S. Environmental Protection Agency
Office of Water Office of Science and Technology
Health and Ecological Criteria Division Washington, D.C.
Office of Research and Development National Health and Environmental Effects Research Laboratories Duluth, Minnesota
Narragansett, Rhode Island
EPA Contract No. 68-C-98-134
Work Assignment No. 1-22
DRAFT
DRAFT AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
DIAZINON
(CAS Registry Number 333-41-5)
August 2000
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF WATER
OFFICE OF SCIENCE AND TECHNOLOGY
HEALTH AND ECOLOGICAL CRITERIA DIVISION
WASHINGTON, D.C.
OFFICE OF RESEARCH AND DEVELOPMENT
NATIONAL HEALTH AND ECOLOGICAL EFFECTS RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
NOTICES
ii
This document has been reviewed by the Health and Ecological Effects Criteria
Division, Office of Science and Technology, U.S. Environmental Protection
Agency, and approved for publication.
Mention of trade names or commercial products does not constitute endorsement
or recommendation for use.
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
iii
FOREWORD
Section 304(a)(1) of the Clean Water Act of 1977 (P.L. 95-217) requires
the Administrator of the Environmental Protection Agency to publish water
quality criteria that accurately reflect the latest scientific knowledge on
the kind and extent of all identifiable effects on health and welfare 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 upon consideration of comments received from EPA staff and independent
peer reviewers. Criteria contained in this document replace any previously
published EPA aquatic life criteria for the same pollutant(s).
The term "water quality criteria" is used in two sections of the Clean
Water Act, section 304(a)(1) and section 303(c)(2). The term has a different
program impact in each section. In section 304, the term represents a nonregulatory,
scientific assessment of ecological effects. Criteria presented
in this document are such scientific assessments. If water quality criteria
associated with specific stream uses are adopted by a state as water quality
standards under section 303, they become enforceable maximum acceptable
pollutant concentrations in ambient waters within that state. Water quality
criteria adopted in state water quality standards could have the same
numerical values as criteria developed under section 304. However, in many
situations states might want to adjust water quality criteria developed under
section 304 to reflect local environmental conditions and human exposure
patterns. Alternatively, states may use different data and assumptions than
EPA in deriving numeric criteria that are scientifically defensible and
protective of designated uses. It is not until their adoption as part of
state water quality standards that criteria become regulatory. Guidelines to
assist the states and Indian tribes in modifying the criteria presented in
this document are contained in the Water Quality Standards Handbook (U.S. EPA
1994). This handbook and additional guidance on the development of water
quality standards and other water-related programs of this agency have been
developed by the Office of Water.
This 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.
Geoffrey H. Grubbs
Director
Office of Science and Technology
iv
ACKNOWLEDGMENTS
Larry T. Brooke
(author)
University of Wisconsin-Superior
Superior, Wisconsin
Gregory J. Smith
(author)
Great Lakes Environmental Center
Columbus, Ohio
Heidi Bell
(document coordinator)
U.S. EPA
Health and Ecological
Criteria Division
Washington, D.C.
v
CONTENTS
Page
Foreword . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . iii
Acknowledgments . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . iv
Tables . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . vi
Figures . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . vi
Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 1
Acute Toxicity to Aquatic Animals . . . . . . . . . . . . . . . . . . . . . 5
Chronic Toxicity to Aquatic Animals . . . . . . . . . . . . . . . . . . . . 7
Toxicity to Aquatic Plants . . . . . . . . . . . . . . . . . . . . . . . . 11
Bioaccumulation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12
Other Data . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12
Unused Data . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 17
Summary . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 20
National Criteria . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 21
Implementation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 22
References . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 54
vi
TABLES
Page
1. Acute Toxicity of Diazinon to Aquatic Animals . . . . . . . . . . . . . 27
2. Chronic Toxicity of Diazinon to Aquatic Animals . . . . . . . . . . . . 34
3. Ranked Genus Mean Acute Values with Species Mean Acute-
Chronic Ratios . . . . . . . . . . . . . . . . . . . . . . . . . . . 36
4. Toxicity of Diazinon to Aquatic Plants . . . . . . . . . . . . . . . . 40
5. Bioaccumulation of Diazinon by Aquatic Organisms . . . . . . . . . . . 41
6. Other Data on Effects of Diazinon on Aquatic Organisms . . . . . . . . 42
FIGURES
1. Ranked Summary of Diazinon GMAVs (Freshwater) . . . . . . . . . . . . . 24
2. Ranked Summary of Diazinon GMAVs (Saltwater) . . . . . . . . . . . . . 25
3. Chronic Toxicity of Diazinon to Aquatic Animals . . . . . . . . . . . . 26
1
Introduction
Diazinon [Chemical Abstract Service registry number 333-41-5; 0,0-diethyl
0-(6-methyl-2-{1-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 soil insects such as cutworms, wireworms, and maggots
(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.
Diazinon is routinely applied to the Central, Imperial and San Joaquin Valley
agricultural areas of California (Bailey et al. 2000; Domagalski et al. 1997).
It is used extensively around households to control cockroaches, and other
insects such as flies (Farm Chemicals Handbook 2000) and ectoparasites on pets
(Bailey et al. 2000). Additional diazinon uses in urban areas include dormant
sprays on fruit trees, professional landscape and maintenance, and structural
pest control (Bailey et al. 2000)
Diazinon is an organo-phosphorus compound with the empirical formula of
C12H21N2O3PS, a molecular weight of 304.35 and has an octanol/water partition
coefficient (log Pow) of 3.40 (Hunter et al. 1985; WHO 1998). It is a
colorless oil in its purest form 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. It decomposes above 120°C
(Verschueren 1983, WHO 1998), is susceptible to oxidation above 100°C, is
stable in neutral media, but slowly hydrolyses in alkaline media and more
rapidly in acidic media (WHO 1998). If stored properly, diazinon has a shelflife
of at least three years (SOLARIS Consumer Affairs for Ortho products,
P.O. Box 5008, San Ramos, CA 94583, 1998).
Commercial formulations of diazinon contain the impurity sulfotepp
(0,0,0,0-tetraethyl dithiopyrophosphate), which has been found at levels
ranging from 0.20 to 0.71 percent of the diazinon concentrations (Meier et al.
1979). Meier et al. (1979) compared the toxicity of sulfotepp and diazinon to
four species of freshwater organisms and found sulfotepp 58 times more toxic
to fathead minnows (Pimephales 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). The authors speculated that some
of the toxicity attributed to diazinon is likely due to sulfotepp. 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
2
(Agrochemicals Handbook 1991).
Although 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), Goodman et al. (1979) reported that at the time
of their paper diazinon had not been detected in the marine environment.
However, they stated that the "potential exists for contamination of estuarine
areas via agricultural and urban runoff." 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 reaching greater
than 0.1 :g/L.
Diazinon has been detected in point source (wastewater treatment plant
effluents) and non-point source (storm water) discharges in recent years,
partially due to improved detection procedures (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 and found detectable levels in samples from
17 of the 28 facilities, primarily those facilities located in southern states
(Norberg-King et al. 1989). The authors concluded that the diazinon levels
found in several effluents were sufficiently high enough to be a contributing
factor to the toxicity observed to Ceriodaphnia dubia. The acute and chronic
C. dubia toxicity observed in other POTW final effluents has also been
attributed, in part to diazinon (Amato et al. 1992; Bailey et al. 1997;
Burkhard and Jensen 1993; Guinn et al. 1995). This pass through diazinon
toxicity present in a POTW’s final effluent could potentially cause an adverse
impact on the receiving water community. However, Ku et al. (1998a) achieved
nearly complete decomposition of diazinon within one hour in deionized water
with ozone treatment under controlled laboratory conditions at a constant pH
and temperature.
Diazinon has also been detected in storm water runoff in urban and
agricultural areas (Bailey et al. 1997, 2000; Domagalski et al. 1997; Kratzer
1999; McConnell et al. 1998; NCTOC 1993; Waller et al. 1995). Domagalski et
al. (1997) observed that in the western valley streams of the San Joaquin
River, California, diazinon concentrations peaked within hours of the
rainfall’s end, and then decreased thereafter. Diazinon was also detected in
air samples over the Mississippi River from New Orleans to St. Paul, most
closely related to use on cropland within 40 km of the river (Majewski et al.
1998). Rainfall runoff of pesticides, such as diazinon with a water
solubility exceeding 10 mg/L, can cause toxic additions of 1-2 percent to
freshwater ecosystems (Wauchope 1978), and field runoff concentrations of
diazinon have been measured up to 82 :g/L (Ritter et al. 1974). The
widespread occurrence and concern of diazinon in storm water has been
3
addressed by issuance of storm water permits for large municipalities.
The mobility of diazinon in the soil is influenced by the organic matter
(OM) and calcium 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 was enhanced when a sandy loam soil was
modified with different exogenous organic materials containing humic-like
substances relative to the unmodified sandy loam soil (Iglesias-Jimenez et al.
1997). Martinez-Toledo et al. (1993) found that the presence of 10 to 300
:g/g of diazinon in soil increased the total number of bacteria and the
population of denitrifying bacteria. However, aerobic denitrogen fixing
bacteria and dinitrogen fixation decreased initially (3 days) at diazinon
concentrations of 100 to 300 :g/g before recovering to control levels.
Nitrifying bacteria and fungal soil populations were not affected at the 10 to
300 :g/g soil exposure levels.
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. Diazinon is an exception to other
organophosphorus insecticides in that it hydrolyzes at both acidic and
alkaline pH's (Gomaa et al. 1969). In the laboratory at 20°C, the half-life
was determined to be 12, 4436 and 146 hr at the respective pH's of 3.1, 7.4
and 10.4 (Faust and Gomaa 1972). Ku et al. (1998b) found that hydrolytic
decomposition occurred only for the diazinon-H+ species present in acidic
solutions, and that breakage of the P-O bond was the major decomposition step
for the hydrolysis of diazinon. Morgan (1976) measured diazinon half-life due
to hydrolysis in well water of pH 7.4 to 7.7 and 16°C at 43.3 days.
Hydrolysis of diazinon in laboratory water at 21°C and pH of 7.3 yielded a
half-life of 171 days (Mansour et al. 1999). The breakdown of diazinon in
soils of flooded rice fields occurs at similar rates as in water and is
described in a review of the literature by Sethunathan (1973).
A third, 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 increased when using river or lake water when compared to
distilled water. Medina et al. (1999) compared the half-life of diazinon in
filtered Limon River samples under light and dark conditions and found a
shorter half-life for sunlight exposed samples (t1/2 = 31.13 days) when
compared to samples held in the dark (t1/2 = 37.19 days)
An important factor regulating the rate of microbial decomposition of
diazinon is adaptation of microbes to the chemical. Sethunathan and MacRae
(1969), Sethunathan and Pathak (1972) and Forrest et al. (1981) found a marked
4
increase in the degrading capacity of microbes when repeatedly exposed to
diazinon as compared to a single application. Parkhurst et al. (1981)
measured a degradation rate of 2 percent/day and a half-life of 39 days in
diazinon treated river water at summer temperatures.
A primary mode of toxic action of organophosphorus insecticides is
inhibition of cholinesterases present in the nervous system. The actual
toxicant may be the oxygenated homolog of diazinon - diazoxon. 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 (Hogan and
Knowles 1972). Insect enzymes efficiently convert the P:S bond to the P:O
bond thus producing the toxic oxygen homolog (Albert 1981). Crustacea very
likely have a similar ability. Insects and crustacea probably differ from
vertebrates by having a less efficient de-esterification process to remove the
oxygen homolog from their system, making them more sensitive to diazinon.
Diazinon, on prolonged storage, may became more toxic due to
transformation products. An old diazinon formulation was found to have no
diazinon, but some sulfotepp and monosulfotepp. The monosulfotepp was shown
to be 14,000 times more toxic than diazinon in one test of enzyme inhibition
(Singmaster 1990). The use of the old improperly stored diazinon formulation,
and accompanying transformation of diazinon to 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. Allender and
Britt (1994) conducted a screening program throughout Australia to determine
if a problem existed with toxic levels of breakdown products of diazinon
formulations. Of the 169 samples evaluated, only eight contained the
breakdown products O,S-TEPP and S,S-TEPP, which was directly correlated with
the presence of water in the container.
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, and the
response to public comment (U.S. EPA 1985) is necessary to understand the
following text, tables, and calculations. Whenever adequately justified, a
national criterion may be replaced by a site-specific criterion (U.S. EPA
1983a), which may include not only site-specific criterion concentrations
(U.S. EPA 1983b), but also site-specific durations of averaging periods and
site-specific frequencies of allowed excursions (U.S. EPA 1991).
Results of intermediate calculations such as Species Mean Acute Values are
given to four significant figures to prevent round-off error in subsequent
calculations, not to reflect the precision of the value. The latest
comprehensive literature search for information for this document was
conducted in November, 1999; some of the more recent information was included.
5
Data in the files of the U.S. EPA's Office of Pesticide Programs concerning
the effects of diazinon on aquatic organisms and their uses have also been
evaluated for possible use in the derivation of aquatic life criteria.
Acute Toxicity to Aquatic Animals
The acute toxicity of diazinon to freshwater animals has been determined
for 12 invertebrate species, 10 fish species and one amphibian (Table 1).
Acute values ranged from 0.20 :g/L for an amphipod, Gammarus fasciatus
(Johnson and Finley 1980; Mayer and Ellersieck 1986), to 11,640 :g/L for
planaria, Dugesia tigrina (Phipps 1988). The most sensitive organisms tested
were invertebrates in the Class Crustacea. The amphipod, G. fasciatus, had
the lowest Genus Mean Acute Value (GMAV) of 0.2 :g/L. The cladoceran,
Ceriodaphnia dubia, had the second lowest GMAV which was computed from 14
tests, ten of which were conducted by staff at the U.S. EPA-Duluth laboratory
(Norberg-King 1987; Ankley et al. 1991). Results from these 14 tests were
relatively consistent (acute values ranged from 0.25 to 0.59 :g/L) considering
that different water sources were used and organism age at test initiation
ranged from <6 hr-old to 48 hr-old. Data were included in the table when the
organisms received food during the exposure, but these data were not used to
compute a Species Mean Acute Value (SMAV) for C. dubia. Three other
cladoceran species (Daphnia magna, D. pulex, and Simocephalus serrulatus) were
tested and found to be similarly sensitive to diazinon as C. dubia with EC50s
ranging from 0.65 to 1.8 :g/L. Two species of amphipods were tested, and the
96-hr LC50s for the two amphipod species differed by a factor of 33. One
species, G. fasciatus, was the most sensitive organism tested with diazinon
and had a 96-hr LC50 of 0.20 :g/L. Hyalella azteca was also sensitive to
diazinon, with a 96-hr LC50 value of 6.51 :g/L.
The least sensitive species tested with diazinon was also an invertebrate.
The planarian, D. tigrina had the highest observed diazinon 96-hr LC50 of
11,640 :g/L. Other invertebrate species exhibiting relatively low sensitivity
to diazinon included the snail, Gillia altilis (96-hr LC50 of 11,000 :g/L),
the oligochaete worm, Lumbriculus variegatus (96-hr LC50 values of 9,980 and
6,160 :g/L, or a SMAV of 7,841 :g/L) and the apple snail, Pomacea paludosa
(96-hr LC50 values of 2,950 and 3,270 and 3,390 :g/L or a SMAV of 3,198 :g/L).
Freshwater fish species that were tested showed moderate sensitivity to
diazinon. SMAVs ranged from 425.8 :g/L for the rainbow trout, Oncorhynchus
mykiss, to 9,000 :g/L for the goldfish, Carassius auratus (Table 1). The
cutthroat trout, Oncorhynchus clarki, was considerably less sensitive (2,166
:g/L) to diazinon than rainbow trout. Rainbow trout were evaluated in five
tests with results ranging from 90 :g/L (Cope 1965b; Ciba-Geigy 1976; Johnson
and Finley 1980; Mayer and Ellersieck 1986) to 3,200 :g/L (Bathe et al.
1975a). Certain species of warmwater fish, flagfish (Jordanella floridae),
6
fathead minnow (Pimephales promelas), goldfish, and zebrafish (Brachydanio
rerio) are less sensitive to diazinon than the coldwater species, rainbow
trout, brook trout (Salvelinus fontinalis), 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. Genus
Mean Acute Values for the four most sensitive genera, all crustaceans,
differed by a factor of 7.9 (Table 3 and Figure 1). The Final Acute Value
(FAV) for freshwater organisms is 0.1925 :g/L.
The acute toxicity of diazinon to saltwater animals has been determined
for seven invertebrate species and two fish species (Table 1). SMAVs ranged
from 2.57 :g/L for the copepod, Acartia tonsa (Khattat and Farley 1976), to
>9,600 :g/L for embryos of the sea urchin, Arbacia punctulata (Thursby and
Berry 1988), a factor of about 3,735. Acute values for the mysid,
Americamysis bahia (formerly Mysidopsis bahia), from a renewal, unmeasured
test (8.5 :g/L) and from a flow-through measured test (4.82 :g/L) were
similar. Toxicity tests with copepods, mysids, amphipods (Ampelisca abdita),
grass shrimp (Palaemonetes pugio), pink shrimp (Penaeus duorarum) and inland
silversides (Menidia beryllina) demonstrated an increase in mortalities with
duration of exposure. The remaining fish species, the sheepshead minnnow
(Cyprinodon variegatus), had an LC50 value of 1,400 μg diazinon/L, 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). The saltwater FAV is 1.637 :g/L.
Chronic Toxicity to Aquatic Animals
The chronic toxicity of diazinon was determined for five freshwater
species (Table 2). A life-cycle test was conducted with C. dubia during a
seven-day exposure (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 exposures (0.063, 0.109, and 0.220 :g/L), but no
organisms survived at concentrations $0.520 :g/L. The chronic value
determined for C. dubia was 0.3382 :g/L. Division of the SMAV (0.3760 :g/L)
from ten 48-hr acute tests conducted in the same laboratory with the same
dilution water (Norberg-King 1987; Ankley et al. 1991) by the chronic value
(0.3382 :g/L) results in an Acute-Chronic Ratio (ACR) of 1.112 for C. dubia.
Allison and Hermanutz (1977) exposed brook trout adults to diazinon for
six to eight months and then exposed their progeny for an additional 122 days
and observed effects. After 173 days of exposure, survival was reduced at 9.6
:g/L and deformities were seen at 4.8 :g/L. However, when these fish spawned
there were no differences in the number of eggs produced per female or the
viability of these eggs. Continued exposure of the progeny showed measurable
7
effects at 30 days, but at 122 days post-hatch, all exposure concentrations
had significantly shorter total lengths and lighter weights. The chronic
value was <0.8 :g/L which was the lowest exposure concentration for the
progeny. Division of the SMAV (723.0 :g/L) from three 96-hr acute tests
(Allison and Hermanutz 1977) by the chronic value (<0.8 :g/L) results in an
ACR of >903.8.
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 of test fish exposed to only the highest
exposure concentration of 285 :g/L were significantly different from that of
the control fish. Total length was significantly affected at concentrations
$160 :g/L and dry weight was significantly reduced at 37.8 :g/L, but not at
16.5 :g/L. Based upon dry weight, the chronic value for the test was 24.97
:g/L. Division of the 96-hr LC50 (9,350 :g/L) from another group of
researchers (University of Wisconsin-Superior 1988) at the same laboratory
using the same water supply and the same genetic stock of fish by the chronic
value of 24.97 :g/L results in an ACR of 374.4.
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
:g/L, and reduced weight (10.1 percent reduction) at 90 :g/L, but no weight
difference from the control fish at 50 :g/L. The chronic value for fathead
minnows in the test was 67.08 :g/L based upon reduced weight. Division of the
96-hr acute value of 6,900 :g/L from a flow-through and measured toxicant
concentration test (Jarvinen and Tanner 1982) by the chronic value of 67.08
:g/L results in an ACR of 102.9. The geometric mean of 374.4 and 102.9 is
196.3, which is the species mean acute-chronic ratio for fathead minnows.
Flagfish were exposed to diazinon through one and one-half generations
(Allison 1977). The study began with one-day-old larvae and continued through
spawning, which occurred at about 60 days, then continued with the fish
progeny for 35 days post-hatch. An effect was seen with the parents at 61
days of exposure. The average wet weight of the males was significantly
reduced from that of the control fish at diazinon concentrations #88 :g/L.
Only two male fish were exposed per treatment and there was a 23.3 percent
reduction in wet weight in the 88 :g/L exposure. However, weights of the four
female fish from each treatment were not significantly reduced at any exposure
concentration even though fish in the highest exposure concentration was
reduced in average weight by 21.4 percent. Effects on the progeny were then
observed and the only effect seen at hatching was a reduction in the
incubation time at all exposure concentrations. At 35 days post-hatch, or a
total exposure time of 96 days, significant reductions in average wet weight
were measured at all exposure concentrations. Therefore, the flagfish chronic
value was <14 μg/L. Division of the SMAV for flagfish of 1,643 :g/L, which is
8
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 of <14 :g/L, results in an
ACR of >117.4.
Bresch (1991) evaluated the chronic toxicity of diazinon to zebrafish
(early life-stage test). Zebrafish eggs (approximately 2-3 hr after spawning)
through juveniles were exposed to diazinon concentration of 8, 40 and 200 :g/L
for 42 days under flow-through measured conditions. Survival and growth of
the three treatment groups were not statistically different (p<0.05) from the
controls. Thus, the zebrafish chronic value was >200 :g/L. An acute-chronic
ratio could not be estimated because a suitable acute test value is not
available.
The chronic toxicity of diazinon for saltwater organisms has been
determined in a life cycle test with the mysid, A. bahia, and a partial lifecycle
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 between the highest concentration tested (4.4
:g/L) and the controls (although there was only 28 percent survival at the
highest concentration). Mysid reproduction was not significantly reduced in
diazinon concentrations #2.1 :g/L, and only the 4.4 :g/L exposure
concentration exhibited significantly reduced reproduction when compared to
controls. Based on these observations, the chronic limits were 2.1 and 4.4
:g/L, and the resultant chronic value for the mysid was 3.040 :g/L. A
corresponding flow-through measured acute value of 4.82 :g/L (Nimmo et al.
1981) yielded an ACR of 1.586.
Sheepshead minnow reproduction was significantly reduced in all diazinon
exposure concentrations observed 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 :g diazinon/L average measured concentrations were 69, 50, 50, 55 and
45 percent of control fish, respectively. Acetylcholinesterase activity in
fish exposed to 0.47 :g/L was consistently less than control fish levels, and
levels averaged 71 percent inhibition in the 6.5 :g/L exposure. Neither
survival nor growth were affected in #6.5 :g/L exposures to diazinon. The
chronic value for sheepshead minnow was <0.47 :g/L, and when coupled with the
96-hr acute value of 1,400 :g/L by the same author, the resultant ACR for this
fish was >2,979.
Chronic toxicity tests have been conducted on seven aquatic species and
chronic values ranged from 0.34 :g/L for C. dubia to >200 :g/L for rainbow
trout and zebrafish (Table 2 and Figure 3). The chronic values for sheepshead
minnows (<0.47 :g/L) and brook trout (<0.8 :g/L) cannot be determined
accurately because all concentrations tested adversely affected reproduction.
Alternatively, an effect level on either survival or growth could not be
9
determined for zebrafish (>200 :g/L). Acute-chronic ratios for acutely
sensitive crustacean invertebrates were 1.586 for mysids and 1.112 for C.
dubia. In contrast, ratios are markedly higher for relatively acutely
insensitive fishes; >117.4 for flagfish, 102.9 and 374.4 for fathead minnows,
>903.8 for brook trout and >2,979 for sheepshead minnows.
Three valid acute-chronic ratios are available for diazinon using the
second and seventeenth (Table 3) most sensitive tested species of freshwater
animals and the third most sensitive saltwater animal. Two acute-chronic
ratios are available for the fathead minnow, which differ by a factor of
approximately 3.6 times. The geometric mean of these two values is 196.3.
The cladoceran C. dubia has an acute-chronic ratio of 1.112 when using the
data provided by the U.S. EPA Duluth laboratory (Norberg-King 1987 and Ankley
et al. 1991), which was very similar to the mysid acute-chronic ratio of 1.586
(Nimmo et al. 1981). An apparent pattern displayed by the data reviewed shows
that a number of invertebrate species (especially crustacea) are acutely
sensitive to diazinon, but have a low (<2) acute-chronic ratio. In contrast,
most fish species are generally acutely insensitive to diazinon, but have high
(>100) acute-chronic ratios. Another pattern observed was that the chronic
fish studies conducted with reagent grade diazinon all had relatively high
chronic values (>200 μg/L), and those conducted with technical grade diazinon
all had lower chronic values (>70 μg/L). Although there are a limited number
of chronic fish studies presented, this apparent pattern would suggest that
other toxic impurities may be present in the technical material.
Although the three valid acute-chronic ratios vary by more than a factor
of ten (by a factor of 177), the Guidelines (Stephen 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 2).
Therefore, only the acutely sensitive C. dubia and A. bahia were used to
calculate the FACR of 1.328. The Guidelines also stipulate, 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. Thus the FACR for
diazinon is 2.0. It appears from available data (Fig. 3) that all tested
freshwater species will be protected from adverse effects due to diazinon by
the freshwater Chronic Value. Saltwater fish species may not be protected by
the established saltwater Chronic Value, and the FCV for salt water species is
lowered to 0.40 μg/L to protect the sheepshead minnow.
Toxicity to Aquatic Plants
Acceptable data on the effects of diazinon to freshwater algae are
10
available for one species (Table 4), but no acceptable data are available
concerning toxicity to freshwater vascular plants. Hughes (1988) exposed the
green alga, Selenastrum capricornutum, for seven days in a static, measured
toxicant concentration test. An EC50 of 6,400 :g/L was determined based upon
reduced cell numbers. No saltwater tests with plants are suitable, according
to the Guidelines, for inclusion in this section. Some freshwater and
saltwater information is included with "Other Data."
Based upon a single aquatic plant test, the Final Plant Value for diazinon
is 6,400 :g/L.
Bioaccumulation
Three freshwater species of fish, rainbow trout, carp (Cyprinus carpio)
and a guppy (Poecilia reticulata), were exposed to diazinon for 14 days and
the whole body tissue loadings determined (Seguchi and Asaka 1981; Keizer et
al. 1993). Diazinon accumulated rapidly in each study, and reached a plateau
approximately in three days. The bioconcentration factor (BCF) for rainbow
trout and carp exposed to 15 :g diazinon/L was 62 and 120, respectively (Table
5). The half-life for diazinon in these fish was less than seven days. The
guppy was exposed to 350 :g diazinon/L for 14 days, which yielded a BCF value
of 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 :g/L were 147, 147 and 213, respectively (Table 5).
No U.S. FDA action level or other maximum acceptable concentration in
tissue, as defined in the Guidelines, is available for diazinon. Therefore,
the Final Residue Value cannot be calculated.
Other Data
Additional data on the lethal and sublethal effects of diazinon for
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. Data seem to vary greatly for several species of single celled
green plants and diatoms. The green algal species, Chlorella ellipsoidea and
Chlamydomonas sp., were affected only at concentrations of 100,000 :g/L. The
green algae Scenedesmus quadricauda was not affected at 1,000 :g/L, but a
mixture of green alga and diatoms had reduced growth at <10 :g/L (Butler et
al. 1975a). From Table 4, the green alga Selenastrum capricornutum showed
adverse reproduction at 6,400 :g/L. Duckweed (Wolffia papulifera) had 100
percent mortality at 100,000 :g/L saturation and developed deformities at
11
10,000 :g/L in 11-day exposures (Worthley and Schott 1971). Various tested
species of protozoans demonstrated low sensitivity to diazinon compared to
crustacean and vertebrate species. Adverse affects were reported for
protozoans from .3,000 :g/L (Evtugyn et al. 1997) to 29,200 :g/L (Fernandez-
Casalderrey et al. 1992b). In contrast, the rotifer Brachionus calyciflorus,
was investigated by Fernandez-Casalderrey (1992a,b,c,d) and found to be
substantially less sensitive than cladocerans and insects to diazinon with
respect to survival (24-hr LC50 of 29,220 :g/L), filtration and ingestion
rates (50 percent reduction at 14,000 :g/L), reproduction (decreased
reproduction at <5,000 :g/L), and median lethal time effects (LT50 values
ranged from 2.5 to 4 days for 14,000 and 5,000 :g/L, respectively). Juchelka
and Snell (1994) estimated a 48-hr ingestion rate NOEC of 20,000 :g/L for B.
calyciflorus, and Snell and Moffat (1992) calculated a reproductive NOEC of
8,000 :g/L. Chatterjee and Konar (1984) observed a 96-hr LC50 of 2,220 :g/L
for the tubificid worm, Branchiura sowerbyi. A snail species (Physa acuta)
had a 48-hr LC50 of 4,800 :g/L which is near the upper end of the range of
fish 96-hr LC50s (Hashimoto and Nishiuchi 1981).
Dortland (1980) conducted a series of tests with the cladoceran, Daphnia
magna, and found in one exposure that 0.2 :g/L did not affect the organisms
during the 21-day exposure, but 0.3 :g/L reduced reproduction and mobility.
In four other 21-day tests in which the test organisms were fed, the EC50s
ranged from 0.22 to 0.8 :g/L. D. magna 21-day unmeasured renewal tests
conducted by Fernandez-Casalderrey et al. (1995) yielded survival NOEC and
LOEC effect levels of 0.15 :g/L and 0.18 :g diazinon/L, respectively. The
mean total young per female and mean brood size were both significantly
reduced at the 0.15 :g/L (lowest exposure) concentration when compared to the
controls.
Amphipods are usually very sensitive to diazinon. 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 :g/L. One exception to
the normally sensitive amphipod was the 96-hr LC50 of 200 :g diazinon/L
determined for Gammarus lacustris by Sanders (1969).
Mosquito larvae appear to be about as sensitive to diazinon as cladocerans
and amphipods. Yasuno and Kerdpibule (1967) exposed mosquito larvae, Culex
pipiens fatigans, to diazinon in 24-hr exposures and measured LC50s ranging
from 1.8 to 5.7 :g/L. Caddisfly larvae have been exposed to diazinon in 6-hr
exposures (Fredeen 1972). The results were highly variable with LC50s ranging
from 500 to 2,500 :g/L for Hydropsyche morosa, and >500 :g/L for H. recurvata.
It is difficult to predict the LC50 values at exposure durations longer than 6
hr, but it is likely that caddisfly LC50 values would be considerably lower
than 500 :g/L if exposed to diazinon for longer time periods. A species of
stonefly, Pteronarcys californicus, was exposed for 48 hr and had an EC50 of
12
74 :g/L (Cope 1965a), which again shows insects to be quite sensitive to
diazinon. In contrast, the rotifer Brachionus calyciflorus, was investigated
by Fernandez-Casalderrey (1992a,b,c,d) and found to be substantially less
sensitive than cladocerans and insects to diazinon with respect to survival
(24-hr LC50 of 29,220 :g/L), filtration and ingestion rates (50 percent
reduction at 14,000 :g/L), reproduction (decreased reproduction at <5,000
:g/L), and median lethal time effects (LT50 values ranged from 2.5 to 4 days
for 14,000 and 5,000 :g/L, respectively).
Rainbow trout fingerlings were exposed to diazinon concentration of 8, 40
and 200 :g/L under flow-through measured 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
resultant chronic value for rainbow trout was >200 :g/L diazinon.
Rainbow trout were also exposed to an insecticidal soap formulation of
diazinon for 96 hr and an unspecified form of diazinon for 48 hr, and the
resultant LC50s were 20 and 170 :g/L, respectively. Cutthroat trout of two
sizes were exposed to diazinon for 96 hr which resulted in LC50s of 3,850 :g/L
for the smaller and 2,760 :g/L for the larger fish. The LC50s for rainbow
trout and cutthroat 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 :g/L for an unspecified
formulation of diazinon.
Goldfish and carp are relatively tolerant of diazinon in acute exposures,
but newly hatched fathead minnow larvae were found to be sensitive to the
technical form of diazinon in seven-day exposures (Norberg-King 1989).
Jarvinen and Tanner (1982) exposed fathead minnows to an encapsulated
formulation of diazinon in acute and chronic exposures. The encapsulated
formulation was less toxic (5,100 and 6,100 :g/L) than the technical grade
(2,100 and 4,300 :g/L; Table 1) in 96-hr exposures. They obtained a chronic
value of 55.14 :g/L, based upon reduction in weight in embryo-larval 32-day
exposures with the encapsulated formulation. The fathead minnow acute-chronic
ratio for the encapsulated formulation is 101.6 which is similar to the acutechronic
ratio of 102.9 for the technical grade chemical (Table 2) with this
species.
Allison (1977) exposed flagfish, J. floridae, in a 21-day pulsed dose
exposure with diazinon followed by a period without the chemical to observe
effects. Exposure of the parental stock beginning at hatch and lasting 21
days resulted in decreased egg production by the females at concentrations
$290 :g/L. Exposure to diazinon for 21 days just prior to spawning resulted
in decreased parental survival at concentrations $250 :g/L, but there were no
effects upon reproduction at the 250 and 450 :g/L exposure concentrations.
Exposure of adults to diazinon for 21 days once spawning had been initiated
resulted in decreased survival of the parents at the highest exposure
13
concentration (1,170 :g/L), and reduced survival of larval progeny at 1,170
:g/L.
Chen et al. (1971) exposed the guppy, P. reticulata, to diazinon and
measured 24-hr LC50s of 3,700 and 3,800 :g/L. These values were in agreement
with the work of Ciba-Geigy (1976) which measured a 96-hr LC50 of 3,000 :g/L
for the same fish species. Ohayo-Mitoko and Deneer (1993) estimated a lethal
body burden of 2,495 :g 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. macrochirus, were 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 of 30 :g/L), whereas
the work of Li and Chen (1981) indicate intermediate sensitivity (48-hr LC50
of 1,493 :g/L) relative to other fish species.
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).
Other data on the lethal and sublethal effects of diazinon on saltwater
species (Table 6) did not indicate greater sensitivities than indicated
previously. Saltwater algae appear to be less sensitive to diazinon than
aquatic animals. Photosynthesis of natural phytoplankton was essentially
unaffected by a 4-hr exposure to 1,000 :g/L (Butler 1963). There was no
effect of diazinon at 1,000 :g/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 :g diazinon/L had no effect on the growth of
the alga in a subsequent 18-day grow-out period (Shacklock and Croft 1981).
Rotifers, Brachionis plicatilis, were also not acutely sensitive to diazinon
(Thursby and Berry 1988). Growth of eastern oysters, Crassostrea virginica,
was not reduced in a diazinon exposure of 1,000 :g/L (Butler 1963). Shacklock
and Croft (1981) showed that two days after a 3-hr exposure to 1,000 :g
diazinon/L, 100 percent of the amphipod, Gammarus oceanicus, and the isopod,
Idotea baltica, as well as 88 percent of the saltwater snail, Lacuna vincta,
test organisms were dead. The 48-hr EC50 of diazinon to grass shrimp,
Palaemonetes pugio, was 28 :g/L (Mayer 1987). The brown shrimp, Penaeus
aztecus, had a 24-hr EC50 of 44 :g/L (Butler 1963) and a 48-hr EC50 of 28 :g/L
(Mayer 1987). The 24- and 48-hr LC50s for the white mullet, Mugil curema,
were both 250 :g/L.
An aquatic microcosm study was conducted by Giddings et al. (1996) with
technical grade diazinon to measure the effects of a range of diazinon
exposure regimes to many taxonomic groups under simulated field conditions,
14
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 level
plus two controls. The amounts of diazinon added during each application
corresponded to theoretical concentrations from 2.0 :g/L to 500 :g/L. The
most sensitive ecological components of the microcosms were Cladocera
(zooplankton), and Pentaneurini and Ceratopogonidae (chironomid insects),
which were reduced at all treatment levels. Effects on many zooplankton and
macroinvertebrate taxa occurred at diazinon concentrations (time-weighted
averages) of 9.2 :g/L and higher. Total fish biomass was reduced at 22 :g/L
and higher, and fish survival was reduced at 54 :g/L and higher. Odonates,
some dipterans, and plants were not adversely affected by diazinon at 443
:g/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 (4.3 μg/L) in the microcosms (70-d timeweighted
average) was near the 10th percentile of single species LC50 values.
Outdoor experimental channels at EPA’s Monitcello Ecological Research
Station (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 channels as low and high treatments. The low and high
treatment channels were continuously dosed at either 0.3 or 3 :g/L nominal
diazinon concentrations for 12 weeks, then increased to 6 and 12 :g/L nominal
diazinon levels for four weeks, and finally the high treatment was increased
to 30 :g/L and the low treatment channel returned to ambient. Only the first
12 week dosing regime achieved nominal diazinon levels (0.3 and 3 :g/L) as
indicated by analytical measurements, the latter two dosing regimes did not
reach the intended levels. No consistent interchannel differences were
observed in total macroinvertebrate abundance or in species diversity indices.
Hyalella was the most sensitive species encountered, exhibiting substantially
higher (5 to 8 times) drift rates in the 0.3 :g diazinon/L dosed channel
relative to the control channel, and had sharply reduced population levels at
diazinon concentrations as low as 5 :g/L. Macroinvertebrate diazinon
tolerance from most tolerant to least tolerant 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 sensitive.
Unused Data
15
Some data concerning the effects of diazinon on aquatic organisms and
their uses were not used because the tests were conducted with species that
are not resident in North America or because the test species was not obtained
from a wild population in North America and was not identified well enough to
determine whether it is resident in North America (e.g., Alabaster 1969; Alam
and Maughan 1993; Alam et al. 1995; Anees 1974, 1976, 1978; Arab et al. 1990;
Asaka et al. 1980; Bajpai and Perti 1969; Boumaiza et al. 1979; Ceron et al.
1996a,b; Chu and Lau 1994; El-Elaimy et al. 1990; Ferrando et al. 1991; Hamm
et al. 1998; Hidaka et al. 1984; Hirayama and Tamanoi 1980; Hirose and
Kawakami 1977; Hirose and Kitsukama 1976; Hirose et al. 1979; Iqbal et al.
1992; Kabir and Ahmed 1979; Kabir and Begum 1978; Kanazawa 1975, 1980,
1981a,b, 1983a; Khalaf-Allah 1999; Kikuchi et al. 1992; Kimura and Keegan
1966; Kobayashi et al. 1993; Miah et al. 1995; Morale et al. 1998; Niforos and
Lim 1998; Nishiuchi and Yoshida 1972; Rompas et al. 1989; Sakr and Gabr 1992;
Sakr et al. 1991; Sancho et al. 1992a,b, 1993a,b, 1994; Setakana and Tan 1991;
Shigehisa and Shiraishi 1998; Sinha et al. 1987; Stevens 1991, 1992; Stevens
and Warren 1992; Tsuda et al. 1989, 1992, 1995a,b, 1997a,b; Uno et al. 1997;
Van der Geest et al. 1999; Yasutomi and Takahashi 1987). Results (e.g.
Kuwabara et al. 1980) of tests conducted with brine shrimp, Artemia sp., were
not used because these species are from a unique saltwater environment.
Bay et al. 1993; Connolly 1985; Dyer et al. 1997; Eisler 1986; Garten and
Trabalka 1983; Kaiser et al. 1997; Kanazawa 1982; Kenaga 1979, 1982; Robinson
1999; Roex et al. 2000; Sanchez et al. 1998; Steen et al. 1999; Van der Geest
et al. 1997; Vighi and Calamari 1987; Vittozzi and DeAngelis 1991; Yoshioka et
al. 1986; Zaroogian et al. 1985a,b compiled data from other sources. 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; Chatterjee 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).
Data were not used when diazinon was a component of a drilling mud,
effluent, fly ash, mixture, formulation, sediment, or sludge (e.g., Alam and
Maughan 1992; Amato et al. 1992; Bailey et al. 1996, 2000; Bathe et al. 1975a,
b; Bishop et al. 1999; Burchfield and Storrs 1954; Burkhard and Jenson 1993;
Deanovic et al. 1996, 1997; Dennis et al. 1979a,b; DeVlaming et al. 2000;
Doggett and Rhodes 1991; Duursma and Hanafi 1975; Foe 1995; Foe et al. 1998;
Glass et al. 1995; Gruber and Munn 1998; Hashimoto et al. 1982; Hatakeyama et
al. 1997; Hendriks et al. 1998; Hilsenhoff 1959; Kikuchi et al. 1996; Kuivila
and Foe 1995; LaBrecque et al. 1956; Larsen et al. 1998; Lehotay et al. 1998;
McLeay and Hall 1999; Macek 1975; Malone and Blaylock 1970; Matsuo and Tamura
1970; Mazidji et al. 1990; Mulla et al. 1963; Nishiuchi 1977; Pan and Dutta
1998; Rettich 1979; Singh 1973; Steinberg et al. 1992; Tripathi 1992; Tsuda et
al. 1997a,b; Verma et al. 1982; Werner et al. 2000; Wong 1997; Wong and Chang
16
1988), unless data were available to show that the toxicity was the same as
diazinon alone. Anjum and Siddiqui 1990; Ansari and Kumar 1988; Ariyoshi et
al. 1990; Burbank and Snell 1994; Christensen and Tucker 1976; Dutta et al.
1992a,b, 1993, 1994, 1997; Dyer et al. 1993; Fujii and Asaka 1982; Garrood et
al. 1990; Hiltibran 1974, 1982; Keizer et al. 1995; Kraus 1985; Mitsuhashi et
al. 1970; Moore and Waring 1996; Olson and Christensen 1980; Qadri and Dutta
1995; Sastry and Malik 1982a,b; Sastry and Sharma 1980, 1981; Vigfusson et al.
1983; Weiss 1959, 1961; Weiss and Gakstater 1964; Whitmore and Hodges (1978)
exposed plasma, enzymes, excised or homogenized tissue, tissue extracts, or
cell cultures. Tests conducted without controls or with too few test
organisms were not used (e.g., Applegate et al. 1957; Devillers et al. 1985;
Federle and Collins 1976). Data of Norland et al. (1974) were not used
because it was derived using organisms preconditioned to organophosphorus
chemicals.
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 watermiscible
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.
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).
Summary
The acute toxicity of diazinon to freshwater organisms was determined for
17
12 invertebrate species, 10 fish species and one amphibian (Figure 1). Eight
of the invertebrate species (two insects and six crustaceans) were the most
sensitive organisms tested (0.20 to 25 :g/L) and one invertebrate species
(planarian) was the most tolerant species tested (11,640 :g/L). Freshwater
fish were intermediate in sensitivity to the two groups of invertebrates.
Rainbow trout (Oncorhynchus mykiss) was the most sensitive fish (425.8 :g/L),
and goldfish (Carassius auratus) was the most tolerant fish tested (9,000
:g/L). No relationships have been demonstrated between water quality
characteristics such as hardness and toxicity. The freshwater Final Acute
Value is 0.1925 :g/L.
Six chronic exposures were conducted with five species of freshwater
organisms (Figure 3). Chronic values ranged from 0.3382 to >200 :g/L, and the
Acute-Chronic Ratios (ACRs) ranged from 1.112 for Ceriodaphnia dubia to >903.8
for brook trout (Salvelinus fontinalis). The Final Acute-Chronic Ratio for
diazinon was derived using two ACR’s for tested species near the FAV because
the ACR’s decreased with SMAV’s. Because the computed FACR was less than 2.0
indicating that the organisms may have become acclimated to diazinon during
the study, the value was changed to 2.0. Thus, the freshwater Final Chronic
Value (FCV) for diazinon is 0.0963 μg/L (FAV ÷ FACR, or 0.1925 μg/L ÷ 2.0 =
0.0963 μg/L).
The acute toxicity of diazinon to saltwater organisms was determined for
nine species, of which seven were invertebrates (Figure 2). Five of the
invertebrates were crustaceans and the most sensitive species tested (2.57 to
21 :g/L) and two species (an annelid and an echinoderm) were the most tolerant
species tested (>2,880 and >9,600 :g/L, respectively). Two species of
saltwater fish were tested and they were intermediate in sensitivity with
acute values of 1,170 and 1,470 :g/L. The saltwater Final Acute Value is
1.637 :g/L.
Chronic values were determined for two species of saltwater organisms.
The mysid, Americamysis bahia, and the sheepshead minnow, Cyprinodon
variegatus, had chronic values of 3.040 and <0.47 :g/L, respectively (Figure
3). ACRs were 1.586 and >3,128 for the mysid and sheepshead minnow,
respectively. The Final Acute-Chronic Ratio for diazinon is 2.0 (see previous
text). Thus, the saltwater Final Chronic Value (FCV) for diazinon is 0.8185
μg/L (FAV ÷ FACR, or 1.637 μg/L ÷ 2.0 = 0.8185 μg/L). The FCV for salt water
is lowered to 0.4 :g/L to protect the important sheepshead minnow.
Only one acceptable test with a freshwater algal species (Selenastrum
capricornutum) was conducted, 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 upon this single test, the Final Plant Value is 6,400 :g/L.
Bioaccumulation of diazinon was measured in three species of freshwater
fish and steady-state levels were reached in about three days.
18
Bioconcentration factors of 62, 120 and 188 were determined for rainbow trout,
carp (Cyprinus carpio) and guppies (Poecilia reticulata), respectively. The
tissue half-life 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 and had a mean bioconcentration factor of 169
times the concentration in water. No U.S. FDA action level or other maximum
acceptable concentration in tissue, as defined in the Guidelines, is available
for diazinon. Therefore, the Final Residue Value cannot be calculated.
National Criteria
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 0.10 μg/L more than once every three years on
the average and if the four-day average concentration of diazinon does not
exceed 0.10 μg/L more than once every three years on the average.
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" (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 μg/L more than once every three years on
the average and if the four-day average concentration of diazinon does not
exceed 0.40 μg/L more than once every three years on the average. 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.
Implementation
As discussed in the Water Quality Standards Regulation (U.S. EPA 1983a)
and the Foreword to this document, a water quality criterion for aquatic life
has regulatory impact only after it has been adopted in a state water quality
standard. Such a standard specifies a criterion for a pollutant that is
consistent with a particular designated use. With the concurrence of the U.S.
EPA, states designate one or more uses for each body of water or segment
thereof and adopt criteria that are consistent with the use(s) (U.S. EPA
1983b, 1987). In each standard a state may adopt the national criterion, if
one exists, or, if adequately justified, a site-specific criterion. (If the
19
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 1983b), 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 differing rates. Therefore, if
adequate justification is provided, site-specific and/or pollutant-specific
concentrations, durations, and frequencies may be higher or lower than those
given in national water quality criteria for aquatic life.
Use of criteria, which have been adopted in state water quality standards,
for developing water quality-based permit limits and for designing waste
treatment facilities requires selection of an appropriate wasteload allocation
model. Although dynamic models are preferred for the application of these
criteria (U.S. EPA 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).
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
% Rank GMAVs
0.01
0.1
1
10
100
1000
104
105
Diazinon Effect Concentrations (μg/L)
Figure 1. Ranked Summary of Diazinon GMAVs
Freshwater
Fish
Invertebrates
Amphibians
Freshwater Final Acute Value = 0.1925 μg/L Diazinon
Criteria Maximum Concentration = 0.0963 μg/L Diazinon
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
% Rank GMAVs
0.1
1
10
100
1000
104
Diazinon Effect Concentrations (μg/L)
Figure 2. Ranked Summary of Diazinon GMAVs
Saltwater
Fish
Invertebrates
Saltwater Final Acute Value = 1.637 μg/L Diazinon
Criteria Maximum Concentration = 0.8185 μg/L Diazinon
0.00 0.15 0.30 0.45 0.60 0.75 0.90
% Rank Genus Mean Chronic Value
0.01
0.1
1
10
100
1000
Chronic Value (μg/L)
Figure 3. Chronic Toxicity of Diazinon to Aquatic Animals
Freshwater Invertebrates
Freshwater Fish
Saltwater Invertebrates
Saltwater Fish
Saltwater Final Chronic Value = 0.40 μg/L Diazinon
Freshwater Final Chronic Value = 0.0963 μg/L Diazinon
Table 1. Acute Toxicity of Diazinon to Aquatic Animals
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
FRESHWATER SPECIES
Planaria,
Dugesia tigrina
S, M Technical
(85%)
46.5-
47.5
11,640 11,640 Phipps 1988
Oligochaete worm,
Lumbriculus
variegatus
S, M Technical
(85%)
46-48 9,980 - Phipps 1988
Oligochaete worm,
Lumbriculus
variegatus
S, U Technical
(95%)
42-47 6,160 7,841 Ankley and Collyard
1995
Snail (2.4 g),
Gillia altilis
S, U Technical
(89%)
22-35 11,000 11,000 Robertson and
Mazzella 1989
Apple snail (1-day),
Pomacea paludosa
F, M Technical
(87%)
130.5 2,950 - Call 1993
Apple snail (7-days),
Pomacea paludosa
F, M Technical
(87%)
219 3,270 - Call 1993
Apple snail (7-days),
Pomacea paludosa
F, M Technical
(87%)
173.5 3,390 3,198 Call 1993
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
40 0.57c,d - Norberg-King 1987
Table 1. (continued)
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
45 0.66c,d - Norberg-King 1987
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
40-48 0.57c,d - Norberg-King 1987
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- >1.0c,d - Norberg-King 1987
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
40 >0.6d - Norberg-King 1987
Cladoceran (<6 hr),
Ceriodaphnia dubia
S, M Technical
(85%)
40 0.66c,d - Norberg-King 1987
Cladoceran (<48 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.35 - Norberg-King 1987
Cladoceran (<48 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.35 - Norberg-King 1987
Cladoceran (<6 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.25 - Norberg-King 1987
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.33 - Norberg-King 1987
Cladoceran (<48 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.35 - Norberg-King 1987
Table 1. (continued)
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Cladoceran (<48 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.59 - Norberg-King 1987
Cladoceran (<48 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.43 - Norberg-King 1987
Cladoceran (<48 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.35 - Norberg-King 1987
Cladoceran (<48 hr),
Ceriodaphnia dubia
S, U Technical
(85%)
- 0.36 - Norberg-King 1987
Cladoceran (<48 hr),
Ceriodaphnia dubia
S, U Technical
(95%)
40-48 0.5 - Ankley et al. 1991
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, M Analytical
(99%)
80-100 0.58 - Bailey et al. 1997
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, M Analytical
(99%)
80-100 0.48 - Bailey et al. 1997
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, M Analytical
(99%)
80-100 0.26 - Bailey et al. 1997
Cladoceran (<24 hr),
Ceriodaphnia dubia
S, M Analytical
(99%)
80-100 0.29 0.3773 Bailey et al. 1997
Cladoceran (<20 hr),
Daphnia magna
S, U Technical 50 0.96 - Vilkas 1976
Table 1. (continued)
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Cladoceran (<24 hr),
Daphnia magna
S, U Analytical 200 1.5 - Dortland 1980
Cladoceran (<48 hr),
Daphnia magna
S, U Technical
(95%)
40-48 0.8 1.048 Ankley et al. 1991
Cladoceran (first
instar),
Daphnia pulex
S, U Technical
(89%)
47 0.90 - Cope 1965a; Sanders
and Cope 1966
Cladoceran (first
instar),
Daphnia pulex
S, U Technical
(89%)
47 0.8 - Johnson and Finley
1980; Mayer and
Ellersieck 1986
Cladoceran (<48 hr),
Daphnia pulex
S, U Technical
(95%)
40-48 0.65 0.7764 Ankley et al. 1991
Cladoceran (first
instar),
Simocephalus
serrulatus
S, U Technical
(89%)
47 1.8 - Cope 1965a; Sanders
and Cope 1966; Mayer
and Ellersieck 1986
Cladoceran (first
instar),
Simocephalus
serrulatus
S, U Technical
(89%)
47 1.4 1.587 Sanders and Cope
1966; Johnson and
Finley 1980; Mayer
and Ellersieck 1986
Table 1. (continued)
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Amphipod (mature),
Gammarus fasciatus
S, U Technical
(89%)
44 0.20 0.20 Johnson and Finley
1980; Mayer and
Ellersieck 1986
Amphipod (7-14 days),
Hyalella azteca
S, U Technical
(95%)
42-47 6.51 6.51 Ankley and Collyard
1995
Stonefly (larva 30-35
mm), Pteronarcys
californica
S, U Technical
(89%)
47 25 25 Cope 1965a; Sanders
and Cope 1968;
Johnson and Finley
1980; Mayer and
Ellersieck 1986
Midge (third instar),
Chironomus tentans
S, U Technical
(95%)
42-47 10.7 10.7 Ankley and Collyard
1995
Cutthroat trout (2.0
g), Oncorhynchus
clarki
S, U Technical
(92%)
162 1,700 - Johnson and Finley
1980; Mayer and
Ellersieck 1986
Cutthroat trout (2.0
g), Oncorhynchus
clarki
S, U Technical
(92%)
44 2,760 2,166 Mayer and Ellersieck
1986
Rainbow trout (3.7
cm),
Oncorhynchus mykiss
S, U Technical - 400 - Beliles 1965
Table 1. (continued)
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Rainbow trout (1.20
g),
Oncorhynchus mykiss
S, U Technical
(89%)
44 90 - Cope 1965a; Johnson
and Finley 1980;
Mayer and Ellersieck
1986
Rainbow trout (25-50
g),
Oncorhynchus mykiss
S, U Technical - 3,200 - Bathe et al. 1975a
Rainbow trout,
Oncorhynchus mykiss
S, U Technical - 90 - Ciba-Giegy 1976
Rainbow trout,
Oncorhynchus mykiss
S, U Reagent 192 1,350 425.8 Meier et al. 1979;
Dennis et al. 1980
Brook trout (1 yr),
Salvelinus fontinalis
F, M Technical
(92.5%)
45 800 - Allison and Hermanutz
1977
Brook trout (1 yr),
Salvelinus fontinalis
F, M Technical
(92.5%)
45 450 - Allison and Hermanutz
1977
Brook trout (1 yr),
Salvelinus fontinalis
F, M Technical
(92.5%)
45 1,050 723.0 Allison and Hermanutz
1977
Lake trout (3.20 g),
Salvelinus namaycush
S, U Technical
(92%)
162 602 602 Johnson and Finley
1980; Mayer and
Ellerseick 1986
Zebrafish (0.4 g),
Brachydanio rerio
R, M Technical
(98%)
- 8,000 8,000 Keizer et al. 1991
Table 1. (continued)
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Fathead minnow,
Pimephales promelas
S, U Reagent 192 10,300d - Meier et al. 1979;
Dennis et al. 1980
Fathead minnow
(newly hatched
larva),
Pimephales promelas
S, M Technical
(87.1%)
(fresh
stock
solution)
45.8 4,300d - Jarvinen and Tanner
1982
Fathead minnow
(newly hatched
larva),
Pimephales promelas
S, M Technical
(87.1%)
(aged
stock
solution)
45.8 2,100d - Jarvinen and Tanner
1982
Fathead minnow
(juvenile),
Pimephales promelas
F, M Technical
(92.5%)
45 10,000 - Allison and Hermanutz
1977
Fathead minnow
(newly hatched
larva),
Pimephales promelas
F, M Technical
(87.1%)
45 6,900 - Jarvinen and Tanner
1982
Fathead minnow
(juvenile),
Pimephales promelas
F, M Technical
(87.1%)
43.6 9,350 8,641 University of
Wisconsin-Superior
1988
Table 1. (continued)
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Goldfish (2.5-6.0
cm),
Carassius auratus
S, U Technical
(91%)
- 9,000 9,000 Beliles 1965
Flagfish (6 wk),
Jordanella floridae
F, M Technical
(92.5%)
45 1,500 - Allison and Hermanutz
1977
Flagfish (7 wk),
Jordanella floridae
F, M Technical
(92.5%)
45 1,800 1,643 Allison and Hermanutz
1977
Guppy (0.6 g),
Poecilia reticulata
R, M Technical
(98%)
- 800 800 Keizer et al. 1991
Bluegill (2.5-5.0
cm),
Lepomis macrochirus
S, U Technical - 136d - Beliles 1965
Bluegill (0.87 g),
Lepomis macrochirus
S, U Technical - 22d - Cope 1965b
Bluegill,
Lepomis macrochirus
S, U Technical - 22d - Ciba-Geigy 1976
Bluegill (0.8 g),
Lepomis macrochirus
S, U Reagent 192 120d - Meier et al. 1979;
Dennis et al. 1980
Bluegill (1.00 g),
Lepomis macrochirus
S, U Technical
(92%)
44 168.0d - Johnson and Finley
1980; Mayer and
Ellersieck 1986
Table 1. (continued)
Species Method
a
Chemicalb
Hardness
(mg/L as
CaCO3)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Bluegill (1 yr.),
Lepomis macrochirus
F, M Technical
(92.5%)
45 480 - Allison and Hermanutz
1977
Bluegill (1 yr.),
Lepomis macrochirus
F, M Technical
(92.5%)
45 440 459.6 Allison and Hermanutz
1977
Green frog (stage 8),
Rana clamitans
R, U Technical - >50 >50 Harris et al. 1998
Table 1. (continued)
Species Method
a
Chemicalb
Salinity
(g/kg)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
SALTWATER SPECIES
Annelid worm
(juvenile),
Neanthes
arenaceodentata
R, U (96%) 30 >2,880 >2,880 Thursby & Berry 1988
Copepod (adult),
Acartia tonsa
S, M Technical
(97.6%)
20 2.57 2.57 Khattat & Farley 1976
Mysid (juvenile),
Americamysis bahia
R, U (96%) 29 8.5d - Thursby & Berry 1988
Mysid (juvenile),
Americamysis bahia
S, U Technical 25 8.5d - Cripe 1994
Mysid (juvenile),
Americamysis bahia
F, M Diazinon 17 4.82 4.82 Nimmo et al. 1981
Amphipod (juvenile),
Ampelisca abdita
R, U (96%) 30 6.6 6.6 Thursby & Berry 1988
Pink shrimp (larval),
Penaeus duorarum
S, U Technical 25 21 21 Cripe 1994
Grass shrimp
(larval),
Palaemonetes pugio
R, U (96%) 30 2.8 2.8 Thursby & Berry 1988
Table 1. (continued)
Species Method
a
Chemicalb
Salinity
(g/kg)
LC50
or EC50
(μg/L)
Species
Mean
Acute
Value
(μg/L)
Reference
Sea urchin
(embryo/larval),
Arbacia punctulata
S, U (96%) 31 >9,600 >9,600 Thursby & Berry 1988
Sheepshead minnow
(juvenile),
Cyprinodon variegatus
F, M (92.6%) 23 1,400 1,400 Goodman et al. 1979;
Mayer 1987
Inland silverside
(juvenile),
Menidia beryllina
R, U (96%) 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
c Animals were fed during the exposure
d Results were not used in the calculation of the Species Mean Acute Value due to availability of data from more
sensitive test conditions.
Table 2. Chronic Toxicity of Diazinon to Aquatic Animals
Species Testa Chemicalb
Hardness
(mg/L as
CaCO3)
Chronic
Limits
(μg/L)
Chronic
Value
(μg/L)
Reference
FRESHWATER SPECIES
Cladoceran (<6-hr.
old),
Ceriodaphnia dubia
LC
(7-
day)
Technical
(85%)
40 0.220-0.520 0.3382 Norberg-King
1987
Brook trout
(yearling),
Salvelinus
fontinalis
PLC Technical
(92.5%)
45 0-0.8 <0.8 Allison and
Hermanutz 1977
Zebrafish,
Brachydanio rerio
ELS Analytical 360 200->200 >200 Bresch 1991
Fathead minnow
(embryo-larva),
Pimephales promelas
ELS Technical
(87.1%)
45.8 50-90 67.08 Jarvinen and
Tanner 1982
Fathead minnow
(embryo-larva),
Pimephales promelas
ELS Technical
(88.2%)
44-49 16.5-37.8 24.97 Norberg-King
1989
Flagfish (1-day
old),
Jordanella floridae
LC - - 0-14 <14 Allison 1977
SALTWATER SPECIES
Table 2. (continued)
Mysid (juvenile),
Americamysis bahia
LC - 30-31c 2.1-4.4 3.040 Nimmo et al.
1981
Sheepshead minnow
(juvenile),
Cyprinodon
variegatus
PLC Technical
(92.6%)
16.5c 0-0.47 <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.
Acute-Chronic Ratio
Species
Hardness
(mg/L as
CaCO3)
Acute Value
(μg/L)
Chronic Value
(μg/L) Ratio
Mean
Ratio
Cladoceran,
Ceriodaphnia dubia
40 0.3760 0.3382 1.112 1.112
Mysid,
Americamysis bahia
17c 4.82 3.040 1.586 1.586
Flagfish,
Jordanella
floridae
45 1,643 <14 >117.4 >117.4
Table 2. (continued)
Fathead minnow,
Pimephales
promelas
45.8 6,900 67.08 102.9 -
Fathead minnow,
Pimephales
promelas
44-49 9,350 24.97 374.4 196.3
Brook trout,
Salvelinus
fontinalis
45 723.0 <0.8 >903.8 >903.8
Sheepshead minnow,
Cyprinodon
variegatus
16.5c 1,400 <0.47 >2,979 >2,979
c Salinity (g/kg).
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
Ranka
Genus Mean
Acute Value
(μg/L) Species
Species Mean
Acute Value
(μg/L)b
Species Mean
Acute-Chronic
Ratioc
FRESHWATER SPECIES
20 11,640 Planaria,
Dugesia tigrina
11,640 -
19 11,000 Snail,
Gillia altilis
11,000 -
18 9,000 Goldfish,
Carassius auratus
9,000 -
17 8,641 Fathead minnow,
Pimephales promelas
8,641 196.3
16 8,000 Zebrafish,
Brachydanio rerio
8,000 -
15 7,841 Oligachaete worm,
Lumbricus variegatus
7,841 -
14 3,198 Snail,
Pomacea paludosa
3,198 -
13 1,643 Flagfish,
Jordanella floridae
1,643 >117.4
12 960.4 Cutthroat trout,
Oncorhynchus clarki
2,166 -
Rainbow trout,
Oncorhynchus mykiss
425.8 -
11 800 Guppy,
Poecilia reticulata
800 -
10 660 Brook trout,
Salvelinus fontinalis
723 >903.8
Table 3. (continued)
Ranka
Genus Mean
Acute Value
(μg/L) Species
Species Mean
Acute Value
(μg/L)b
Species Mean
Acute-Chronic
Ratioc
Lake trout,
Salvelinus namaycush
602 -
9 459.6 Bluegill,
Lepomis macrochirus
459.6 -
8 >50 Green frog
Rana clamitans
>50 -
7 25 Stonefly,
Pteronarcys californica
25 -
6 10.7 Midge,
Chironomus tentans
10.7 -
5 6.51 Amphipod,
Hyalella azteca
6.51 -
4 1.587 Cladoceran,
Simocephalus serrulatus
1.587 -
3 0.9020 Cladoceran,
Daphnia magna
1.048 -
Cladoceran,
Daphnia pulex
0.7764 -
2 0.3773 Cladoceran,
Ceriodaphnia dubia
0.3773 1.112
1 0.20 Amphipod,
Gammarus fasciatus
0.20 -
Table 3. (continued)
Ranka
Genus Mean
Acute Value
(μg/L) Species
Species Mean
Acute Value
(μg/L)b
Species Mean
Acute-Chronic
Ratioc
SALTWATER SPECIES
9 >9,600 Sea urchin,
Arbacia punctulata
>9,600 -
8 >2,880 Annelid worm,
Neanthes
arenaceodentata
>2,880 -
7 1,400 Sheepshead minnow,
Cyprinodon variegatus
1,400 >2,979
6 1,170 Inland silverside,
Menidia beryllina
1,170 -
5 21 Pink shrimp,
Penaeus duorarum
21 -
4 6.6 Amphipod,
Ampelisca abdita
6.6 -
3 4.82 Mysid,
Americamysis bahia
4.82 1.586
2 2.8 Grass shrimp
Palaemonetes pugio
2.8 -
1 2.57 Copepod,
Acartia tonsa
2.57 -
a Ranked from most resistant to most sensitive based on Genus Mean Acute Values.
b From Table 1.
c From Table 2.
Table 3. (continued)
Fresh Water
Final Acute Value = 0.1925 μg/L
Criterion Maximum Concentration = (0.1925 μg/L)/2 = 0.0963 μg/L
Final Acute-Chronic Ratio = 2.0 (see text)
Final Chronic Value = (0.1925 μg/L)/2.0 = 0.0963 μg/L
Salt Water
Final Acute Value = 1.637 μg/L
Criterion Maximum Concentration = (1.637 μg/L)/2 = 0.8185 :g/L
Final Acute-Chronic Ratio = 2.0 (see text)
Final Chronic Value = (1.637 μg/L)/2.0 = 0.8185 μg/L
Table 4. Toxicity of Diazinon to Aquatic Plants
Species
Hardness
(mg/L as CaCO3)
Duration
(days) Effect
Concentration
(μg/L) Reference
FRESHWATER SPECIES
Green algae,
Selenastrum capricornutum
- 7 EC50
(cell numbers)
6,400 Hughes 1988
Table 5. Bioaccumulation of Diazinon by Aquatic Organisms
Species
Concentration
in Water
(μg/L)a
Duration
(days) Tissue
Percent
Lipids
BCF or
BAFb
Normalized
BCF or
BAFc
Reference
FRESHWATER SPECIES
Rainbow trout (16
g),
Oncorhynchus
mykiss
15 14 Whole body - 62 - Seguchi and Asaka
1981
Carp (8 g),
Cyprinus carpio
15 14 Whole body - 120 - Seguchi and Asaka
1981
Guppy,
Poecilia
reticulata
350 14 Whole body - 188 - Keizer et al. 1993
SALTWATER SPECIES
Sheepshead minnow,
Cyprinodon
variegatus
1.8 108 Whole body
(less
brain)
- 147 - Goodman et al.
1979
Sheepshead minnow,
Cyprinodon
variegatus
3.5 108 Whole body
(less
brain)
- 147 - Goodman et al.
1979
Sheepshead minnow,
Cyprinodon
variegatus
6.5 108 Whole body
(less
brain)
- 213 - 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.
Table 6. Other Data on Effects of Diazinon on Aquatic Organisms
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
FRESHWATER SPECIES
Sewage microbes Regent - 22 hr No reduction of
oxygen
consumption
40,000 Bauer et al. 1981
Actinomycete bacteria Technical - 20 days Stimulated
growth
40,000 Sethunathan and
MacRae 1969
Green alga,
Chlorella ellipsoidea
- - 72 hr Decreased ATP
content
100,000 Clegg and Koevenig
1974
Green alga,
Chlamydomonas sp.
- - 72 hr Decreased ATP
content
100,000 Clegg and Koevenig
1974
Green alga,
Scenedesmus quadricauda
- - 10 days No decrease in
cell number,
biomass, or
photosynthesis
1,000 Stadnyk and Campbell
1971
Mixture of green alga
and diatoms
(99.9%) - 14 days Decreased growth <10 Butler et al. 1975a
Euglenoid,
Euglena elastica
- - 72 hr Decreased ATP
content
100,000 Clegg and Koevenig
1974
Duckweed,
Wolffia papulifera
(97%) - 11 days Lethal 100,000 Worthley and Schott
1971
Duckweed,
Wolffia papulifera
(97%) - 11 days Teratogenic
effects
10,000 Worthley and Schott
1971
Protozan,
Paramecium caudatum
- - 1 hr LC50 .3,000 Evtugyn et al. 1997
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Rotifer,
Brachionus calyciflorus
Technical
(92%)
80-100 24 hr LC50 29,220 Fernandez-
Casalderrey et al.
1992a
Rotifer (16-18 hr),
Brachionus calyciflorus
Technical
(92%)
80-100 5 hr Reduced (50%)
filtration and
ingestion ratios
14,000 Fernandez-
Casalderrey et al.
1992b
Rotifer (<2 hr),
Brachionus calyciflorus
Technical
(92%)
80-100 10 days Decreased
reproduction
<5,000 Fernandez-
Casalderrey et al.
1992c
Rotifer (<2 hr),
Brachionus calyciflorus
Technical
(99%)
80-100 4.04 days LT50 5,000 Fernandez-Casalderry
et al. 1992d
Rotifer (<2 hr),
Brachionus calyciflorus
Technical
(99%)
80-100 4.66 days LT50 7,000 Fernandez-
Casalderrey et al.
1992d
Rotifer (<2 hr),
Brachionus calyciflorus
Technical
(99%)
80-100 2.49 days LT50 14,000 Fernandez-Casalderry
et al. 1992d
Rotifer (<2 hr),
Brachionus calyciflorus
- 80-100 48 hr NOEC
Reproduction
8,000 Snell and Moffat
1992
Rotifer (<2 hr),
Brachionus calyciflorus
- 80-100 48 hr NOEC Ingestion 20,000 Juchelka and Snell
1994
Oligochaete worm,
Lumbriculus variegatus
- - 4 hr Lethal 20,000 Rogge and Drewes
1993
Tubificid worm,
Branchiura sowerbyi
- - 96 hr LC50 2,220 Chatterjee and Konar
1984
Snail,
(Physa acuta)
- - 48 hr LC50 4,800 Hashimoto and
Nishiuchi 1981
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Cladoceran (<6 hr),
Ceriodaphnia dubia
Technical
(85%)
40 7 days No effect on
survival or
reproduction
0.220 Norberg-King 1987
Cladoceran (<6 hr),
Ceriodaphnia dubia
Technical
(85%)
40 7 days Lethal 0.520 Norberg-King 1987
Cladoceran
Daphnia magna
- 202 50 hr EC50 4.3 Anderson 1959
Cladoceran (adult),
Daphnia magna
- - 24 hr Adhesion of
algal particles
on 2nd antennae
and
immobilization
1 Stratton and Corke
1981
Cladoceran (<24 hr),
Daphnia magna
Analytical
(95%)
200 21 days Reduced
reproduction and
mobility
0.3 Dortland 1980
Cladoceran (<24 hr),
Daphnia magna
Analytical
(99%)
200 21 days No reduction in
reproduction or
mobility
0.2 Dortland 1980
Cladoceran (<24 hr),
Daphnia magna
Analytical
(99%)
200 21 days EC50
(immobilization)
0.22 Dortland 1980
Cladoceran (<24 hr),
Daphnia magna
Analytical
(99%)
200 21 days EC50
(immobilization)
0.24 Dortland 1980
Cladoceran (<24 hr),
Daphnia magna
Analytical
(99%)
200 21 days EC50
(immobilization)
0.7 Dortland 1980
Cladoceran (<24 hr),
Daphnia magna
Analytical
(99%)
200 21 days EC50
(immobilization)
0.8 Dortland 1980
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Cladoceran (<24 hr),
Daphnia magna
Insecticidal
soap
- 48 hr LC50 0.74 Mitchell 1985
Cladoceran (<24 hr),
Daphnia magna
Insecticidal
soap
- 96 hr LC50 0.21 Mitchell 1985
Cladoceran (adult),
Daphnia magna
Technical - 3 hr LC50 7.8 Nishiuchi and
Hashimoto 1967
Cladoceran,
Daphnia magna
Technical - 3 hr LC50 80 Hashimoto and
Nishiuchi 1981
Cladoceran,
Daphnia magna
Technical
(92%)
- 5 hr Reduced (50%)
filtration rate
0.47 Fernandez-
Casalderrey et al.
1994
Cladoceran (<24 hr),
Daphnia magna
Technical
(92%)
250 21 days NOEC survival 0.15 Fernandez-
Casalderrey et al.
1995
Cladoceran (<24 hr),
Daphnia magna
Technical
(92%)
250 21 days LOEC survival 0.18 Fernandez-
Casalderrey et al.
1995
Cladoceran (<24 hr),
Daphnia magna
Technical
(92%)
250 21 days LOEC
reproduction
0.15 Fernandez-
Casalderrey et al.
1995
Cladoceran,
Daphnia magna
Optimum 160-180 30 min IC50 0.45 Fort et al. 1996
Cladoceran,
(Daphnia pulex)
- - 3 hr LC50 80 Hashimoto and
Nishiuchi 1981
Cladoceran,
(Daphnia pulex)
- - 3 hr LC50 7.8 Nishiuchi and
Hashimoto 1967
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Cladoceran (adult),
Moina macrocopa
Technical - 3 hr LC50 26 Nishiuchi and
Hashimoto 1967
Cladoceran,
Moina macrocopa
Technical - 3 hr LC50 50 Hashimoto and
Nishiuchi 1981
Copepod,
Cyclops vividis
- - 96 hr LC50 2,600 Chatterjee and Konar
1984
Amphipod (adult),
Hyalella azteca
Technical 160-180 48 hr LC50 19
(measured)
Werner and Nagel
1997
Amphipod (0-2 days),
Hyalella azteca
Technical 40 96 hr LC50 6.2 Collyard et al. 1994
Amphipod (2-4 days),
Hyalella azteca
Technical 40 96 hr LC50 4.2 Collyard et al. 1994
Amphipod (6-8 days),
Hyalella azteca
Technical 40 96 hr LC50 4.3 Collyard et al. 1994
Amphipod (8-10 days),
Hyalella azteca
Technical 40 96 hr LC50 4.4 Collyard et al. 1994
Amphipod (12-14 days),
Hyalella azteca
Technical 40 96 hr LC50 3.8 Collyard et al. 1994
Amphipod (16-18 days),
Hyalella azteca
Technical 40 96 hr LC50 4.4 Collyard et al. 1994
Amphipod (20-22 days),
Hyalella azteca
Technical 40 96 hr LC50 4.6 Collyard et al. 1994
Amphipod (24-26 days),
Hyalella azteca
Technical 40 96 hr LC50 4.6 Collyard et al. 1994
Amphipod (2 mo.),
Gammarus lacustris
- - 96 hr LC50 200 Sanders 1969
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Crayfish,
Procambarus clarkii
- - 7 days BCF = 4.9 10 Kanazawa 1978
Stonefly (nymph),
Pteronarcys
californicus
- - 48 hr EC50 74 Cope 1965a
Caddisfly (larva),
Hydropsyche morosa
- - 6 hr LC50 2,500 Fredeen 1972
Caddisfly (larva),
Hydropsyche morosa
- - 6 hr LC50 500 Fredeen 1972
Caddisfly (larva),
Hydropsyche recurvata
- - 6 hr LC50 >500 Freeden 1972
Caddisfly (larva),
Hydropsyche recurvata
- - 6 hr LC50 >500 Freeden 1972
Mosquito (4th instar),
Aedes aegypti
Technical - 24 hr LC50 350 Klassen et al. 1965
Mosquito (3rd-4th
instar),
Culex pipiens fatigans
Technical - 24 hr LC50 61 Chen et al. 1971
Mosquito (3rd-4th
instar),
Culex pipiens fatigans
Technical - 24 hr LC50 80 Chen et al. 1971
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 3.5 Yasuno and
Kerdpibule 1967
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 5.7 Yasuno and
Kerdpibule 1967
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 2.2 Yasuno and
Kerdpibule 1967
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 3.2 Yasuno and
Kerdpibule 1967
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 4.6 Yasuno and
Kerdpibule 1967
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 4.5 Yasuno and
Kerdpibule 1967
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 1.9 Yasuno and
Kerdpibule 1967
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 1.8 Yasuno and
Kerdpibule 1967
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 5.4 Yasuno and
Kerdpibule 1967
Mosquito (4th instar),
Culex pipiens fatigans
Technical - 24 hr LC50 3.5 Yasuno and
Kerdpibule 1967
Midge (1st instar),
Chironomus riparius
Analytical
(99.7%)
- 96 hr LC50 (fed) 23 Stuijfzand et al.
2000
Midge (4th instar),
Chironomus riparius
Analytical
(99.7%)
- 96 hr LC50 (fed) 167 Stuijfzand et al.
2000
Salmonidae Emulsible
concentrate
(60%)
- 96 hr LC50 8,000 Ciba-Geigy 1976
Brown Trout (3.22 g),
Salma trutta lacustris
- - 96 hr LC50 602 Swedberg 1973
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Cutthroat trout (0.52
g),
Oncorhynchus clarki
- - 96 hr LC50 3,850 Swedberg 1973
Cutthroat trout (2.02
g),
Oncorhynchus clarki
- - 96 hr LC50 2,760 Swedberg 1973
Rainbow trout (fry),
Oncorhynchus mykiss
Insecticidal
soap
- 96 hr LC50 20 Mitchell 1985
Rainbow trout,
Oncorhynchus mykiss
- - 48 hr EC50 170 Cope 1965a
Rainbow trout (16 g),
Oncorhynchus mykiss
Synthesized - 14 days BCF = 62 15 Seguchi and Asaka
1981
Rainbow trout,
Oncorhynchus mykiss
Analytical 360 28 days NOEC 200 Bresch 1991
Goldfish (4.01 cm),
Carassius auratus
Technical - 48 hr LC50 5,100 Nishiuchi and
Hashimoto 1967;
Hashimoto and
Nishiuchi 1981
Carp,
Cyprinus carpio
- - 7 days BCF = 65.1 10 Kanazawa 1978
Carp (4.2 cm),
Cyprinus carpio
Technical - 72 hr LC50 2,000 Nishiuchi and Asano
1981
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Carp (6.0 cm),
Cyprinus carpio
Technical - 48 hr LC50 3,200 Nishiuchi and
Hashimoto 1967;
Hashimoto and
Nishiuchi 1981;
Nishiuchi and Asano
1981
Carp (8 g),
Cyprinus carpio
Synthesized - 14 days BCF = 120 18 Seguchi and Asaka
1981
Carp (1.1-1.4 g),
Cyprinus carpio
- - 72 hr LC50 1,420 Dutt and Guha 1988
Carp (24-35 g),
Cyprinus carpio
Reagent
(98%)
- 7 days BCF = 20.9 2.4 Tsuda et al. 1990
Fathead minnow (larva),
Pimephales promelas
Technical
(88.2%)
44-49 7 days No reduction in
growth or
survival
277 Norberg-King 1989
Fathead minnow
(embryo-larva),
Pimephales promelas
Technical
(88.2%)
44-49 12 days No reduction in
growth or
survival
285 Norberg-King 1989
Fathead minnow (larva),
Pimephales promelas
Technical
(88.2%)
44-49 7 days Reduction in dry
weight
347 Norberg-King 1989
Fathead minnow (larva),
Pimephales promelas
Technical
(88.2%)
44-49 7 days Reduction in dry
weight
277 Norberg-King 1989
Fathead minnow (newly
hatched larvae),
Pimephales promelas
Encapsulated
formulation
(fresh stock)
45.8 96 hr LC50 6,100 Jarvinen and Tanner
1982
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Fathead minnow (newly
hatched larvae),
Pimephales promelas
Encapsulated
formulation
(11 week-old
stock)
45.8 96 hr LC50 5,100 Jarvinen and Tanner
1982
Fathead minnow
(embryo-larva),
Pimephales promelas
Encapsulated
formulation
45.8 32 days No effect on
weight
40 Jarvinen and Tanner
1982
Fathead minnow
(embryo-larva),
Pimephales promelas
Encapsulated
formulation
45.8 32 days Significant
reduction in
weight
76 Jarvinen and Tanner
1982
Ide
Leucisuc idus
Emulsifiable
concentrate
(60%)
- 96 hr LC50 150 Ciba-Geigy 1976
Catfish
Ictalurus sp.
Emulsifiable
concentrate
(60%)
- 96 hr LC50 8,000 Ciba-Geigy 1976
Flagfish (larvajuvenile),
Jordanella floridae
- - 21-day
pulsed dose
+ recovery
Decreased egg
production
290 Allison 1977
Flagfish (juvenileadult),
Jordanella floridae
- - 21-day
pulsed dose
+ recovery
Decreased
parental
survival
250 Allison 1977
Flagfish (adultspawning),
Jordanella floridae
- - 21-day
pulsed dose
+ recovery
Decreased
survival of
parents and
larvae
1,170 Allison 1977
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Oriental weatherfish,
Misqurnus
anguillicaudatus
Technical - 48 hr LC50 500 Hashimoto and
Nishiuchi 1981
Oriental weatherfish
(2.6 g),
Misgurnus
anguillicaudatus
Synthesized - 14 days BCF = 28 14 Seguchi and Asaka
1981
Guppy (7 wk),
Poecilia reticulata
Technical - 24 hr LC50 3,700 Chen et al. 1971
Guppy (7 wk),
Poecilia reticulata
Technical - 24 hr LC50 3,800 Chen et al. 1971
Guppy (7 wk),
Poecilia reticulata
Technical - 30 min Loss of
equilibrium
7,000 Chen et al. 1971
Guppy,
Poecilia reticulata
Emulsifiable
concentrate
(60%)
- 96 hr LC50 3,000 Ciba-Geigy 1976
Guppy,
Poecilia reticulata
- - 7 days BCF = 17.5 10 Kanazawa 1978
Guppy (2-3 mon),
Poecilia reticulata
Technical
(99%)
100 3 days Lethal body
burden
2,495 Ohayo-Mitoko and
Deneer 1993
Guppy (2-3 mon),
Poecilia reticulata
- 75 24 hr Lethal body
burden
(@ 4,330 μg/l
exposure)
2.1 (μmol/g) Deneer et al. 1999
Guppy (2-3 mon),
Poecilia reticulata
- 75 7 days Lethal body
burden (@ 2,420
μg/L exposure)
1.8 (μmol/g) Deneer et al. 1999
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Tilapia,
Tilapia sp.
- - 48 hr LC50 1,492 Li and Chen 1981
Mozambique tilapia (5-9
g),
Tilapia mossambica
Technical - - LC100 15,850 Mustafa et al. 1982
Mozambique tilapia
(3.56 g),
Tilapia mossambica
- - 96 hr LC50 2,280 Chatterjee and Konar
1984
Mozambique tilapia (1.4
g),
Tilapia mossambica
- - 72 hr LC50 2,880 Dutt and Guha 1988
Bluegill,
Lepomis macrochirus
- - 48 hr EC50 30 Cope 1965a
Bluegill,
Lepomis macrochirus
Basudin
(93%)
- 48 hr LC50 1,493 Li and Chen 1981
Experimental stream
community
Technical
(92.5%)
170-195 84 days Increased drift
rates for
Hyalella
0.3 Arthur et al. 1983
Experimental stream
community
Technical
(92.5%)
170-195 112 days Reduced Hyalella
populations
5 Arthur et al. 1983
Experimental pond
community
Technical
(88%)
70-150 70 days NOEC for
phytoplankton
and periphyton
chlorophyll, and
macrophyte
biomass
443 Giddings et al. 1996
Table 6. (continued)
Species Chemicala
Hardness
(mg/L as
CaCO3) Duration Effect
Concentratio
n
(μg/L)
Reference
Experimental pond
community
Technical
(88%)
70-150 70 days LOEC for
Cladocera,
Pentaneurcini,
and
Ceratopogonidae
abundance
2.4 Giddings et al. 1996
Experimental pond
community
Technical
(88%)
70-150 70 days LOEC for
zooplankton and
macroinvertebrat
e taxonomic
richness
9.2 Giddings et al. 1996
Experimental pond
community
Technical
(88%)
70-150 70 days Reduced bluegill
sunfish biomass
22 Giddings et al. 1996
Experimental pond
community
Technical
(88%)
70-150 70 days Reduced bluegill
sunfish survival
54 Giddings et al. 1996
Species Chemicala
Salinity
(g/kg) Duration Effect
Concentrati
on (ug/L) Reference
SALTWATER SPECIES
Natural photoplankton - - 4 hr 6.8% decrease in
photosynthesis
1,000 Butler 1963
Table 6. (continued)
Species Chemicala
Salinity
(g/kg) Duration Effect
Concentrati
on (ug/L) Reference
Red alga,
Chondrus crispus
(12.5%) - 24 hr
exposure 18
day holding
No effect on
growth
10,000 Shacklock & Croft 1981
Red alga,
Champia parvula
(96%) - 48 hr
exposure
No effect on
sexual
reproduction
1,000 Thursby & Tagliabue
1988
Rotifer,
Brachionus plicatilis
(96%) - 24 hr LC50 55,100 Thursby & Berry 1988
Rotifer,
Brachionus plicatilis
Standard
($95%)
- 24 hr EC50 28,000 Guzzella et al. 1997
Snail,
Lacuna vincta
(12.5%) - 3 hr
exposure, 48
hr holding
88% mortality 1,000 Shacklock & Croft 1981
Snail,
Lacuna vincta
(12.5%) - 3 hr
exposure, 48
hr holding
75% mortality 10,000 Shacklock & Croft 1981
Eastern oyster,
Crassostrea virginica
- - 96 hr No decrease in
shell growth
1,000 Butler 1963; Mayer
1987
Eastern oyster
(5-10 cm height),
Crassostrea virginica
Technical and
14C- labeled
- 96 hr LC50 shell growth 1,115 Williams 1989
Eastern oyster
(6-10 cm height),
Crassostrea virginica
Technical and
14C-labeled
- 5 days BFC = 56 100 Williams 1989
Amphipod (adult),
Ampelisea aldita
Technical 25 48 hr LC50 10 Werner & Nagel 1997
Amphipod,
Gammarus oceanicus
(12.5%) - 3 hr
exposure
100% mortality 1,000 Shacklock & Croft 1981
Table 6. (continued)
Species Chemicala
Salinity
(g/kg) Duration Effect
Concentrati
on (ug/L) Reference
Amphipod (adult),
Rhepoxynius abronius
Technical 31 24 hr LC50 9.2 Werner & Nagel 1997
Isopod,
Idotea baltica
(12.5%) - 3 hr
exposure
100% mortality 1,000 Shacklock & Croft 1981
Brown shrimp,
Penaeus aztecus
- - 24 hr EC50 44 Butler 1963
Brown shrimp,
Penaeus aztecus
Technical
95.1% pure
- 48 hr EC50 28 Mayer 1987
Grass shrimp,
Palaemonetes pugio
Technical
95.1% pure
- 48 hr EC50 28 Mayer 1987
White mullet,
Mugil curema
- - 24 & 48 hr LC50 250 Butler 1963
Striped mullet,
Mugil cephalus
Technical
95.1% pure
- 48 hr LC50 150 Mayer 1987
Sheepshead minnow,
Cyprinodon variegatus
92.6% pure - 108 days Decrease in
acetylcholinester
ase activity
0.47 Goodman et al. 1979;
Mayer 1987
a Percent purity is listed in parentheses when available.
52
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Hazadorous Material Moving!

Wednesday, March 12, 2008

PARKLAND OUT, Pesticides Come AS SECRETARY OF DNREC created Dump!: With all the Warnings of this Dump causing health problem, including cancer, Secretary Hughes has to be removed?

PARKLAND OUT, Pesticides Come AS SECRETARY OF DNREC created Dump!: With all the Warnings of this Dump causing health problem, including cancer, Secretary Hughes has to be removed?

Thursday, March 6, 2008

"WHAT'S IN YOUR DRINKING WATER"?

Thursday, February 28, 2008

DIAZINON, It's every where decaying leaves and trees and grass clippings are:

These are hearings for Garbage locations.

Drinking Water Healthy or cause of long term terminal illness?

"WHAT'S IN YOUR DRINKING WATER"?

Looks Like I have more People coming out of the Woods! NoW Drungs in drinking water!!

CANCER Do We Do It to Ourselves, Beware of Pesticides by Sara Little

Children and Drinking Water from the EPA

Water Pollution

Who is at Greater Risk?

You don't just start dumping to make a Dump!!!

Federal Report of Drinking Water, what's expected to be accomplished!!