oEPA
United States Office of Water EPA-820-D-24-003
Environmental Protection 4304T December 2024
Agency
DRAFT
Supporting Information for Comparison of OPP Aquatic Life Benchmarks,
OW Aquatic Life Criteria and Alternative Criteria-Related Approaches
When Data are Insufficient to Develop Aquatic Life Criteria
Data supporting the analyses in
Draft Comparison of Aquatic Life Protective Values Developed for Pesticides under the
Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA)
and the Clean Water Act (CWA)
Prepared by:
U.S. Environmental Protection Agency
Office of Water & Office of Pesticide Programs
Washington, DC
December 2024
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Table of Contents
Table of Contents ii
1 Insecticides 1
1.1 Data-Rich Pesticides 1
1.1.1 Comparison of Aquatic Life Toxicity Values for Carbaryl: Data Sources and
Considerations 1
1.1.2 Comparison of Aquatic Life Toxicity Values for Methomyl: Data Sources and
Considerations 26
1.1.3 Comparison of Aquatic Life Toxicity Values for Propoxur: Data Sources and
Considerations 35
1.1.4 Comparison of Aquatic Life Toxicity Values for Malathion: Data Sources and
Considerations 42
1.1.5 Comparison of Aquatic Life Toxicity Values for Diazinon: Data Sources and
Considerations 65
1.1.6 Comparison of Aquatic Life Toxicity Values for Chlorpyrifos: Data Sources and
Considerations 83
1.1.7 Comparison of Aquatic Life Toxicity Values for Dichlorvos: Data Sources and
Considerations 95
1.1.8 Comparison of Aquatic Life Toxicity Values for Acrolein: Data Sources and
Considerations 101
1.2 Data-Limited Pesticides 106
1.2.1 Comparison of Aquatic Life Toxicity Values for Oxamyl: Data Sources and
Considerations 106
1.2.2 Comparison of Aquatic Life Toxicity Values for Acephate: Data Sources and
Considerations 114
1.2.3 Comparison of Aquatic Life Toxicity Values for Dimethoate: Data Sources and
Considerations 124
1.2.4 Comparison of Aquatic Life Toxicity Values for Phosmet: Data Sources and
Considerations 132
1.2.5 Comparison of Aquatic Life Toxicity Values for Terbufos: Data Sources and
Considerations 140
1.3 Data Insufficient Pesticides 150
1.3.1 Comparison of Aquatic Life Toxicity Values for Methamidophos: Data Sources
and Considerations 150
1.3.2 Comparison of Aquatic Life Toxicity Values for Profenofos: Data Sources and
Considerations 159
1.3.3 Comparison of Aquatic Life Toxicity Values for Fenpropathrin: Data Sources
and Considerations 168
1.3.4 Comparison of Aquatic Life Toxicity Values for Fenbutatin Oxide: Data Sources
and Considerations 176
1.3.5 Comparison of Aquatic Life Toxicity Values for Methoxyfenozide: Data Sources
and Considerations 184
1.3.6 Comparison of Aquatic Life Toxicity Values for Norflurazon: Data Sources and
Considerations 192
1.3.7 Comparison of Aquatic Life Toxicity Values for Propargite: Data Sources and
Considerations 199
ii
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1.3.8 Comparison of Aquatic Life Toxicity Values for Pyridaben: Data Sources and
Considerations 206
2 Herbicides 213
2.1 Data-Rich Herbicides 213
2.1.1 Comparison of Aquatic Life Toxicity Values for Atrazine: Data Sources and
Considerations 213
2.1.2 Comparison of Aquatic Life Toxicity Values for Propazine: Data Sources and
Considerations 230
2.1.3 Comparison of Aquatic Life Toxicity Values for Simazine: Data Sources and
Considerations 240
2.1.4 Comparison of Aquatic Life Toxicity Values for Bensulide: Data Sources and
Considerations 254
2.1.5 Comparison of Aquatic Life Toxicity Values for Glyphosate: Data Sources and
Considerations 265
in
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1 Insecticides
1.1 Data-Rich Pesticides
1.1.1 Comparison of Aquatic Life Toxicity Values for Carbaryl: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA) (U.S.EPA 2024) for carbaryl were obtained from Appendix A of the
2012 carbaryl criteria document, supplemented with additional data reported in Table L-6 of U.S.
EPA (2007), the OPP pesticide effects determination document that served as the basis for the
invertebrate OPP benchmark concentration.
1.1.1.1 Carbaryl Acute Toxicity Data
The EPA obtained acute data from the carbaryl Aquatic Life Criteria (ALC; 2012) and the OPP
pesticide effects determination value document (2007) (See Table 1). Table L-6 of Appendix L
in U.S. EPA (2007) included three LCsos that were not included in Appendix A of the 2012
carbaryl ALC. These were an LCso of 26 |ig/L for Gammarus fasciatus, an LCso of 8 |ig/L for
Gammarus pseudolimnaeus, and an LCso of 1,900 |ig/L for Procambarus sp. All three of these
LCsos were reported in Mayer and Ellersieck (1986). The G. fasciatus LC50 was not included in
Appendix A of the carbaryl ALC (U.S. EPA 2012) because the test chemical included excessive
solvent. The G. pseudolimnaeus LC50 was not included in Appendix A because it was a 48-hour
test, not the recommended 96-hour duration of a test for this species. The Procambarus sp. LC50
test was not used because no species was reported, and a more sensitive LC50 of 1,000 |ig/L was
available for the clearly specified P. clarkii.
The most sensitive species according to Table L-6 of U.S. EPA (2007) of the OPP pesticide
effects determination was the stonefly Pteronarcella badia, with an LC50 of 1.7 |ig/L. An LC50
of 1.7 |ig/L fori5, badia is reported in Mayer and Ellersieck (1986) and is the most sensitive
value in U.S. EPA (2007). This is one of four LCsos used to generate the P. badia Species Mean
Acute Value (SMAV) of 9.163 |ig/L in the 2012 carbaryl ALC.
The final dataset consists of 61 SMAVs and 47 Genus Mean Acute Values (GMAVs), including
26 invertebrate species representing 20 invertebrate genera. Ranked SMAVs and GMAVs for all
invertebrates included in this analysis are listed in Table 2 below.
1
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Table 1. Acute toxicity data of carbaryl to freshwater aquatic organisms.
(ATDR specifics OW minimum data requirements under the Guidelines )
OW
M l)K
(iroup11
Speck's
l.( 50/l.( 50
(fiii/l.)
SM.W
(iM.W
(flli/l.)
Reference
H
Oligochaete worm,
Lumbriculus variegatus
8,200
8,200
8,200
Bailey and Liu 1980
G
Snail (adult),
Aplexa hypnorum
>27,000
>27,000
>27,00
Phipps and Holcombe 1985
G
Mussel (juvenile; 1-2 d),
Anodonta imbecillis
23,700
24,632
24,632
Johnson etal. 1993
G
Mussel (juvenile; 7-10 d),
Anodonta imbecillis
25,600
Johnson etal. 1993
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
3.06
5.958
5.958
Brooke 1990; 1991
D
Cladoceran (<12 hr),
Ceriodaphnia dubia
11.6
Oris et al. 1991
D
Cladoceran (adult; 2-2.5 mm),
Daphnia carinata
35
35
Santharam et al. 1976
D
Cladoceran (5 d),
Daphnia magna
7.2
Lakotaetal. 1981
D
Cladoceran (<24 hr),
Daphnia magna
1,900
29.658
18.80
Johnson etal. 1993
D
Cladoceran (<24 hr),
Daphnia magna
5.6
Sanders et al. 1983
D
Cladoceran (<24 hr),
Daphnia magna
10.1
Brooke 1991
D
Cladoceran (<24 hr),
Daphnia pulex
6.4
6.4
Sanders and Cope 1966
D
Cladoceran (<24 hr),
Simocephalus serrulatus
11
Mayer and Ellersieck 1986
D
Cladoceran (<24 hr),
Simocephalus serrulatus
8.1
8.781
8.781
Mayer and Ellersieck 1986
D
Cladoceran (<24 hr),
Simocephalus serrulatus
7.6
Sanders and Cope 1966
E
Mysid,
My sis relicta
230
230
230
Landrum and Dupuis 1990
E
Aquatic sowbug (mature),
Asellus brevicaudus
280
280
280
Johnson and Finley 1980;
Mayer and Ellersieck 1986
E
Amphipod (2 mo),
Gammarus lacustris
16
18.76
Sanders 1969
E
Amphipod (mature),
Gammarus lacustris
22
Johnson and Finley 1980;
Mayer and Ellersieck 1986
E
Amphipod,
Gammarus fasciatus
26
26
MRID 40098001; Mayer and
Ellersieck 1986
E
Amphipod,
Gammarus pseudolimnaeus
8
16.76
MRID 40098001; Mayer and
Ellersieck 1986
E
Amphipod,
Gammarus pseudolimnaeus
13
9.65
Woodward and Mauck 1980
E
Amphipod (mature),
Gammarus pseudolimnaeus
7
Woodward and Mauck 1980
E
Amphipod (mature),
Gammarus pseudolimnaeus
7.2
Woodward and Mauck 1980
2
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()\\
MIJR
(iroup11
Species
l.( 50/l.( 50
(Jlg/I.)
SMAY
(fm/i.)
(;\1AY
(flli/l.)
Reference
E
Amphipod (mature),
Gammarus pseudolimnaeus
16
Sanders et al. 1983
E
Amphipod (14 d),
Hyalella azteca
15.2
15.2
15.2
McNulty et al. 1999
E
Amphipod,
Pontoporeia hoyi
250
250
250
Landrum and Dupuis 1990
E
Crayfish (3-4 cm),
Cambarus bartoni
839.6
839.6
839.6
Simon 1982
E
Crayfish (3.9 g),
Orconectes immunis
2,870
2,870
2,462
Phipps and Holcombe 1985
E
Crayfish (5-8 cm; males),
Orconectes virilis
2,112
2,112
Simon 1982
E
Crayfish (15-38 g),
Procambarus clarkii
1,000
1,000
1,378
Andreu-Moliner et al. 1986
E
Crayfish,
Procambarus sp.
1,900
1,900
MRID 40098001; Mayer and
Ellersieck 1986
F
Stonefly (nymph),
Claassenia sabulosa
5.6
5.6
5.6
Sanders and Cope 1968
F
Stonefly (1st yr class),
Isogenus sp.
2.8
3.175
3.175
Mayer and Ellersieck 1986
F
Stonefly (1st yr class),
Isogenus sp.
3.6
Mayer and Ellersieck 1986
F
Stonefly (1st yr class; 15-20
mm),
Pteronarcella badia
1.7
Sanders and Cope 1968
F
Stonefly (1st yr class),
Pteronarcella badia
11
9.163
9.163
Woodward and Mauck 1980;
Mayer and Ellersieck 1986
F
Stonefly (1st yr class),
Pteronarcella badia
13
Woodward and Mauck 1980;
Mayer and Ellersieck 1986
F
Stonefly (1st yr class),
Pteronarcella badia
29
Woodward and Mauck 1980;
Mayer and Ellersieck 1986
F
Stonefly (1st yr class),
Pteronarcys californica
4.8
4.8
4.8
Sanders and Cope 1968
F
Stonefly (naiad),
Skwala sp.
3.6
3.6
3.6
Johnson and Finley 1980
F
Backswimmer (adult),
Notonecta undulata
200
200
200
Federle and Collins 1976
A
Apache trout (0.38-0.85 g),
Oncorhynchus apache
1,540
1,540
Dwyeretal. 1995
A
Coho salmon (2.7-4.1 g),
Oncorhynchus kisutch
997
Katz 1961
A
Coho salmon,
Oncorhynchus kisutch
764
Macek and McAllister 1970
A
Coho salmon (1.50 g),
Oncorhynchus kisutch
1,300
1,654
1,994
Post and Schroeder 1971
A
Coho salmon (1.0 g),
Oncorhynchus kisutch
4,340
Johnson and Finley 1980;
Mayer and Ellersieck 1986
A
Coho salmon (10.10 g),
Oncorhynchus kisutch
2,700
Mayer and Ellersieck 1986
A
Coho salmon (19.1 g),
Oncorhynchus kisutch
1,150
Mayer and Ellersieck 1986
3
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()\\
MIJR
(iroup11
Species
l.( 50/l.( 50
(Jlg/I.)
SMAY
(fm/i.)
(;\1AY
(flli/l.)
Reference
A
Coho salmon (4.6 g),
Oncorhynchus kisutch
2,400
Mayer and Ellersieck 1986
A
Coho salmon (5.1g),
Oncorhynchus kisutch
1,750
Mayer and Ellersieck 1986
A
Chinook salmon (fingerling),
Oncorhynchus tshawytscha
2,400
2,541
Johnson and Finley 1980;
Mayer and Ellersieck 1986
A
Chinook salmon (3.0 g),
Oncorhynchus tshawytscha
2,690
Phipps and Holcombe 1985;
1990
A
Cutthroat trout (0.37 g),
Oncorhynchus clarkii
1,500
3,300
Post and Schroeder 1971
A
Cutthroat trout (1.30 g),
Oncorhynchus clarkii
2,169
Post and Schroeder 1971
A
Cutthroat trout (0.5 g),
Oncorhynchus clarkii
7,100
Johnson and Finley 1980;
Mayer and Ellersieck 1986
A
Cutthroat trout (0.6 g),
Oncorhynchus clarkii
6,000
Woodward and Mauck 1980;
Mayer and Ellersieck 1986
A
Cutthroat trout (0.7 g),
Oncorhynchus clarkii
5,000
Woodward and Mauck 1980;
Mayer and Ellersieck 1986
A
Cutthroat trout (0.6 g),
Oncorhynchus clarkii
970
Woodward and Mauck 1980;
Mayer and Ellersieck 1986
A
Cutthroat trout (0.5 g),
Oncorhynchus clarkii
3,950
Woodward and Mauck 1980;
Mayer and Ellersieck 1986
A
Cutthroat trout (0.5 g),
Oncorhynchus clarkii
6,800
Mayer and Ellersieck 1986
A
Cutthroat trout (0.9 g),
Oncorhynchus clarkii
6,700
Mayer and Ellersieck 1986
A
Cutthroat trout,
Oncorhynchus clarkii
3,950
Woodward and Mauck 1980
A
Greenback cutthroat trout (0.31
g), Oncorhynchus clarkii stomias
1,550
Dwyeretal. 1995
A
Lahontan cutthroat trout (0.34-
0.57 g),
Oncorhynchus clarkii henshawi
2,250
Dwyeretal. 1995
A
Rainbow trout (3.2 g),
Oncorhynchus mykiss
1,350
1,476
Katz 1961
A
Rainbow trout,
Oncorhynchus mykiss
4,340
Macek and McAllister 1970
A
Rainbow trout (1.24 g),
Oncorhynchus mykiss
1,470
Post and Schroeder 1971
A
Rainbow trout (1.5 g),
Oncorhynchus mykiss
1,950
Johnson and Finley 1980;
Mayer and Ellersieck 1986;
A
Rainbow trout,
Oncorhynchus mykiss
2,200
Sanders et al. 1983
A
Rainbow trout,
Oncorhynchus mykiss
2,800
Sanders et al. 1983
A
Rainbow trout,
Oncorhynchus mykiss
1,100
Sanders et al. 1983
A
Rainbow trout,
Oncorhynchus mykiss
800
Sanders et al. 1983
A
Rainbow trout,
Oncorhynchus mykiss
1,500
Sanders et al. 1983
4
-------
()\\
MIJR
(iroup11
Species
l.( 50/l.( 50
(Jlg/I.)
SMAY
(fm/i.)
c;may
Reference
A
Rainbow trout,
900
Sanders et al. 1983
Oncorhynchus mykiss
A
Rainbow trout,
800
Sanders et al. 1983
Oncorhynchus mykiss
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
935
Marking et al. 1984
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
1,000
Marking et al. 1984
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
1,400
Marking et al. 1984
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
1,000
Marking et al. 1984
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
1,740
Marking et al. 1984
A
Rainbow trout (juvenile),
Oncorhynchus mykiss
4,835
Douglas et al. 1986
A
Rainbow trout (1.5 g),
Oncorhynchus mykiss
1,200
Mayer and Ellersieck 1986
A
Rainbow trout (0.8 g),
Oncorhynchus mykiss
1,360
Mayer and Ellersieck 1986
A
Rainbow trout (0.8 g),
Oncorhynchus mykiss
2,080
Mayer and Ellersieck 1986
A
Rainbow trout (1.1 g),
Oncorhynchus mykiss
1,900
Mayer and Ellersieck 1986
A
Rainbow trout (1.1 g),
Oncorhynchus mykiss
2,300
Mayer and Ellersieck 1986
A
Rainbow trout (0.5 g),
Oncorhynchus mykiss
1,330
Mayer and Ellersieck 1986
A
Rainbow trout (0.8 g),
Oncorhynchus mykiss
<750
Mayer and Ellersieck 1986
A
Rainbow trout (1.1 g),
Oncorhynchus mykiss
<320
Mayer and Ellersieck 1986
A
Rainbow trout (1.2 g),
Oncorhynchus mykiss
1,090
Mayer and Ellersieck 1986
A
Rainbow trout (1.1 g),
Oncorhynchus mykiss
1,460
Mayer and Ellersieck 1986
A
Rainbow trout (1.2 g),
Oncorhynchus mykiss
3,500
Mayer and Ellersieck 1986
A
Rainbow trout (1.2 g),
Oncorhynchus mykiss
3,000
Mayer and Ellersieck 1986
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
1,600
Mayer and Ellersieck 1986
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
1,100
Mayer and Ellersieck 1986
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
1,200
Mayer and Ellersieck 1986
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
780
Mayer and Ellersieck 1986
A
Rainbow trout (1.0 g),
Oncorhynchus mykiss
1,450
Mayer and Ellersieck 1986
5
-------
()\\
MIJR
(iroup11
Species
l.( 50/l.( 50
(Jlg/I.)
SMAY
(fm/i.)
(;\1AY
(flli/l.)
Reference
A
Rainbow trout (0.48-1.25 g),
Oncorhynchus mykiss
1,880
Dwyeretal. 1995
A
Rainbow trout (juvenile; 2.7 g),
Oncorhynchus mykiss
5,400
Ferrari et al. 2004
A
Rainbow trout (19.7 g),
Oncorhynchus mykiss
860
Phipps and Holcombe 1985
A
Atlantic salmon (0.4 g),
Salmo salar
4,500
Mayer and Ellersieck 1986
A
Atlantic salmon (0.8 g),
Salmo salar
2,070
Mayer and Ellersieck 1986
A
Atlantic salmon (0.8 g),
Salmo salar
1,180
Mayer and Ellersieck 1986
A
Atlantic salmon (0.4 g),
Salmo salar
905
Mayer and Ellersieck 1986
A
Atlantic salmon (0.8 g),
Salmo salar
2,010
Mayer and Ellersieck 1986
A
Atlantic salmon (0.8 g),
Salmo salar
1,430
Mayer and Ellersieck 1986
A
Atlantic salmon (0.2 g),
Salmo salar
500
1,119
Mayer and Ellersieck 1986
A
Atlantic salmon (0.2 g),
Salmo salar
1,000
Mayer and Ellersieck 1986
A
Atlantic salmon (0.2 g),
Salmo salar
1,150
1,510
Mayer and Ellersieck 1986
A
Atlantic salmon (0.2 g),
Salmo salar
1,100
Mayer and Ellersieck 1986
A
Atlantic salmon (0.2 g),
Salmo salar
1,350
Mayer and Ellersieck 1986
A
Atlantic salmon (0.2 g),
Salmo salar
220
Mayer and Ellersieck 1986
A
Atlantic salmon (0.2 g),
Salmo salar
900
Mayer and Ellersieck 1986
A
Atlantic salmon (0.2 g),
Salmo salar
1,000
Mayer and Ellersieck 1986
A
Brown trout,
Salmo trutta
1,950
Macek and McAllister 1970
A
Brown trout (0.6 g),
Salmo trutta
6,300
2,036
Johnson and Finley 1980;
Mayer and Ellersieck 1986
A
Brown trout (fingerling),
Salmo trutta
2,000
Mayer and Ellersieck 1986
A
Brown trout (fry),
Salmo trutta
700
Lakotaetal. 1981
A
Brook trout (1.15 g),
Salvelinus fontinalis
1,070
Post and Schroeder 1971
A
Brook trout (2.04 g),
Salvelinus fontinalis
1,450
1,629
1,269
Post and Schroeder 1971
A
Brook trout (1.0 g),
Salvelinus fontinalis
680
Mayer and Ellersieck 1986
A
Brook trout (0.7 g),
Salvelinus fontinalis
4,560
Mayer and Ellersieck 1986
6
-------
()\\
MIJR
(iroup11
Species
l.( 50/l.( 50
(Jlg/I.)
SMAY
(fm/i.)
(;\1AY
(flli/l.)
Reference
A
Brook trout (0.7 g),
Salvelinus fontinalis
2,130
Mayer and Ellersieck 1986
A
Brook trout (0.7 g),
Salvelinus fontinalis
1,130
Mayer and Ellersieck 1986
A
Brook trout (0.8 g),
Salvelinus fontinalis
1,200
Mayer and Ellersieck 1986
A
Brook trout (0.8 g),
Salvelinus fontinalis
1,290
Mayer and Ellersieck 1986
A
Brook trout (1.3 g),
Salvelinus fontinalis
4,500
Mayer and Ellersieck 1986
A
Lake trout (1.7 g),
Salvelinus namaycush
690
988.1
Johnson and Finley 1980;
Mayer and Ellersieck 1986
A
Lake trout (1.7 g),
Salvelinus namaycush
740
Mayer and Ellersieck 1986
A
Lake trout (1.7 g),
Salvelinus namaycush
920
Mayer and Ellersieck 1986
A
Lake trout (0.5 g),
Salvelinus namaycush
872
Mayer and Ellersieck 1986
A
Lake trout (2.6 g),
Salvelinus namaycush
2,300
Mayer and Ellersieck 1986
B
Goldfish (0.9 g),
Carassius auratus
13,200
14,907
14,907
Macek and McAllister 1970
B
Goldfish (0.9 g),
Carassius auratus
12,800
Mayer and Ellersieck 1986
B
Goldfish (juvenile; 1.3-3.3 g),
Carassius auratus
17,500
Pfeiffer et al. 1997
B
Goldfish (14.2 g),
Carassius auratus
16,700
Phipps and Holcombe 1985
B
Common carp (0.6 g),
Cyprinus carpio
5,280
4,153
4,153
Macek and McAllister 1970
B
Common carp (0.38 g),
Cyprinus carpio
1,700
Chin and Sudderuddin 1979
B
Common carp (fry),
Cyprinus carpio
4,220
Lakotaetal. 1981
B
Common carp (20-34 mm),
Cyprinus carpio
7,850
de Mel and Pathiratne 2005
B
European chub (12.43 cm; 18.14
g)>
Leuciscus cephalus
8,656
8,656
8,656
Verep 2006
B
Fathead minnow (0.5 g),
Pimephales promelas
14,000
7,367
7,367
Mayer and Ellersieck 1986
B
Fathead minnow (0.8 g),
Pimephales promelas
14,600
Macek and McAllister 1970;
Sanders et al. 1983
B
Fathead minnow (0.8 g),
Pimephales promelas
7,700
Mayer and Ellersieck 1986
B
Fathead minnow (larvae),
Pimephales promelas
>1,600
Norberg-King 1989
B
Fathead minnow (0.32-0.56 g),
Pimephales promelas
5,210
Dwyeretal. 1995
B
Fathead minnow (2 mo),
Pimephales promelas
9,000
Carlson 1971
7
-------
()\\
MIJR
(iroup11
Species
l.( 50/l.( 50
(Jlg/I.)
SMAY
(fm/i.)
(;\1AY
(flli/l.)
Reference
B
Fathead minnow (0.3 g),
Pimephales promelas
5,010
Phipps and Holcombe 1985
B
Fathead minnow (28 d),
Pimephales promelas
8,930
Geigeretal. 1985; 1988
B
Fathead minnow (28 d),
Pimephales promelas
10,400
Geigeretal. 1985; 1988
B
Fathead minnow (29 d),
Pimephales promelas
6,670
Geigeretal. 1985; 1988
B
Fathead minnow (31 d),
Pimephales promelas
9,470
Geigeretal. 1985; 1988
B
Bonytail chub (0.29-0.52 g),
Gila elegans
3,490
2,655
2,655
Dwyeretal. 1995
B
Bonytail chub (6 d),
Gila elegans
2,020
Beyers etal. 1994
B
Colorado pikeminnow (0.32-
0.34 g),
Ptychochelius lucius
3,070
2,005
2,005
Dwyeretal. 1995
B
Colorado pikeminnow (26 d),
Ptychochelius lucius
1,310
Beyers etal. 1994
B
Razorback sucker (0.31-0.32 g),
Xyrauchen texanus
4,350
4,350
4,350
Dwyeretal. 1995
B
Black bullhead (1.2 g),
Ameiurus melas
20,000
20,000
20,000
Macek and McAllister 1970
B
Channel catfish (1.5 g),
Ictalurus punctatus
15,800
8,075
8,075
Macek and McAllister 1970
B
Channel catfish (0.3 g),
Ictalurus punctatus
1,300
Brown etal. 1979
B
Channel catfish (1.5 g),
Ictalurus punctatus
7,790
Mayer and Ellersieck 1986
B
Channel catfish (fingerling),
Ictalurus punctatus
17,300
Mayer and Ellersieck 1986
B
Channel catfish (27.6 g),
Ictalurus punctatus
12,400
Phipps and Holcombe 1985
B
Walking catfish (17-18 cm; 60-
70 g),
Clarias batrachus
46,850
27,609
27,609
Tripathi and Shukla 1988
B
Walking catfish (14 cm; 25 g),
Clarias batrachus
16,270
Lata et al. 2001
B
Guppy (2.0 cm),
Poecilia reticulata
2,515
2,515
2,515
Gallo et al. 1995
B
Gila topminnow (219 mg),
Poeciliopsis occidentalis
>3,000
>3,000
>3,000
Dwyeretal. 1999b
B
Striped bass (56 d),
Morone saxatilis
760
1,322
1,322
Palawski et al. 1985
B
Striped bass,
Morone saxatilis
2,300
Palawski et al. 1985
B
Green sunfish (1.1 g),
Lepomis cyanellus
9,460
9,460
9,460
Mayer and Ellersieck 1986
B
Redear sunfish (1.1 g),
Lepomis microlophus
11,200
11,200
7,920
Macek and McAllister 1970
8
-------
()\\
MIJR
(iroup11
Species
l.( 50/l.( 50
(Jlg/I.)
SMAY
(fm/i.)
(;\1AY
(flli/l.)
Reference
B
Bluegill,
Lepomis macrochirus
14,000
McCann and Young 1969
B
Bluegill (1.2 g),
Lepomis macrochirus
6,760
Macek and McAllister 1970
B
Bluegill,
Lepomis macrochirus
16,000
Sanders et al. 1983
B
Bluegill,
Lepomis macrochirus
8,200
Sanders et al. 1983
B
Bluegill,
Lepomis macrochirus
5,400
Sanders et al. 1983
B
Bluegill,
Lepomis macrochirus
5,200
Sanders et al. 1983
B
Bluegill,
Lepomis macrochirus
1,800
Sanders et al. 1983
B
Bluegill,
Lepomis macrochirus
2,200
Sanders et al. 1983
B
Bluegill,
Lepomis macrochirus
1,000
Sanders et al. 1983
B
Bluegill (1.2 g),
Lepomis macrochirus
5,230
Mayer and Ellersieck 1986
B
Bluegill (0.6 g),
Lepomis macrochirus
5,047
5,261
Mayer and Ellersieck 1986
B
Bluegill (0.4 g),
Lepomis macrochirus
7,400
Mayer and Ellersieck 1986
B
Bluegill (0.4 g),
Lepomis macrochirus
5,200
Mayer and Ellersieck 1986
B
Bluegill (0.8 g),
Lepomis macrochirus
16,000
Mayer and Ellersieck 1986
B
Bluegill (0.8 g),
Lepomis macrochirus
7,000
Sanders et al. 1983; Mayer
and Ellersieck 1986
B
Bluegill (0.8 g),
Lepomis macrochirus
8,200
Mayer and Ellersieck 1986
B
Bluegill (0.4 g),
Lepomis macrochirus
6,200
Mayer and Ellersieck 1986
B
Bluegill (0.7 g),
Lepomis macrochirus
5,400
Mayer and Ellersieck 1986
B
Bluegill (0.7 g),
Lepomis macrochirus
5,200
Mayer and Ellersieck 1986
B
Bluegill (0.7 g),
Lepomis macrochirus
1,800
Mayer and Ellersieck 1986
B
Bluegill (0.7 g),
Lepomis macrochirus
2,600
Mayer and Ellersieck 1986
B
Bluegill (0.5 g),
Lepomis macrochirus
6,970
Phipps and Holcombe 1985
B
Largemouth bass (0.9 g),
Micropterus salmoides
6,400
6,400
6,400
Macek and McAllister 1970
B
Black crappie (1.0 g),
Pomoxis nigromaculatus
2,600
2,600
2,600
Johnson and Finley 1980;
Mayer and Ellersieck 1986;
B
Greenthroat darter (133 mg),
Etheostoma lepidum
2,140
2,140
2,079
Dwyeretal. 1999b
9
-------
()\\
MIJR
(iroup11
Species
l.( 50/l.( 50
(Jlg/I.)
SMAY
(fm/i.)
(;\1AY
(flli/l.)
Reference
B
Fountain darter (62 mg),
Etheostoma fonticola
2,020
2,020
Dwyer et al. 2005
B
Yellow perch (1.4 g),
Perca flavescens
745
2,480
2,480
Macek and McAllister 1970
B
Yellow perch (0.6 g),
Perca flavescens
5,100
Johnson and Finley 1980;
Mayer and Ellersieck 1986
B
Yellow perch (1.0 g),
Perca flavescens
13,900
Mayer and Ellersieck 1986
B
Yellow perch (1.0 g),
Perca flavescens
5,400
Mayer and Ellersieck 1986
B
Yellow perch (1.0 g),
Perca flavescens
3,400
Mayer and Ellersieck 1986
B
Yellow perch (1.0 g),
Perca flavescens
1,200
Mayer and Ellersieck 1986
B
Yellow perch (0.9 g),
Perca flavescens
4,000
Mayer and Ellersieck 1986
B
Yellow perch (0.9 g),
Perca flavescens
4,200
Mayer and Ellersieck 1986
B
Yellow perch (0.9 g),
Perca flavescens
480
Mayer and Ellersieck 1986
B
Yellow perch (0.9 g),
Perca flavescens
350
Mayer and Ellersieck 1986
B
Yellow perch (1.0 g),
Perca flavescens
3,800
Mayer and Ellersieck 1986
B
Yellow perch (1.0 g),
Perca flavescens
5,000
Mayer and Ellersieck 1986
B
Yellow perch (1.0 g),
Perca flavescens
3,750
Mayer and Ellersieck 1986
B
Yellow perch (fingerling),
Perca flavescens
1,420
Mayer and Ellersieck 1986
B
Shortnosed sturgeon,
Acipenser brevirostrum
1,810
1,810
1,810
Dwyer et al. 2000
B
Nile tilapia (45-55 mm; 3.17 g),
Oreochromis niloticus
2,930
2,930
2,930
dela Cruz and Cagauan 1981
C
Green frog (Gosner stage 25
tadpole),
Rana clamitans
22,020
16,296
16,296
Boone and Bridges 1999
C
Green frog (Gosner stage 25
tadpole),
Rana clamitans
17,360
Boone and Bridges 1999
C
Green frog (Gosner stage 25
tadpole),
Rana clamitans
11,320
Boone and Bridges 1999
C
Boreal toad (200 mg),
Bufo boreas
12,310
12,310
12,310
Dwyer etal. 1999b
C
Gray tree frog (tadpole),
Hyla versicolor
2,470
2,470
2,470
Zagaetal. 1998
C
African clawed frog (embryo),
Xenopus laevis
15,250
5,136
5,136
Zagaetal. 1998
C
African clawed frog (tadpole),
Xenopus laevis
1,730
Zagaetal. 1998
10
-------
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark value for carbaryl is 0.85 |ig/L, which is V2 the LC50 of
1.7 |ig/L, the stonefly Pteronarcella badia as described above.
The OPP fish acute benchmark value is 110 |ig/L, which is V2 the LC50 of 220 |ig/L for the
Atlantic salmon (Salmo salaf).
OW Acute Criterion
The acute criterion, or CMC, for carbaryl is 2.1 |ig/L (U.S. EPA 2012).
Genus-Level Invertebrate-Only HC05
The invertebrate acute HC05 OW calculated using invertebrate genera data only is shown in
Table 2. The invertebrate-only value was calculated following the U.S. EPA (1985)
methodology, resulting in a value of 3.074 |ig/L (Table 3).
Table 2. Carbaryl invertebrate SMAVs and GMAVs (ng/L).
(iOIIIIS
Species
SMAY
CMAY
CMAY Kiink
Aplexa
hyonorum
27,000
27,000
20
Anodonta
imbecillis
24,632
24,632
19
Lumbriculus
variegatus
8,200
8,200
18
Orconectes
virilis
2,112
2,462
17
Orconectes
immunis
2,870
Procambarus
clarkii
1,000
1,378
16
Procambarus
sp.
1,900
Cambarus
bartoni
839.6
840
15
Asellus
brevicaudus
280
280
14
Pontoporeia
hoyi
250
250
13
Mysis
relicta
230
230
12
Notonecta
undulata
200
200
11
Daphnia
magna
29.66
18.80
10
Daphnia
pulex
6.4
Daphnia
carinata
35
Gammarus
pseudolimnaeus
9.654
16.76
9
Gammarus
lacustris
18.76
Gammarus
fasciatus
26.00
Hyalella
azteca
15.2
15.2
8
Pteronarcella
badia
9.163
9.163
7
Simocephalus
serrulatus
8.781
8.781
6
Ceriodaphnia
dubia
5.958
5.958
5
11
-------
Genus
Species
SMAV
GMAV
GMAV Rank
Claassenia
sabulosa
5.6
5.6
4
Pteronarcvs
californica
4.8
4.8
3
Skwala
sp.
3.6
3.6
2
Isogemis
sp.
3.175
3.175
1
Table 3. Invertebrate-Only acute HCos value calculated using the only the genus-level
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
20
4
5.6
1.723
2.97
0.1905
0.4364
3
4.8
1.569
2.46
0.1429
0.3780
2
3.6
1.281
1.64
0.0952
0.3086
1
3.175
1.155
1.335
0.0476
0.2182
Sum:
5.73
8.40
0.4762
1.3412
S2 =
7.654
L =
0.504
A =
1.123
hc05 =
3.074
Table 4. Summary and comparison of acute values for carbaryl.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP Invertebrate
ALB
(lowest LCso/2)
(Year published,
species)
OW ALC (FAV/2)
(Year published,
# of genera,
magnitude relative to
ALB)
OW Genus-level
Invertebrate-only
HCos/2
(# of genera, magnitude
relative to ALB)
Notes
Carbaryl
0.85 ng/L
(2022; P. badia)
2.1 (ig/L
(2012, 47 genera,
0.40X)
1.54 (ig/L
(20 genera, 0.55X)
FIFRA ALB is based on one of
four LCso values used to
generate the P. badia SMAV of
9.163 |ig/L in the 2012 carbaryl
ALC.
Figure 1 shows a genus-level sensitivity distribution for the carbaryl dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the CMC, invertebrate HCos/2, and OPP acute benchmark values are also included.
12
-------
100,000.00
10,000.00
1,000.00
bJD
u.
ro
-Q
nj
U
100.00
10.00
1.00
•
Arthropod
o
Annelid
A
Mollusk
¦
Salmonid Fish
~
Other Fish
~
Amphibian
CMC
Genus-level Invertebrate
OPP Invert. Benchmark
OPP Fish Benchmark
~ ~
~ •
Cambarus •
Pontoporeia
•Asellus
* N.
~ ~
Anodonta .
>A AD
~ ~ f
„ * Aplexa
D ~ ~ ~ ° ~
Lumbriculus
Orconectes
Procambarus
Notonecta i
LMysis.
OPP Fish Benchmark= 110 ng/L
_ •Daphnia
Simocephalus
\ Hyalella
Claassen,a\^ '^Gammarus
• «c- Pteronarcella
^Ceriodaphnia
^Ptexonarcys
"Skwala
X
FAV/2 = Criterion Maximum Concentration = 2.1 |_ig/L
Isogenus
• Genus-level Invertebrate HC05/2 = 1.537 ng/L
OPP Invertebrate Benchmark = 0.85 ng/L
0.10
0.0
0.1
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Carbaryl genus-level SD.
Symbols represent GMAVs calculated using all quantitative data from the aquatic life criteria document for carbaryl (U.S. EPA 2012),
and additional data from the OPP benchmark document for carbaryl (U.S. EPA 2007).
13
-------
1.1.1.2 Carbaryl Chronic Toxicity Data
For chemicals lacking sufficient chronic data to satisfy the minimum taxonomic data
requirements, such as the pesticide carbaryl, EPA Office of Water (OW) calculates the final
chronic value (FCV) as the final acute value (FAV) divided by the final acute-to chronic ratio
(FACR). The Office of Pesticide Programs (OPP) will also apply Acute to Chronic Ratios
(ACRs) to acute data to calculate chronic benchmarks when chronic test data are not available.
Calculations of ACRs following OPP and OW methodologies were conducted, and the effects of
these ACRs on the resulting OPP and OW chronic values were compared.
Chronic Data Sources
The primary data source for this analysis was the 2012 freshwater carbaryl criteria document
(U.S. EPA 2012). The OPP-authored carbaryl problem formulation (U.S. EPA 2010) and
California red legged frog effects determination (U.S. EPA 2007) reports were also examined.
The latter reports did not include additional test data but did report test concentrations used to
calculate ACRs that were used to calculate chronic benchmarks. In addition, one chronic value
for Ceriodaphnia dubia was obtained from Oris et al. (1991) that was not included in the other
data sources.
ACR Calculations
ACR calculations following OW and OPP methodologies are described below. All available
chronic carbaryl data are shown in Table 5. All available acute data for species that also have
chronic data are shown in Table 6. Table 7 lists all ACRs by species and calculation method.
Invertebrate ACRs
Ceriodaphnia dubia
The ACR following the OW approach is 1.328, calculated as the acute value from Oris et al.
(1991) divided by the geometric mean of the MATCs from two replicate chronic tests performed
in the same laboratory.
The ACR following the OPP approach is 1.609, calculated as the acute value from Oris et al.
(1991) divided by the geometric mean of the NOECs from two replicate chronic tests performed
in the same laboratory as per the OPP ACR guidelines (U.S. EPA 2005).
Daphnia magna
The ACR described in the 2012 ALC deviated from the conventional OW approach. Brooke
(1991) conducted paired acute and chronic tests, with an EC50 of 10.1 ng/L, a NOEC of 4.04
Hg/L, and a LOEC of >4.04 ng/L. Because there was no MATC, OW noted the "theoretical
ACR" could fall anywhere between 1.0-2.5, and estimated the ACR as 1.581, calculated as the
acute value (10.1 ng/L) divided by the geometric mean of the NOEC and the acute value (6.388
Hg/L)-
The ACR following the OPP approach is 2.5, calculated as the acute value from Brooke (1991)
divided by the NOEC for the paired chronic test.
14
-------
Americamysis bahia
The ACR following the OW approach is 0.8530, calculated as the acute value of 8.46 ng/L from
Thursby and Champlin (1991) divided by the MATC of 9.918 ng/L from the paired chronic test.
The ACR following the OPP approach is 1.178, calculated as the acute value of 8.46 ng/L from
Thursby and Champlin (1991) divided by the No Observed Effect Concentration (NOEC) of 7.18
Hg/L from the paired chronic test. As described in the carbaryl ALC document, these ACRs are
treated as qualitative because control survival and number of young produced per female did not
meet American Society for Testing and Materials (ASTM) test requirements (U.S. EPA 2012).
Vertebrate (Fish) ACRs
Gila elegans
An ACR for this species could not be calculated following the OW approach. Beyers et al.
(1994) performed an early life stage (ELS) chronic test and a static renewal acute test. Although
the acute and chronic tests were performed in the same laboratory, the Guidelines (U.S. EPA
1985) specifies that acute test data should also be from a flow through study (except for
Daphnids, where static acute tests are acceptable). The ACR following the more flexible OPP
approach is 3.108, calculated as the acute value of 2,020 ng/L from Beyers et al. (1994) divided
by the NOEC of 650 ng/L from ELS test performed in the same laboratory.
Pimephales promelas
Two ACRs fori5, promelas could be calculated following the OW approach. An ACR of 23.82
was calculated as the acute value of 9,000 ng/L reported in Carlson (1971) divided by the MATC
of 377.9 ng/L from a paired life cycle test. An ACR of 6.256 was calculated using test data from
three studies performed at the same laboratory. The geometric mean of two acute LC50s from
tests performed at the same laboratory, 9,000 |ag/L as reported in Carlson (1971) and 5,100 |ag/L
as reported in Phipps and Holcombe (1985) was divided by the MATC of 1,073 |ag/L from an
ELS test performed in the same laboratory (Norberg-King 1989). Because ACRs calculated from
life cycle tests are preferable to those calculated from ELS test, the ACR of 23.82 is used for this
species.
The corresponding P. promelas ACRs calculated following the OPP approach are 42.86 for the
life cycle ACR and 9.326 for the ELS ACR, using the acute data described above divided by a
NOEC of 210 |ag/L from the life cycle test (Carlson 1971), and a NOEC of 720 ng/L from the
ELS test (Norberg-King 1989). As described above, the life cycle ACR of 42.86 is used by OPP
for this species.
Ptychocheilus lucius
An ACR for this species could not be calculated following the OW approach. Beyers et al.
(1994) performed an early life stage (ELS) chronic test and a static renewal acute test. Although
the acute and chronic tests were performed in the same laboratory, the Guidelines (U.S. EPA
1985) specifies that acute test data should also be from a flow through study (except for
Daphnids, where static acute tests are acceptable). Also worth noting is the study authors
reported that the water for the acute and chronic tests was inadvertently aged differently, with the
acute tests having higher dissolved oxygen and pH, and lower hardness and alkalinity, than the
chronic tests.
15
-------
The ACR following the more flexible OPP approach is 2.944, calculated as the acute value of
1,310 |ag/L from Beyers et al. (1994) divided by the NOEC of 445 ng/L from ELS test
performed in the same laboratory. Despite the differences in water quality from the acute and
chronic Beyers et al. (1994) tests, they were still treated as being more similar to one another
than the other acute test for this species, which was an unmeasured static test (Dwyer et al.
1995).
Final ACRs
The final ACRs (FACRs) for the two approaches, expressed as the geometric mean of all
available ACRs, is 3.684 following the OW approach, and 4.361 following the OPP approach.
The OW FACR consists of ACRs for C. dubia, I), magna (using the estimated Maximum
Acceptable Toxicant Concentration (MATC) following the 2012 ALC methodology), and the life
cycle ACR for P. promelas.
The Guidelines (U.S. EPA 1985) specify that if the ACRs appear to increase or decrease as the
species mean acute values (SMAVs) increase, the FACR should be calculated as the geometric
mean for those species whose SMAVs are close to the final acute value (FAV).This is the case
for carbaryl, and following the approach used in the 2005 ALC, the FACR is calculated as the
geometric mean of the acutely sensitive invertebrate species. When limited to invertebrate
species, the FACR following the OW approach is calculated as the geometric mean of the ACRs
for C. dubia (1.328) and D. magna (1.581). Because the final chronic value cannot be larger than
the final acute value, the calculated ACR of 1.449 is rounded up to 2. The invertebrate-only
FACR following the OPP approach, but applying the Guidelines stipulation that the FACR
should be calculated using species with SMAVs close to the FAV if ACRs are proportional to
acute sensitivity, is the geometric mean of the ACRs for C. dubia (1.609) and D. magna (2.5), or
2.006.
The OPP FACR consists of ACRs for C. dubia, D. magna, and P. promelas, as well as G.
elegans, and P. lucius. The A. bahia qualitative ACR was not included here because the chronic
test did not meet ASTM test acceptability guidelines.
Comparison of Freshwater Chronic Values for Carbaryl
OPP Chronic Benchmarks
For carbaryl, the freshwater invertebrate chronic benchmark is 0.5 |ig/L, calculated as an LC50
of 1.7 |ig/L for Pteronarcella badia (Mayer and Ellersieck 1986) divided by the OPP-calculated
ACR of 3.73 for D. magna.
The freshwater fish chronic benchmark is 6.8 |ig/L, calculated as the LC50 of 250 |ig/L for
Salmo salar divided by the OPP-calculated ACR of 36.67 for P. promelas.
OW Freshwater Chronic Values - All Taxa
Final chronic concentrations following the ACR methodology are calculated by dividing the final
acute value by a final ACR (FACR). For carbaryl, the FAV calculated using data from all taxa is
4.219 |ag/L (U.S. EPA 2012). The final chronic value following the OW-ACR approach is 2.110
Hg/L (4.219 |ag/L 2), and the final chronic value following the OPP-ACR approach (with the
Guidelines stipulation described above) is 2.103 |ag/L (4.219 |ag/L ^ 2.006).
16
-------
OW Freshwater Chronic Values - Invertebrate-Only Data
Final chronic concentrations for the invertebrate-only carbaryl dataset are calculated by dividing
the final invertebrate acute value by an ACR. This dataset was comprised of acute invertebrate
test data found in the 2012 ALC and Appendix L of U.S. EPA (2007). The resulting acute HCos
calculated from the 20 invertebrate genera using the calculated following the Guidelines (U.S.
EPA 1985) methodology was 3.074 ng/L. The final invertebrate chronic value following the
OW-ACR approach is 1.537 ng/L (3.074 ng/L -h 2), and the final chronic value following the
OPP-ACR approach is 1.532 jig/L (3.074 jig/L - 2.006).
Table 8 lists all chronic values calculated following the different approaches.
17
-------
Table 5. Chronic test data for carbaryl.
All concentrations expressed as ng/L, values are grouped by genus.
Genus
Species
NOEC
LOEC
MATC
Reference
Test data reported in:
Notes
2012 ALC
2007
OPP
2010
OPP
Invertebrates
Ceriodaphnia
dubia
8
14
10.58
Oris et al. 1991
Appendix C
Ceriodaphnia
dubia
6.5
8
7.211
Oris et al. 1991
Appendix Cb
Daphnia
magna
1.5
3.3
2.225
Surprenant 1985
Appendix C
Table 21
Daphnia
magna
4.04
>4.04
6.388°
Brooke 1991
Appendix C
Americamysis
bahia
7.18
13.7
9.918
Thursby and
Champlin 1991
Appendix D
Low control survival
and young per female
Vertebrates
Gila
elegans
650
1,240
897.8
Beyers et al.
1994
Appendix C
ELS test
Pimephales
promelas
210
680
377.9
Carlson 1971
Appendix C
Life cycle test
Pimephales
promelas
720
1,600
1,073
Norberg-King
1989
Appendix C
ELS test
Ptychocheilus
lucius
445
866
620.8
Beyers et al.
1994
Appendix C
ELS test
a- Estimated from Figure 1 of Oris et al. (1991) using WebPlotDigitizer (https://automeris.io/WebPlotDigitizer/)
b- Reported in Table 2 of Oris et al. (1991)
Calculated in 2012 ALC as geometric mean of NOEC and acute value
18
-------
Table 6. Acute Carbaryl Test Data for Species with Chronic Data.
All concentrations expressed as ng/L.
Genus
Species
EC50 or
LC50
Reference
Test data reported in:
2012 ALC
2007 OPP
2010
OPP
Notes
Invertebrates
Ceriodaphnia
dubia
11.6
Oris et al. 1991
Appendix A
Paired with Oris et al. 1991 chronic values
Ceriodaphnia
dubia
3.6
Brooke 1990, 1991
Appendix A
Not used
Daphnia
magna
12
Lakotaetal. 1981
Appendix A
Not used
Daphnia
magna
5.6
Sanders et al. 1983
Appendix A
Table 21
Not used
Daphnia
magna
10.1
Brooke 1991
Appendix A
Paired with Brooke 1991 chronic values
Americamysis
bahia
IA6
Thursby and Champlin
1991
Appendix B
Paired with Thursby and Champlin 1991
chronic values
Americamysis
bahia
5.7
Lintott 1992a
Appendix B
Table 4
Not used
Vertebrates
Gila
elegans
2,020
Beyers etal. 1994
Appendix A
Paired with Beyers et al. 1994 chronic
value (OPP-ACR only)
Gila
elegans
3,490
Dwyeretal. 1995
Appendix A
Not used
Pimephales
promelas
14,000
Mayer and Ellersieck 1986
Appendix A
Not used
Pimephales
promelas
14,600
Macek and McAllister
1970; Sanders etal. 1983
Appendix A
Not used
Pimephales
promelas
7,700
Mayer and Ellersieck 1986
Appendix A
Not used
Pimephales
promelas
>1,600
Norberg-King 1989
Appendix A
Not used
Pimephales
promelas
5,210
Dwyeretal. 1995
Appendix A
Not used
Pimephales
promelas
9,000
Carlson 1971
Appendix A
Paired with Carlson 1971 (LC-ACR) and
Norberg-King 1989 (ELS ACR) chronic
value
Pimephales
promelas
5,010
Phipps and Holcombe
1985
Appendix A
Paired with Norberg-King 1989 (ELS
ACR) chronic value
Pimephales
promelas
9,470
Geigeretal. 1985; 1988
Appendix A
Not used
Pimephales
promelas
8,930
Geigeretal. 1985; 1988
Appendix A
Not used
Pimephales
promelas
10,400
Geigeretal. 1985; 1988
Appendix A
Not used
Pimephales
promelas
6,670
Geigeretal. 1985; 1988
Appendix A
Not used
Ptychocheilus
lucius
1,310
Beyers etal. 1994
Appendix A
Paired with Beyers et al. 1994 chronic
value (OPP-ACR only)
Ptychocheilus
lucius
3,070
Dwyeretal. 1995
Appendix A
Not used
19
-------
Table 7. ACRs by species and calculation method.
Genus
Species
ACR
Notes
OW-ACR
OPP-ACR
Invertebrates
Ceriodaphnia
dubia
1.328
1.609
Daphnia
magna
1.581
2.5
Americamvsis
bahia
0.8530
1.178
Qualitative ACR
Vertebrate
Gila
elegans
N/A
3.108
ELS chronic test
Pimephales
promelas
23.82
42.86
Life cycle chronic test
Pimephales
promelas
6.256
9.326
ELS chronic test
Ptvchocheilus
lucius
N/A
2.944
ELS chronic test
All Taxa"
3.684
4.361
All Invertebrates (FACR)
2
2.006
OW-FACR rounded up to 2
1 Of the two ACRs for P. promelas, only the life cycle test was included in this calculation.
Table 8. Summary and comparison of freshwater chronic values for carbaryl.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP Most Sensitive ALB
(Year published, species)
OW ALC (# of ACRs filled,
magnitude relative to ALB)
OW Invertebrate-only
HCos
(# of ACRs filled,
magnitude relative to ALB)
Carbaryl
0.5 ng/L
(2022; estimated NOAEC value for
Pteronarcella badia calculated using
the ACR for Daphnia magna)
2.1 (ig/L
(ALC, 0.24X)
1.54 (ig/L
(0.32X)
1.1.1.3 Carbaryl References
MRID 40098001: Mayer, F.L. and M.R. Ellersieck. 1986. Manual of acute toxicity:
Interpretation and data base for 410 chemicals and 66 species of freshwater animals. Resour.
Publ. No. 160, U.S. Dep. Interior, Fish Wildl. Serv., Washington, DC. 505 p.
Andreu-Moliner, E.S., M.M. Almar, I. Legarra and A. Nunez. 1986. Toxicity of some ricefteld
pesticides to the crayfish P. clarkii, under laboratory and field conditions in Lake Albufera
(Spain). J. Environ. Sci. Health Part B. 21(6): 529-537.
Bailey, H.C., and D.H.W. Liu. 1980. Lumbriculus variegatus, a Benthic Oligochaete, as a
Bioassay Organism. ASTM Spec. Tech. Publ., 205-215.
Beyers, D.W., T.J. Keefe and C.A. Carlson. 1994. Toxicity of carbaryl and malathion to two
federally endangered fishes, as estimated by regression and ANOVA. Environ. Toxicol. Chem.
13(1): 101-107.
Boone, M.D. and C.M. Bridges. 1999. The effect of temperature on the potency of carbaryl for
survival of tadpoles of the green frog (Rana clamitans). Environ. Toxicol. Chem. 18(7): 1482
1484.
20
-------
Brooke, L.T. 1990. Center for Lake Superior Environmental Studies, University of Wisconsin
Superior, Superior, WI. (Memorandum to R.L. Spehar, U.S. EPA, Duluth, MN. January 30).
Brooke, L.T. 1991. Results of freshwater exposures with the chemicals atrazine, biphenyl,
butachlor, carbaryl, carbazole, dibenzofuran, 3,3'-dichlorobenzidine, dichlorvos, 1,2-
epoxyethylbenzene (styrene oxide), isophorone, isopropalin, oxychlordane, pentachloroanisole,
propoxur (baygon), tetrabromobisphenol a, 1,2,4,5-tetrachlorobenzene, and 1,2,3-
trichloropropane to selected freshwater organisms. Center for Lake Superior Environmental
Studies, University of Wisconsin-Superior, Superior, WI. 110 p.
Brown, K.W., D.C. Anderson, S.G. Jones, L.E. Deuel and J.D. Price. 1979. The relative toxicity
of four pesticides in tap water and water from flooded rice paddies. Int. J. Environ. Stud. 14(1):
49-53.
Carlson, A.R. 1971. Effects of long-term exposure to carbaryl (sevin) on survival, growth, and
reproduction of the fathead minnow (Pimephales promelas). J. Fish. Res. Board Canada. 29: 583-
587.
Chin, Y.N. and K.I. Sudderuddin. 1979. Effect of methamidophos on the growth rate and
esterase activity of the common carp Cyprinus carpio L. Environ. Pollut. 18(3): 213-220.
de Mel, G.W.J.L.M.V.T.M. and A. Pathiratne. 2005. Toxicity assessment of insecticides
commonly used in rice pest management to the fry of common carp, Cyprinus carpio, a food fish
culturable in rice fields. J. Appl. Ichthyol. 21(2): 146-150.
dela Cruz, C.R. and A.G. Cagauan. 1981. Preliminary study on the bioassay of seven pesticides
and five weedicides with tilapia, carps, clam and shrimp as test species. Fish. Res. J. Philipp.
6(1): 11-18.
Douglas, M.T., D.O. Chanter, I.B. Pell and G.M. Burney. 1986. A proposal for the reduction of
animal numbers required for the acute toxicity to fish test (LC50 determination). Aquat. Toxicol.
8(4): 243-249.
Dwyer, F.J., L.C. Sappington, D.R. Buckler and S.B. Jones. 1995. Use of surrogate species in
assessing contaminant risk to endangered and threatened fishes. EPA/600/R-96/029, U.S. EPA,
Washington, D.C.
Dwyer, F.J., D.K. Hardesty, C.E. Henke, C.G. Ingersoll, D.W. Whites, D.R. Mount and C.M.
Bridges. 1999b. Assessing contaminant sensitivity of endangered and threatened species:
Effluent toxicity tests. EPA 600/R-99/099, U.S. EPA, Washington, D.C.
Dwyer, F.J., D.K. Hardesty, C.G. Ingersoll, J.L. Kunz and D.W. Whites. 2000. Assessing
contaminant sensitivity of American shad, Atlantic sturgeon and shortnose sturgeon, Final
Report - February 2000. Final Rep., U.S. Geol. Surv., Columbia Environ. Res. Ctr., Columbia,
MO.
Dwyer, F.J., F.L. Mayer, L.C. Sappington, D.R. Buckler, C.M. Bridges, I.E. Greer, D.K.
Hardesty, C.E. Henke, C.G. Ingersoll, J.L. Kunz, D.W. Whites, T. Augspurger, D.R. Mount, K.
Hattala, and G.N. Neuderfer. 2005. Assessing contaminant sensitivity of endangered and
threatened aquatic species: Part I. Acute toxicity of five chemicals. Arch. Environ. Contam.
Toxicol. 48: 143-154.
21
-------
Federle, P.F. and W.J. Collins. 1976. Insecticide toxicity to three insects from Ohio ponds. Ohio
J. Sci. 76(1): 19-24.
Ferrari, A., O.L. Anguiano, J. Soleno, A. Venturino and A.M. Pechen de D' Angelo. 2004.
Different susceptibility of two aquatic vertebrates (Oncorhynchus mykiss and Bufo arenarum) to
azinphos methyl and carbaryl. Compar. Biochem. Physiol. Part C. 139: 239-243.
Gallo, D., A. Merendino, J. Keizer, and L.Vittozzi. 1995. Acute toxicity of two carbamates to the
guppy (Poecilia reticulata) and the zebrafish (Brachydanio rerio). Sci. Total Environ. 171: 131
136.
Geiger, D. L., C.E. Northcott, D.J. Call and L.T. Brooke. 1985. Acute toxicities of organic
chemicals to fathead minnows (Pimephales promelas). Vol. 2. Center for Lake Superior
Environmental Studies, Univ. of Wisconsin-Superior, Superior, WI.
Geiger, D.L., D.J. Call and L.T. Brooke. 1988. Acute toxicities of organic chemicals to fathead
minnows (Pimephales promelas) Volume IV. Center for Lake Superior Environmental Studies,
University of Wisconsin-Superior, WI.
Johnson, I C., A.E. Keller and S.G. Zam. 1993. A method for conducting acute toxicity tests with
the early life stages of freshwater mussels. In: Environmental toxicology and risk assessment.
Landis, W.G., J.S. Hughes and M.A. Lewis (Eds.), ASTM STP 1179. American Society for
Testing and Materials, Philadelphia, PA. pp. 381-396.
Johnson, W.W. and M.T. Finley. 1980. Handbook of acute toxicity of chemicals to fish and
aquatic invertebrates. Resour. Publ. 137, Fish Wildl. Serv., U.S. D.I., Washington, D.C. 98 p.
Katz, M. 1961. Acute toxicity of some organic insecticides to three species of salmonids and to
the threespine stickleback. Trans. Am. Fish. Soc. 90: 264-268.
Lakota, S., A. Raszka and I. Kupczak. 1981. Toxic effect of cartap, carbaryl, and propoxur on
some aquatic organisms. Acta Hydrobiol. 23(2): 183-190.
Landrum, P.F. and W.S. Dupuis. 1990. Toxicity and toxicokinetics of pentachlorophenol and
carbaryl to Pontoporeia hoyi and Mysis relicta. In: Aquatic toxicology and risk assessment, 13th
Volume. Landis, W.G. and W.H. Van der Schalie (Eds.). ASTM STP 1096. American Society
for Testing and Materials, Philadelphia, PA. pp. 278-289.
Lata, S., K. Gopal, and N.N. Singh. 2001. Toxicological Evaluations and Morphological Studies
in a Catfish Clarias batrachus Exposed to Carbaryl and Carbofuran. J. Ecophysiol. Occup. Health
1(1-2): 121-130.
Lintott, D.R. 1992. Carbaryl technical: acute toxicity to the mysid, Mysidopsis bahia, under
flow-through test conditions. Laboratory Project ID: J9112004a. Study performed by Toxikon
Environmental Sciences for Rhone-Poulenc Ag Company.
Macek, K.J. and W.A. McAllister. 1970. Insecticide susceptibility of some common fish family
representatives. Trans. Am. Fish. Soc. 99(1): 20-27.
Marking, L.L., T.D. Bills and J.R. Crowther. 1984. Effects of five diets on sensitivity of rainbow
trout to eleven chemicals. Prog. Fish-Cult. 46: 1-5.
22
-------
Mayer, F.L. and M.R. Ellersieck. 1986. Manual of acute toxicity: Interpretation and database for
410 chemicals and 66 species of freshwater animals. Resour. Publ. No. 160, U.S. Dep. Interior,
Fish Wildl. Serv., Washington, DC. 505 p.
McCann, J.A. and R. Young. 1969. Sevin: toxicity to bluegill: test no. 142. U.S. Agricultural
Research Service, Pesticides Regulation Div., Animal Biology Laboratory. Unpublished study;
CDL: 104387-A.
McNulty, E.W., F.J. Dwyer, M.R. Ellersieck, E.I. Greer, C.G. Ingersoll and C.F. Rabeni. 1999.
Evaluation of ability of reference toxicity tests to identify stress in laboratory populations of the
amphipod Hyalella azteca. Environ. Toxicol. Chem. 18(3): 544-548.
Norberg-King, T.J. 1989. An evaluation of the fathead minnow seven-day subchronic test for
estimating chronic toxicity. Environ. Toxicol. Chem. 8(11): 1075-1089.
Oris, J.T., R.W. Winner and M.V. Moore. 1991. A four-day survival and reproduction toxicity
test for Ceriodaphnia dubia. Environ. Toxicol. Chem. 10(2): 217-224.
Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and
inorganic contaminants in fresh and saline waters. Trans. Am. Fish. Soc. 114(5): 748-753.
Pfeiffer, C.J., B. Qiu and C.H. Cho. 1997. Electron microscopic perspectives of gill pathology
induced by 1-naphthyl-N-methylcarbamate in the goldfish (Carassius auratus Linnaeus). Histol.
Histopathol. 12(3): 645-653.
Phipps, G.L. and G.W. Holcombe. 1985. A method for aquatic multiple species toxicant testing:
Acute toxicity of 10 chemicals to 5 vertebrates and 2 invertebrates. Environ. Pollut. Ser. A 38(2):
141-157.
Phipps, G.L. and G.W. Holcombe. 1990. Toxicity of sevin (carbaryl) to Chinook salmon. U.S.
EPA, Duluth, MN. (Memorandum to L. Brooke, Center of Lake Superior Environmental Studies,
University of Wisconsin-Superior, WI. September 11).
Post, G. and T.R. Schroeder. 1971. The toxicity of four insecticides to four salmonid species.
Bull. Environ. Contam. Toxicol. 6(2): 144-155.
Sanders, H.O. 1969. Toxicity of pesticides to the crustacean Gammarus lacustris. Tech. Pap. No.
25, U.S. D.I., Bur. Sports Fish. Wildl., Fish Wildl. Serv., Washington, D.C. 18 p.
Sanders, H.O. and O.B. Cope. 1966. Toxicities of several pesticides to two species of
cladocerans. Trans. Am. Fish. Soc. 95(2): 165-169.
Sanders, H.O., M.T. Finley and J.B. Hunn. 1983. Acute toxicity of six forest insecticides to three
aquatic invertebrates and four fishes. Tech. Pap. No. 110, U.S. Fish Wildl. Serv., Washington,
D.C. pp.1-5.
Santharam, K.R., B. Thayumanavan and S. Krishnaswamy. 1976. Toxicity of some insecticides
to Daphnia carinata King, and important link in the food chain in the freshwater ecosystems.
Indian J. Ecol. 3: 70-73.
Schafers, C. 2002. Chloroperla grammatica, Acute toxicity test, 96 h exposure: carbaryl;
substance, technical. Lab Project Number: C018556: ACS-001/4-26/N. Unpublished study
23
-------
prepared by Fraunhofer-Institute for Molecular Biology and Applied Ecology. 31 p. {OPPTS
850.1020}.
Simon, K.A. 1982. Acute toxicity of carbaryl, alpha naphthol and sevin-4-oil tank mix to
Cambarus bartoni and Orconectes virilis. In: Environmental monitoring report from the 1982
Maine cooperative spruce budworm suppression project. Maine Forest Service, Dept. of
Conservation, Augusta, ME. pp. 61-91.
Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. 1985.
Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic
Organisms and their Uses. PB85-227049. Office of Research and Development. Duluth, MN,
Narragansett, RI, Corvallis, OR.
Surprenant, D. 1985a. Acute toxicity of sevin technical to sheepshead minnow (Cyprinodon
variegatus). Bionomics Report No. BW-85-4-1773: Bionomics Study No. 565.0185.6109.510.
Unpublished study prepared by Springborn Bionomics, Inc. 14 p.
Surprenant, D. 1985b. The chronic toxicity of carbaryl technical to Daphnia magna under flow
through conditions. Report No. BW-85-7-1813: Study No. 565.0185.6109.130. Unpublished
study prepared by Springborn Bionomics, Inc. 35 p.
Thursby, G.B. and D. Champlin. 1991. Flow-through acute and chronic toxicity of carbaryl to
Mysidopsis bahia. (Memorandum to D.J. Hansen. U.S. EPA, Narragansett, RI. June 13).
Tripathi, G. and S.P. Shukla. 1988. Toxicity bioassay of technical and commercial formulations
of carbaryl to the freshwater catfish, Clarias batrachus. Ecotoxicol. Environ. Saf. 15(3): 277 281.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA 2004. Interim reregi strati on eligibility decision document for carbaryl.
https://www3.epa.gov/pesticides/chem search/reg actions/reregistration/ired PC-056801 22-
Oct.-O4.pclf
U.S. EPA. 2007. Risks of carbaryl use to the federally-listed California red legged frog (Rana
aurora draytonii). Pesticide effects determination. Office of Pesticide Programs. Washington,
D C. 20460. October 19, 2007.
U.S. EPA. 2010. Problem formulation for the environmental fate and ecological risk, endangered
species, and drinking water assessments in support of the registration review of carbaryl. Office
of Pesticide Programs. Washington, D.C. 20460. September 3, 2010.
U.S. EPA. 2012. Aquatic life ambient water quality criteria for carbaryl. Office of Water. EPA-
820-R-12-007. April 2012.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
24
-------
Verep, B.A. 2006. A research on the sensitivity of European chub to some pesticides. Fresenius
Environ. Bull. 15(12A): 1517-1520.
Woodward, D.F., and W.L. Mauck (1980). Toxicity of Five Forest Insecticides to Cutthroat
Trout and Two Species of Aquatic Invertebrates. Bull. Environ. Contam. Toxicol., 25, (6), 846-
854.
Zaga, A., E.E. Little, C.F. Rabeni and M.R. Ellersieck. 1998. Photoenhanced toxicity of a
carbamate insecticide to early life stage anuran amphibians. Environ. Toxicol. Chem. 17(12):
2543-2553.
25
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1.1.2 Comparison of Aquatic Life Toxicity Values for Methomyl: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) are described below. Data for methomyl were gathered by OW in 2015
and combined with data from OPP's registration review document for methomyl (U.S. EPA
2010).
1.1.2.1 Methomyl Acute Toxicity Data
Acute data for methomyl were gathered by OW in 2015 and combined with data from OPP's
registration review document for methomyl (U.S. EPA 2010). (See Table 1.) Methomyl data
include thirty-nine acute effect LCsos representing 14 species in 13 genera that were classified as
"quantitative" data; and two 96-hour LCsos for the species Daphnia magna and Ictalurus
punctatus conducted in acute toxicity tests using a 24% formulation of methomyl that served as
the basis for the invertebrate and fish freshwater acute OPP benchmarks. Additional studies
using 24% and 29% methomyl formulations were included in the OPP document; however, only
the two LCsos noted above that served as the basis of the OPP fish and invertebrate benchmarks
were added to the final dataset. The final acute methomyl dataset consisted of 41 LCsos for 14
species across 13 genera, including six invertebrate species representing six genera. Ranked
invertebrate GMAVs are listed in Table 2.
Table 1. Acute toxicity data of methomyl
to freshwater aquatic organisms.
OW
MDR
Group3
Genus
Species
LC50/
EC50
(Hg/L)
SMAV
(^g/L)
GMAV
(^g/L)
Reference
D
Daphnia
magna
5
11.17
11.17
Mayer and Ellersieck 1985
D
Daphnia
magna
8.8
Mayer and Ellersieck 1986
D
Daphnia
magna
31.7
Goodman 1978
F
Chironomus
plumosus
88
88
88
Mayer and Ellersieck 1986
F
Isogenus
sp
343
343
343
Mayer and Ellersieck 1986
F
Skwala
sp
34
34
34
Johnson and Finley 1980
F
Pteronarcella
badia
69
69
69
Mayer and Ellersieck 1986
E
Gammarus
pseudolimnaeus
920
920
920
Mayer and Ellersieck 1986
B
Pimephales
promelas
2,089
2,419
2,419
Geigeretal. 1988
B
Pimephales
promelas
2,800
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
1,200
896.4
896.4
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
840
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
480
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
600
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
620
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
1,050
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
2,000
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
1,150
Mayer and Ellersieck 1986
26
-------
()\\
MDR
(Iroup1
(ion us
Species
I X 50/
I X 50
(Mli/U
S\1 AY
(MS/'-)
(IMAY
(MB/'-)
Reference
B
Lepomis
macrochirus
860
Mayer and Ellersieck 1986
B
Micropterus
salmoides
1,250
1,250
1,250
Mayer and Ellersieck 1986
A
Oncorhynchus
clarkii
6,800
6,800
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,700
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,400
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
2,000
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,050
3,015
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
860
1,337
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,500
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,100
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,200
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,600
Mayer and Ellersieck 1986
A
Salmo
salar
1,120
Mayer and Ellersieck 1986
A
Salmo
salar
560
Mayer and Ellersieck 1986
A
Salmo
salar
700
Mayer and Ellersieck 1986
A
Salmo
salar
1,220
939.6
939.6
Mayer and Ellersieck 1986
A
Salmo
salar
1,050
Mayer and Ellersieck 1986
A
Salmo
salar
1,000
Mayer and Ellersieck 1986
A
Salmo
salar
1,150
Mayer and Ellersieck 1986
A
Salvelinus
fontinalis
2,200
1,817
1,817
Mayer and Ellersieck 1986
A
Salvelinus
fontinalis
1,500
Mayer and Ellersieck 1986
B
Ictalurus
punctatus
320
412
412
Mayer and Ellersieck 1986
B
Ictalurus
punctatus
530
Mayer and Ellersieck 1986
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
27
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 2.5 |ig/L, which is V2 of the I), magna LC50 of 5.0 |ig/L
from a test conducted with a 24% formulation of methomyl (U.S. EPA 2010).
The OPP fish acute benchmark is 160 |ig/L, which is V2 of the I. punctatus LC50 of 320 |ig/L
from a test conducted with a 24% formulation of methomyl (U.S. EPA 2010).
OW Acute Criterion
There is no acute criterion, or criterion maximum concentration (CMC), for methomyl.
An illustrative example calculated for this analysis, using all available data (Table 2) was
developed.
The FAV calculated following the U.S. EPA (1985) methodology for the 13 genera in the
methomyl dataset was 8.652 |ig/L (Table 3).
Table 2. Methomyl SMAVs and GMAVs (ng/L).
(Ion us
Species
S\1 AY
(IMAY
CMAY kit 11k
Oncorhynchus
clarkii
6,800
3,015
13
Oncorhynchus
mykiss
1,337
Pimephales
promelas
2,419
2,419
12
Salvelinus
fontinalis
1,817
1,817
11
Micropterus
salmoides
1,250
1,250
10
Salmo
salar
939.6
939.6
9
Gammarus
pseudolimnaeus
920
920
8
Lepomis
macrochirus
896.4
896.4
7
Ictalurus
punctatus
411.8
411.8
6
Isogenus
sp
343
343
5
Chironomus
plumosus
88
88
4
Pteronarcella
badia
69
69
3
Skwala
sp
34
34
2
Daphnia
magna
11.17
11.17
1
28
-------
Table 3. Genus-level acute HCos for methomyl calculated following the U.S. EPA (1985)
N
Rank
GMAV
In(GMAV)
n(GMAV)
P=R/(N+1)
sqrt(P)
13
4
88
4.477
20.05
0.2857
0.5345
3
69
4.234
17.93
0.2143
0.4629
2
34
3.526
12.44
0.1429
0.3780
1
11.17
2.413
5.82
0.0714
0.2673
Sum:
14.65
56.2
0.714
1.643
S2 =
64.73
L =
0.359
A =
2.158
hc05 =
8.652
Genus-Level Invertebrate-only HCos
The genus-level invertebrate acute HCos calculated following the U.S. EPA (1985) methodology
for the four most sensitive invertebrate genera (Table 4) in the methomyl dataset was 5.109 |ig/L
(Table 5). If the D. magna OPP benchmark value was excluded from the dataset (i.e., the value
of 5.0 |ig/L from a test using a 24% formulation of methomyl), the GMAV for I). magna would
increase to 16.70 |ig/L, and the genus-level invertebrate acute HCos would increase to 8.310
Hg/L.
Table 4. Methomyl invertebrate SMAVs and GMAVs (jiig/L).
(Ion us
Species
SMAV
(IMAY
CMAY R;t 11k
Gammarus
pseudolimnaeus
920.0
920.0
6
Isogenus
sp.
343.0
343.0
5
Chironomus
plumosus
88.00
88.00
4
Pteronarcella
badia
69.00
69.00
3
Skwala
sp.
34.00
34.00
2
Daphnia
magna
11.17*
11.17
1
* The D. magna SMAV represents two LC50 values (31.7 and 8.8 |ig/L. respectively) classified as quantitative, and
an LC50 of 5.0 |ig/L from a test using a 24% formulation of methomyl that is the basis of the OPP acute
invertebrate benchmark.
29
-------
Table 5. Genus-level invertebrate-only acute HCos for methomyl calculated using the
Guidelines algorithm.
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
6
4
88
4.477
20.05
0.5714
0.7559
3
69
4.234
17.93
0.4286
0.6547
2
34
3.526
12.44
0.2857
0.5345
1
11.17
2.413
5.82
0.1429
0.3780
Sum:
14.65
56.2
1.429
2.323
S2 =
32.36
L =
0.359
A =
1.631
hc05 =
5.109
Note: The most sensitive GMAV for Daphnia includes an LC50 of 5.0 |ig/L conducted in a test
using a 24% methomyl formulation that is the basis for the OPP invertebrate acute benchmark
value.
Table 6. Summary and comparison of acute values for methomyl. Magnitude relative to ALB
is the OPP ALB/OW value, the ratio for the OPP value/OW value for each value comparison. A
ratio <1 indicates the OPP value is lower than the OW value.
Pesticide
Invertebrate
ALB
(lowest LCso/2)
(Year published,
species)
OW ALC (FAV/2)
(Year published, #
of genera,
magnitude relative
to ALB)
OW Genus-level
Invertebrate-only
H Cos/2
(# of genera, magnitude
relative to ALB)
Notes
Methomyl
2.5 ng/L
(2010; Daphnia
magna)
4.326 ng/L
(illustrative example
calculated for this
analysis, 8 genera,
0.58X)
2.55 ng/L
(6 genera, 0.98X)
The FIFRA ALB of 2.5
|ig/L was calculated as
half the LC50 from a
water flea (J), magna)
test conducted with 24%
pure methomyl (Mayer
and Ellersieck 1986).
Figure 1 shows a genus-level sensitivity distribution for the methomyl dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values, the illustrative ALC example, and invertebrate-only
acute HC05/2 are included.
30
-------
10,000 -
1,000
M
">
E
o
• Arthropod
¦ Salmonid Fish
~ Other Fish
FAV/2 = "Criterion Maximum Concentration"
Genus-level Invertebrate
OPP Invert. Benchmark
•- OPP Fish Benchmark
Isogenus •
\
Gammarus
OPP Fish Benchmark = 160 |ig/L
100
• Chironomus
• Pteronarcella
CD
• Skwala
10
• Daphnia
FAV/2 = "Criterion Maximum Concentration" = 4.326 jig/L
Genus-level Invertebrate FIC05/2 = 2.55 ng/L
"OPP Invertebrate Benchmark = 2.5 pg/L
0.0
0.1
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Methomyl genus-level acute SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from an Office of Water data analysis in
2015, supplemented the Office of Pesticide Programs (OPP) registration review document for methomyl (U.S. EPA 2010). The
"Criterion Maximum Concentration" is an illustrative example calculated for these analyses.
31
-------
1.1.2.2 Methomyl Chronic Toxicity Data
Chronic Data Sources
Data for methomyl were gathered by OW in 2015 and combined with data from OPP's
registration review document for methomyl (U.S. EPA 2010). The final chronic methomyl
dataset consisted of three NOECs/LOECS for two species across two genera, of which one was
an invertebrate and one was a vertebrate (Table 7).
Table 7. Chronic toxicity data of methomyl to freshwater aquatic organisms.
OW
MDR
Group8
Genus
Species
NOEC
(^g/L)
LOEC
(^g/L)
Endpoint
Reference
D
Daphnia
magna
>0.4
0.9
Number of
young/adult
MRID 00118512; Muska
and Britelli 1982
D
Daphnia
magna
0.700
10.00
Delayed reproduction
MRID 131254; Britelli and
Muska 1982
B
Pimephales
promelas
57.00
117.0
Early lifestage;
reduced survival
MRID 131255; Driscoll
and Muska 1982
B
Pimephales
promelas
76
142
Life cycle test;
growth
MRID 43072101; Strawn
et al. 1993
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
wannwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark for methomyl is 0.6 |ig/L, which is the MATC for
Daphnia magna, the geometric mean of the NOEC (>0.4 |ig/L) and LOEC (0.9 |ig/L).
The OPP fish chronic benchmark is 57 |ig/L, which is the NOEC for Pimephalespromelas.
GLI Tier II Chronic Value Calculation
Paired acute and chronic toxicity data were available for water flea (Daphnia magna) and
fathead minnow (Pimephales promelas) allowing for the calculation of two Acute-to-Chronic
Ratios (ACR). The water flea (.Daphnia magna) chronic test reported NOAEC and LOAEC
values of 0.700 and 10.00 |ig/L, respectively based on measurements of delayed reproduction
(Britelli and Muska 1982). The fathead minnow (.Pimephales promelas) chronic test reported
NOAEC and LOAEC values of 57.00 and 117.0 |ig/L based on reduced survival (Driscoll and
Muska 1982). Because three experimentally determined ACRs were not available for methomyl,
a Tier I chronic value could not be derived. However, the GLI Tier II approach was used to
calculate the chronic value. Under the GLI Tier II approach, the default value of 18 was used in
place of the third, missing ACR.
32
-------
The paired acute and chronic tests were conducted in different laboratories using water of
different physical characteristics; therefore, OPP's ACR approach was used in the calculations,
which involves the use of the NOAEC values. The chronic Secondary ACR and Secondary
Chronic Value (SCV) calculations are displayed below:
SACR = Geometric Mean of the ACRs
SACR = V12.57 * 36.65 * 18 = 20.24
FAV
SCV =
SACR
9.541
SCV = = 0.471 ug a. i./L
20.24 ^ '
Table 8. Summary and comparison of chronic values for methomyl. Magnitude relative to
ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for each value
comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II value
(# of ACRs filled,
magnitude relative
to ALB)
OW Invertebrate-only
HCos
(# of ACRs filled,
magnitude relative to
ALB)
Notes
Methomyl
0.6 ng/L
(2020, Daphnia
magna)
0.47 (ig/L
(GLI Tier II; 2 ACRs,
1.3X)
NA
One default ACR
of 18 used to derive
GLI Tier II value.
1.1.2.3 Methomyl References
ECOTOX 12859. Geiger, D.L., Call, D.J., and Brooke L.T. 1988. Acute Toxicities of Organic
Chemicals to Fathead Minnows (Pimephales promelas) Volume IV. Ctr. for Lake Superior
Environ. Stud., Volume 4, Univ. of Wisconsin-Superior, Superior, WI :355.
ECOTOX 6797. Mayer, F.L.J., and Ellersieck, M.R.. 1986. Manual of Acute Toxicity:
Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals. Resour.
Publ. No. 160, U.S. Department of Interior, Fish and Wildlife Services, Washington, DC 505 p.
http://www.cerc.usgs.gov/pubs/center/pdfDocs/90506-intro.pdf
MRID 00118512. Muska, C.; Brittelli, M. (1982) Chronic Toxicity of Methomyl to Daphnia
magna: Haskell Laboratory Report No. 46-82. (Unpublished study received Dec 3, 1982 under
352-342; submitted by E.I. du Pont de Nemours & Co., Inc., Wilmington, DE; CDL: 071268-B)
MRID 131254. Britelli, M.; Muska, C. 1982. Chronic Toxicity of Methomyl to Daphnia magna:
Haskell Laboratory Report No. 4682; MR No. 0581930. (Unpublished study received Oct 3,
1983 under 352366; submitted by E.I. du Pont de Nemours & Co., Inc., Wilmington, DE;
CDL:251426B)
MRID 131255. Driscoll, R.; Muska, C. 1982. Early Life Stage Toxicity of Methomyl to Fathead
Minnow: Haskell Laboratory Report No. 52882; MR No. 0581930. (Unpublished study received
33
-------
Oct 3, 1983 under 352366; submitted by E.I. du Pont de Nemours & Co., Inc., Wilmington, DE;
CDL:251426C)
MRID 19977. Goodman, N.C. 1978. 48HourLC50A2Ito -Daphnia magna-: Haskell Laboratory
Report No. 16578. (Unpublished study received May 22, 1978 under 352342; submitted by E.I.
du Pont de Nemours & Co., Wilmington, Del.; CDL:233993B).
MRID 4009602. Johnson, W.; Finley, M. 1980. Handbook of Acute Toxicity of Chemicals to
Fish and Aquatic Invertebrates: Resource Publication 137. US Fish and Wildlife Service,
Washington, D.C. 106 p.
MRID 43072101. Strawn, T.; Rhodes, J.; Leak, T. 1993. Full Life Cycle Toxicity of
DPXX1179394 (Methomyl) to the Fathead Minnow (Pimephales promelas) Under Flow
Through Conditions: Final Report: Lab Project Number: 39293: HLO 4793. Unpublished study
prepared by ABC Laboratories, Inc. 3582 p.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2010. Problem formulation for the environmental fate, ecological risk, endangered
species, and drinking water exposure assessments in support of the registration review of
methomyl. Office of Pesticide Programs. Washington, D.C. July 16, 2010.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
34
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1.1.3 Comparison of Aquatic Life Toxicity Values for Propoxur: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA) (U.S.EPA 2024) were gathered from the OPP registration review
document for propoxur (U.S. EPA 2009) and an EPA ECOTOX Knowledgebase search
conducted in 2013. There is no chronic OPP ALB for propoxur, so no chronic value analyses
were conducted for this pesticide.
1.1.3.1 Propoxur Acute Toxicity Data
Acute data were gathered from the OPP registration review document for propoxur (U.S. EPA
2009) and an ECOTOX search conducted in 2013 (see Table 1). The propoxur acute dataset
consisted of 20 acceptable LCsos for a total of 12 species across 11 genera, of which six were
invertebrate species representing five genera. Ranked invertebrate GMAVs are listed in Table 2.
Table 1. Acute toxicity data of propoxur to freshwater aquatic organisms.
()\\
l .( 50/
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
MDR
(Iroup1
(ionus
Species
IX 50
(M8/U
Reference
G
Lumbriculus
variegatus
146,000
146,000
146,000
Brooke 1991
D
Daphnia
magna
3,990
Lejczak 1977
D
Daphnia
magna
27.2
107.0
107.0
Brooke 1991
D
Daphnia
magna
110
Lakotaetal. 1981
D
Daphnia
magna
11
MRID: 00149172; Lamb 1981
F
Aedes
aegypti
150
150
150
Lakotaetal. 1981
F
Pteronarcys
californica
13
15.3
15.3
Sanders and Cope 1968
F
Pteronarcys
californica
18
Mayer and Ellersieck 1986
E
Gammarus
fasciatus
50
50
41.2
Sanders 1972
E
Gammarus
lacustris
34
34
Mayer and Ellersieck 1986
B
Cyprinus
carpio
7,340
7,340
7,340
Lakotaetal. 1981
B
Pimephales
promelas
25,000
14,832
14,832
Mayer and Ellersieck 1986
B
Pimephales
promelas
8,800
Geigeretal. 1988/Call et al. 1989
B
Poecilia
reticulata
2,980
2,277
2,277
Lejczak 1977
B
Poecilia
reticulata
1,740
Lakotaetal. 1981
B
Lepomis
macrochirus
4,800
5,455
5,455
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
6,200
Lamb 1981
A
Oncorhynchus
mykiss
8,200
5,508
5,508
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
3,700
Lamb 1981
A
Salmo
trutta
2,110
2,110
2,110
Lakotaetal. 1981
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
35
-------
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark for propoxur is 5.5 |ig/L, which is V2 of the D. magna
LC50 of 11 |ig/L cited in Lamb (1981).
The OPP fish acute benchmark is 1,850 ug/L, which is V2 of the 0. mykiss LC50 of 3,700 ug/L
cited in Lamb (1981).
OW Acute Criterion
There is no acute criterion, or criterion maximum concentration (CMC), for propoxur.
An illustrative example calculated for this analysis, using all available data (Table 2) was
conducted.
The HCos calculated following the U.S. EPA (1985) methodology for the eleven genera in the
propoxur dataset was 9.151 |ig/L (Table 3)
Table 2. Propoxur SMAVs and GMAVs
(Ug/L).
(Ion us
Species
S\1 AY
(IMAY
(J.MAY Ritnk
Lumbriculus
variegatus
146,000
146,000
11
Pimephales
promelas
14,832
14,832
10
Cyprinus
carpio
7,340
7,340
9
Oncorhynchus
mykiss
5,508
5,508
8
Lepomis
macrochirus
5,455
5,455
7
Poecilia
reticulata
2,277
2,277
6
Salmo
trutta
2,110
2,110
5
Aedes
aegypti
150.0
150.0
4
Daphnia
magna
107.0
107.0
3
Gammarus
fasciatus
50.00
41.23
2
Gammarus
lacustris
34.00
Pteronarcys
californica
15.30
15.30
1
36
-------
Table 3. Genus-level acute FAV for propoxur calculated following the U.S. EPA (1985)
methodology.
N
11
K;lllk
4
cmay
150.0
lii((,M \V)
5.011
lii{<.M Wr
25.11
r kiN ii
0.3333
>¦ <|i li 1')
0.5774
3
107.0
4.673
21.84
0.2500
0.5000
2
41.23
3,719
13.83
0.1667
0.4082
1
15.3
2,728
7.441
0.0833
0.2887
Sinn:
16.13
68.22
0.833
1.774
s2-
68.37
L =
0.3649
A =
2.214
FAV =
9.151
FAV/2 =
4.6
Genus-Level Invertebrate-only acute HCos
The genus level invertebrate-only acute HCos calculated following the U.S. EPA (1985)
methodology for the five invertebrate genera (Table 3) in the propoxur dataset was 5.324 |ig/L
(Table 4).
Table 3. Propoxur invertebrate SMAVs and GMAVs (^ig/L).
(Ion us
Species
S\1 AY
(IMAY
(J.MAY k:iiik
Lumbriculus
variegatus
146,000
146,000
5
Aedes
aegypti
150.0
150.0
4
Daphnia
magna
107.0
107.0
3
Gammarus
fasciatus
50.00
41.23
2
Gammarus
lacustris
34.00
Pteronarcys
californica
15.30
15.30
1
37
-------
Table 4. Genus-level invertebrate-only acute HCos for propoxur calculated following the
N
Rank
(.MAY
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
5
4
150.0
5.011
25.11
0.6667
0.8165
3
107.0
4.673
21.84
0.5000
0.7071
2
41.23
3.719
13.83
0.3333
0.5774
1
15.3
2.728
7.441
0.1667
0.4082
Sum:
16.13
68.22
1.667
2.509
S2 =
34.19
L =
0.3649
A =
1.672
hc05 =
5.324
Table 5. Summary and comparison of acute values for propoxur.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate ALB
(lowest LCso/2) (Year
published, species)
ALC (FAV/2)
(Year published, # of genera,
magnitude relative to ALB)
OW Genus-level
Invertebrate-only HCos/2
(# of genera, magnitude
relative to ALB)
Propoxur
5.5 ng/L
(2009; D. magna)
4.6 ng/L
(illustrative example calculated for
this analysis, 11 genera, 1.2X)
2.66 ng/L
(5 genera, 2. IX)
Figure 1 shows a genus-level sensitivity distribution for the propoxur dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. The
OPP benchmark acute values, illustrative ALC example, and invertebrate-only acute HCos/2 are
included.
38
-------
1,000,000 -
100,000
10,000
CUD
3.
X
o
Q.
O
1,000 -
100
10
• Arthropod
¦ Salmonid Fish
~ Other Fish
a Other Invertebrate
— • ¦ Genus-level Invertebrate
OPP Invert. Benchmark
• - OPP Fish Benchmark
FAV/2 = "Criterion Maximum Concentration"
Daphnia
i Aedes
Gammarus
Pteronarcys
~
~
OPP Fish Benchmark = 1,850 pg/L
OPP Invertebrate Benchmark = 5.5 [ig/L
FAV/2 = "Criterion Maximum Concentration" = 4.6 pg/L
Genus-level Invertebrate FIC05/2 = 2.7 pg/L
0.0 0.1 0.2 0.3 0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Propoxur genus-level SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from the Office of Pesticide Program's
registration review document for propoxur (U.S. EPA 2009) and an ECOTOX search conducted by Office of Water in 2013.
Propoxur does not have a recommended 304(a) aquatic life criteria. The "Criterion Maximum Concentration" is an illustrative
example calculated for these analyses.
39
-------
1.1.3.2 Propoxur Chronic Toxicity Data
There is no chronic OPP Aquatic Life Benchmark for propoxur, so no chronic analysis was
conducted for this pesticide.
1.1.3.3 Propoxur References
Brooke, L.T. 1991. Results of Freshwater Exposures with the Chemicals Atrazine, Biphenyl,
Butachlor, Carbaryl, Carbazole, Dibenzofuran, 3,3'-Dichlorobenzidine, Dichlorvos, 1,2-
Epoxyethylbenzene (Styrene Oxide), Isophorone, Isopropalin, Ox. Center for Lake Superior
Environmental Studies, University of Wisconsin, Superior, WI, 110 p. ECOREF#: 17138.
Call, D.J., S.H. Poirier, C.A. Lindberg, S.L. Halting, T.P. Markee, L.T. Brooke, N. Zarvan, and
C.E. Northcott. 1989. Toxicity of Selected Uncoupling and Acetylcholinesterase-Inhibiting
Pesticides to the Fathead Minnow (Pimephales promelas). In: D.L. Weigmann (Ed.), Pesticides
in Terrestrial and Aquatic Environments, Proc. Natl. Res. Conf., Virginia Polytechnic Inst, and
State Univ., Blacksburg, VA, 317-336. ECOREF#: 14097.
Geiger, D.L., D.J. Call, and L.T. Brooke. 1988. Acute Toxicities of Organic Chemicals to
Fathead Minnows (Pimephales promelas) Volume IV. Center for Lake Superior Environmental
Studies, University of Wisconsin, Superior, WI, 4, 355 p. ECOREF#: 12859.
Lakota, S., A. Raszka, and I. Kupczak. 1981. Toxic Effect of Cartap, Carbaryl, and Propoxur on
Some Aquatic Organisms. Acta Hydrobiol., 23, (2), 183-190. ECOREF#: 4888.
Lamb, D. 1981. Acute toxicity of technical propoxur (Baygon) to Daphnia magna: Study No.
81-067-01. Unpublished study prepared by Mobay Chemical Corp. 9p.
Lejczak, B. 1977. Effect of Insecticides: Chlorphenvinphos, Carbaryl and Propoxur on Aquatic
Organisms. Pol. Arch. Hydrobiol., 24, (4), 583-591. ECOREF#: 7558.
Mayer, F.L., Jr., and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data
Base for 410 Chemicals and 66 Species of Freshwater Animals. USDI Fish and Wildlife Service,
Publication No. 160, Washington, DC, 505 p. ECOREF#: 6797.
Sanders, H.O. 1972. Toxicity of Some Insecticides to Four Species of Malacostracan
Crustaceans. Tech. Pap. Bur. Sport Fish. Wildl., 66, 19 p. ECOREF#: 887.
Sanders, H.O., and O.B. Cope. 1968. The Relative Toxicities of Several Pesticides to Naiads of
Three Species of Stoneflies. Limnol. Oceanogr., 13, (1), 112-117.
doi:10.4319/lo,1968.13.1.0112. ECOREF#: 889.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2009. Registration review: preliminary problem formulation for ecological risk,
environmental fate, endangered species, and drinking water assessments for propoxur. Office of
Pesticide Programs. Washington, D.C. October 16, 2009.
40
-------
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
41
-------
1.1.4 Comparison of Aquatic Life Toxicity Values for Malathion: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S.EPA 2024) for malathion were obtained from the 1986 criteria which serves as the
base dataset, supplemented with an update to this data from EPA ECOTOX Knowledgebase in
2010, and with additional data from the U.S. EPA (2010) OPP pesticide effects determination
document that served as the basis for the OPP benchmark concentrations.
1.1.4.1 Malathion Acute Toxicity Data
Acceptable acute data for malathion were obtained from the 1986 criteria which serves as the
base dataset, supplemented with an update to this data from ECOTOX in 2010, and with
additional LCsos reported in Table 4-8 of U.S. EPA (2010), the OPP pesticide effects
determination document that served as the basis for the OPP benchmark concentrations. (See
Table 1.) The final dataset consists of 69 SMAVs and 54 GMAVs, including 36 invertebrate
species representing 29 invertebrate genera. Ranked SMAVs and GMAVs for all invertebrates
included in this analysis are listed in Table 2, below.
Table 1. Acute toxicity data of malathion to freshwater aquatic organisms.
ow
LC50/
SMAV
(^g/L)
GMAV
(^g/L)
MDR
Group8
Genus
Species
EC50
(Hg/L)
Reference
A
Oncorhynchus
clarkii
150
Post and Schroeder 1971
A
Oncorhynchus
clarkii
201
Post and Schroeder 1971
A
Oncorhynchus
clarkii
280
Johnson 1980b; Mayer and
Ellersieck 1986
A
Oncorhynchus
clarkii
174
215.5
Mayer and Ellersieck 1986
A
Oncorhynchus
clarkii
237
Mayer and Ellersieck 1986
A
Oncorhynchus
clarkii
270
Mayer and Ellersieck 1986
A
Oncorhynchus
clarkii
230
Mayer and Ellersieck 1986
A
Oncorhynchus
kisutch
101
Macek and McAllister 1970
A
Oncorhynchus
kisutch
265
Post and Schroeder 1971
A
Oncorhynchus
kisutch
170
168.5
149.1
Johnson 1980b; Mayer and
Ellersieck 1986
A
Oncorhynchus
kisutch
177
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
77
Cope 1965
A
Oncorhynchus
mykiss
68
Cope 1965
A
Oncorhynchus
mykiss
110
Cope 1965
A
Oncorhynchus
mykiss
170
Macek and McAllister 1970
A
Oncorhynchus
mykiss
122
91.2
Post and Schroeder 1971
A
Oncorhynchus
mykiss
93.5
Schoettger 1970
A
Oncorhynchus
mykiss
200
Johnson 1980b; Mayer and
Ellersieck 1986
A
Oncorhynchus
mykiss
94
Mayer and Ellersieck 1986
42
-------
()\\
MIJR
(iioup1
(ionus
Species
I X 50/
I X 50
(M8/U
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
Reference
A
Oncorhynchus
mykiss
4.1
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
138
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
100
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
66
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
80
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
160
McKimetal. 1987
A
Oncorhynchus
mykiss
250
Li and Fan 1996
A
Salmo
trutta
200
142.1
142.1
Macek and McAllister 1970
A
Salmo
trutta
101
Johnson 1980b; Mayer and
Ellersieck 1986
A
Salvelinus
fontinalis
130
124.9
113.9
Post and Schroeder 1971
A
Salvelinus
fontinalis
120
Post and Schroeder 1971
A
Salvelinus
namaycush
76
103.9
Johnson 1980b; Mayer and
Ellersieck 1986
A
Salvelinus
namaycush
142
Mayer and Ellersieck 1986
B
Perca
flavescens
263
263.0
263.0
Macek and McAllister 1970;
Johnson 1980b; Mayer and
Ellersieck 1986
B
Sander
vitreus
64
64.0
64.0
Johnson 1980b; Mayer and
Ellersieck 1986
B
Oreochromis
mossambica
2,000
2,000
1,181
Mayer and Ellersieck 1986
B
Oreochromis
niloticus
140
140.0
Liongetal. 1988
B
Oreochromis
niloticus x
mossambica
5,880
5,880
Sulaiman et al. 1989
B
Umbra
pygmaea
240
240.0
240.0
Bender and Westman 1976
B
Carassius
auratus
2,610
2,867
2,867
Birge et al. 1979
B
Carassius
auratus
3,150
Birge et al. 1979
B
Cyprinus
carpio
6,590
6,590
6,590
Macek and McAllister 1970;
Johnson 1980b; Mayer and
Ellersieck 1986
B
Danio
rerio
760.2
893.4
893.4
Ton et al. 2006
B
Danio
rerio
1,050
Kumar and Ansari 1984
B
Gila
elegans
15,300
15,300
15,300
Beyers etal. 1994
B
Pimephales
promelas
14,100
12,225
12,225
Geigeretal. 1988
B
Pimephales
promelas
10,600
Geigeretal. 1988
B
Ptychocheilus
lucius
9,140
9,140
9,140
Beyers etal. 1994
B
Ameiurus
melas
12,900
12,285
12,285
Macek and McAllister 1970;
Johnson 1980b; Mayer and
Ellersieck 1986
B
Ameiurus
melas
11,700
Mayer and Ellersieck 1986
B
Ictalurus
punctatus
8,970
8,268
8,268
Macek and McAllister 1970;
Johnson 1980b; Mayer and
Ellersieck 1986
B
Ictalurus
punctatus
7,620
Mayer and Ellersieck 1986
B
Jordanella
floridae
349
349.0
349.0
Hermanutz 1978
43
-------
()\\
MIJR
(iioup1
(ionus
Species
I X 50/
I X 50
(M8/U
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
Reference
B
Gambusia
affinis
700
700.0
700.0
Li and Fan 1996
B
Poecilia
reticulata
840
1,614
1,614
Pickering et al. 1962
B
Poecilia
reticulata
3,100
Maas 1982
B
Morone
saxatilis
24.5
39.9
39.9
Palawski et al. 1985
B
Morone
saxatilis
65
Palawski et al. 1985
B
Lepomis
cyanellus
175
163.2
103.8
Johnson 1980b; Mayer and
Ellersieck 1986
B
Lepomis
cyanellus
146
Mayer and Ellersieck 1986
B
Lepomis
cyanellus
170
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
90
66.7
Pickering et al. 1962
B
Lepomis
macrochirus
120
Maceketal. 1969
B
Lepomis
macrochirus
55
Maceketal. 1969
B
Lepomis
macrochirus
46
Maceketal. 1969
B
Lepomis
macrochirus
131
Eaton 1970
B
Lepomis
macrochirus
89
Eaton 1970
B
Lepomis
macrochirus
103
Macek and McAllister 1970;
Johnson 1980b; Mayer and
Ellersieck 1986
B
Lepomis
macrochirus
20
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
40
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
55
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
84
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
87
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
30
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
110
Mayer and Ellersieck 1986
B
Lepomis
microlophus
170
102.7
Macek and McAllister 1970
B
Lepomis
microlophus
62
Johnson 1980b; Mayer and
Ellersieck 1986
B
Micropterus
salmoides
50
152.7
152.7
Pickering et al. 1962
B
Micropterus
salmoides
285
Macek and McAllister 1970;
Johnson 1980b; Mayer and
Ellersieck 1986
B
Micropterus
salmoides
250
Mayer and Ellersieck 1986
C
Bufo
woodhousei
fowleri
420
420.0
420.0
Sanders 1970; Mayer and
Ellersieck 1986
C
Pseudacris
triseriata
200
200.0
200.0
Sanders 1970; Mayer and
Ellersieck 1986
C
Rana
boylii
2,137
2,137
2,137
Sparling and Fellers 2007
C
Xenopus
laevis
10,900
10,900
10,900
Snawder and Chambers 1989
D
Ceriodaphnia
dubia
0.5
0.5
0.5
Foster etal. 1998
D
Daphnia
magna
1.0
2.4
2.1
Johnson 1980b
D
Daphnia
magna
1.8
Kikuchi et al. 2000
D
Daphnia
magna
1.6
Maas 1982
44
-------
()\\
MIJR
(iioup1
(ionus
Species
I X 50/
I X 50
(M8/U
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
Reference
D
Daphnia
magna
33
Hermens et al. 1984
D
Daphnia
magna
0.90
Ren et al. 2007
D
Daphnia
magna
2.2
MRID 41029701; Burgess
1989
D
Daphnia
pulex
2
1.9
Cope 1966
D
Daphnia
pulex
1.8
Sanders and Cope 1966;
Johnson 1980b
D
Simocephalus
serralatus
3
2.5
2.7
Cope 1966
D
Simocephalus
serralatus
3.5
Sanders and Cope 1966;
Johnson 1980b
D
Simocephalus
serralatus
6.2
Sanders and Cope 1966
D
Simocephalus
serralatus
0.59
MRID 40098001; Mayer and
Ellersick 1986
D
Simocephalus
vetulus
2.9
2.9
Olvera-Hernandez et al. 2004
D
Cypridopsis
vidua
47
47.0
47.0
MRID 40098001; Mayer and
Ellersick 1986
E
Asellus
brevicaudus
3,000
3,000
3,000
Sanders 1972; Johnson 1980b;
Mayer and Ellersieck 1986
E
Gammarus
fasciatus
0.76
0.7
1.0
Sanders 1972; Johnson 1980b;
Mayer and Ellersieck 1986
E
Gammarus
fasciatus
0.90
Sanders 1972; Mayer and
Ellersieck 1986
E
Gammaras
fasciatus
0.50
Sanders 1972; Mayer and
Ellersieck 1986
E
Gammaras
lacustris
1.62
1.4
Gaufinetal. 1965
E
Gammaras
lacustris
1.0
Sanders 1969
E
Gammaras
lacustris
1.8
MRID 05009242; Sanders
1969
E
Orconectes
nais
180
180.0
180.0
Sanders 1972; Johnson 1980b;
Mayer and Ellersieck 1986
E
Palaemonetes
kadiakensis
12
32.6
24.8
Sanders 1972; Mayer and
Ellersieck 1986
E
Palaemonetes
kadiakensis
90
Sanders 1972; Johnson 1980b;
Mayer and Ellersieck 1986
E
Palaemonetes
kadiakensis
32
Mayer and Ellersieck 1986
E
Palaemonetes
pugio
8.94
18.9
Key and Fulton 2006
E
Palaemonetes
pugio
39.92
Key and Fulton 2006
E
Procambaras
clarkii
49,170
49,170
49,170
Hoick and Meek 1987
F
Dranella
grandis
100
100.0
100.0
Gaufinetal. 1965
F
Lestes
congener
10
10.0
10.0
Johnson 1980b; Mayer and
Ellersieck 1986
F
Claassenia
sabulosa
2.8
2.8
2.8
Sanders and Cope 1968;
Johnson 1980b; Mayer and
Ellersieck 1986
F
Isoperla
sp.
0.69
0.7
0.7
Johnson 1980b; Mayer and
Ellersieck 1986
45
-------
()\\
MDR
(iioup1
(ionus
Species
I X 50/
I X 50
(M8/U
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
Reference
F
Pteronarcella
badia
1.1
3.9
3.9
Sanders and Cope 1968;
Johnson 1980b; Mayer and
Ellersieck 1986
F
Pteronarcella
badia
6.2
Mayer and Ellersieck 1986
F
Pteronarcella
badia
8.8
Mayer and Ellersieck 1986
F
Pteronarcys
californicus
10
10.0
10.0
Sanders and Cope 1968;
Johnson 1980b; Mayer and
Ellersieck 1986
F
Peltodytes
sp.
1,000
1,000
1,000
Federle and Collins 1976
F
Arctopsyche
grandis
32
32.0
32.0
Gaufinetal. 1965
F
Hydropsyche
californica
22.5
22.5
10.6
Gaufinetal. 1965
F
Hydropsyche
sp.
5
5
MRID 40098001; Mayer and
Ellersick 1986
F
Limnephilus
sp.
1.3
1.3
1.3
Johnson 1980b; Mayer and
Ellersieck 1986
F
Atherix
sp.
385
385.0
385.0
Johnson 1980b
F
Chironomus
plumosus
8.4
8.4
72.2
Vedamanikam 2009
F
Chironomus
dilutus
620
620.0
Hansen and Kawatski 1976
F
Notonecta
undulata
80
80.0
80.0
Federle and Collins 1976
H
Limnodrilus
sp.
16,700
16,700
16,700
Whitten and Goodnight 1966
H
Lumbriculus
variegatus
20,500
20,500
20,500
Bailey and Liu 1980
H
Tubifex
sp.
16,700
16,700
16,700
Whitten and Goodnight 1966
G
Elliptio
icterina
32,000
32,000
32,000
Keller and Ruessler 1997
G
Lampsilis
straminea
claibornen
24,000
24,000
25,923
Keller and Ruessler 1997
G
Lampsilis
subangulata
28,000
28,000
Keller and Ruessler 1997
G
Utterbackia
imbecillis
215,000
108,654
108,654
Keller and Ruessler 1997
G
Utterbackia
imbecillis
219,000
Keller and Ruessler 1997
G
Utterbackia
imbecillis
40,000
Keller and Ruessler 1997
G
Utterbackia
imbecillis
74,000
Keller and Ruessler 1997
G
Villosa
lienosa
109,000
96,382
124,133
Keller and Ruessler 1997
G
Villosa
lienosa
111,000
Keller and Ruessler 1997
G
Villosa
lienosa
74,000
Keller and Ruessler 1997
G
Villosa
villosa
142,000
159,875
Keller and Ruessler 1997
G
Villosa
villosa
180,000
Keller and Ruessler 1997
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
46
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark for malathion is 0.049 |ig/L, which is one half of the
LC50 of 0.098 |ig/L for D. magna.
The OPP fish acute benchmark for malathion is 2.05 |ig/L, which is one half of the LC50 of 4.1
|ig/L for rainbow trout (Oncorhynchus mykiss), the lowest LC50 of any fish species.
OW Acute Criterion
The 1986 acute criterion, or CMC, for malathion of 0.1 |ig/L was not calculated using calculated
the U.S. EPA (1985) methodology, as it pre-dates the Guidelines. Rather, it was calculated by
dividing the effect acute LC50 for G. lacustrus, G. fasciatis, and D. magna, which were all
approximately 1 |ig/L, by an application factor of ten (U.S. EPA 1976 - EPA Red Book).
Genus-Level Invertebrate-only Acute HC05
The acute HC05 calculated from invertebrate-only GMAVs shown in Table 2 was calculated
following the U.S. EPA (1985) methodology is 0.8360 |ig/L (Table 3).
Table 2. Malal
thion Invertebrate SMAVs and GMAVs (jug/L).
Genus
Species
S.MAN'
GMAV
GMAV Rank
Villosa
lienosa
96,382
124,133
29
Villosa
villosa
108,653
Utterbackia
imbecillis
108,653
108,653
28
Procambarus
clarkii
49,170
49,170
27
Elliptic)
icterina
32,000
32,000
26
Lampsilis
straminea claibornen
24,000
25,923
25
Lampsilis
subangulata
28,000
Lumbriculus
variegatus
20,500
20,500
24
Limnodrilus
sp.
16,700
16,700
23
Tubifex
sp.
16,700
16,700
22
Asellus
brevicaudus
3,000
3,000
21
Peltodytes
sp.
1,000
1,000
20
Atherix
sp.
385.0
385.0
19
Orconectes
nais
180.0
180.0
18
Drunella
grandis
100.0
100.0
17
Notonecta
undulata
80.00
80.00
16
Chironomus
plumosus
8.400
72.17
15
Chironomus
dilutus
620.0
Cypridopsis
vidua
47.00
47.00
14
Arctopsyche
grandis
32.00
32.00
13
Palaemonetes
pugio
18.89
24.81
12
Palaemonetes
kadiakensis
32.57
Hydropsyche
californica
22.50
22.50
11
Lestes
congener
10.00
10.00
10
Pteronarcys
californicus
10.00
10.00
9
Pteronarcella
badia
3.915
3.915
8
Claassenia
sabulosa
2.800
2.800
7
Simocephalus
vetulus
2.900
2.687
6
Simocephalus
serrulatus
2.489
47
-------
Genus
Species
SMAV
GMAV
GMAV Rank
Daphnia
magna
2.394
2.131
5
Daphnia
pulex
1.897
Linmephilus
sp.
1.300
1.300
4
Ceriodaphnia
dubia
1.294
1.294
3
Gammarus
lacustris
1.429
0.9995
2
Gammarus
fasciatus
0.6993
Isoperla
sp.
0.6900
0.6900
1
Table 3. Genus-level invertebrate-only acute HCos for malathion calculated following the
U.S. EPA
1985) met
hodolog
y-
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
29
4
1.3
0.262
0.07
0.1333
0.3651
3
1.294
0.258
0.07
0.1000
0.3162
2
0.9995
-0.001
0.00
0.0667
0.2582
1
0.69
-0.371
0.138
0.0333
0.1826
Sum:
0.15
0.27
0.3333
1.1221
S2 =
14.44
L =
-1.029
A =
-0.179
HCos =
0.8360
Table 4. Summary and comparison of acute values for malathion by approach.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value.
Pesticide
OPP Invertebrate ALB
(lowest LCso/2) (Year
published, species)
OW ALC (FAV/2) (Year
published, # of genera,
magnitude relative to ALB)
OW Genus-level
Invertebrate-only HCos/2
(# of genera, magnitude
relative to ALB)
Malathion
0.049 (ig/L
(2016; C. dubia)
0.1 ng/L
(1986, "Gold Book", 0.49X)
0.418 (ig/L
(29 genera, 0.12X)
Figure 1 shows a genus-level sensitivity distribution for the malathion dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the CMC, invertebrate acute HCos/2, and OPP acute benchmark values are also
included.
48
-------
1,000,000.00
100,000.00
10,000.00
^ 1,000.00
tLfl
3
c
o 100.00
TO
10.00
1.00
0.10 -L-
0.01
•
Arthropod
o
Other Invertebrate
A
Mollusk
¦
Salmonid Fish
~
Other Fish
~
Amphibian
CMC
Genus-level Invertebrate
OPP Invert. Benchmark
OPP Fish Benchmark
Villosa v
X
Utterbackia A A
Lumbriculus ¦
Limnodrilus
Tubifex
Lampsilis
~
~ • Asellus
Chironomus
Drunella
Arctopsyche
\
Orconectes
~
~ •
~ ~
~
~
Peltodytes
Atherix
~
n i • K ^Notonecta
Palaemonetes • x\
Cypridopsis
Pteronarcys# # #H d he
Simocephalus 7 r 7
Daphnia Lestes
^ . ... Claassenia
• Limnephilus
**- CeriodaDhnia
Genus-level Invertebrate FIC05/2 = 0.4180 ng/L
N Gammarus
Isoperla
FAV/2 = Criterion Maximum Concentration (CMC) = 0.1 |ig/L
^—. OPP Invertebrate Benchmark = 0.049 ng/L
o.o
o.i
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Malathion acute genus-level SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from the malathion ALC (U.S. EPA
1986), the Office of Pesticide Program's registration review document for malathion (U.S. EPA 2010), and an ECOTOX search
conducted by Office of Water in 2010.
49
-------
1.1.4.2 Malathion Chronic Toxicity Data
For chemicals lacking sufficient chronic data to satisfy the minimum taxonomic data
requirements, such as malathion, the EPA Office of Water (OW) calculates the final chronic
value (FCV) as the final acute value (FAV) divided by the final acute-to chronic ratio (FACR).
The Office of Pesticide Programs (OPP) will also apply ACRs to acute data for sensitive
taxonomic groups to calculate chronic benchmarks when chronic test data are not available.
Calculations of ACRs following OPP and OW methodologies were conducted, and the effects of
these ACRs on the resulting OPP and OW chronic values were compared.
Chronic Data Sources
The data sources for this analysis were a 2010 ECOTOX search for malathion and the OPP-
authored malathion effects determination reports for delta smelt and California tiger salamander
(U.S. EPA 2010) and California red legged frog (U.S. EPA 2007). Many values were reported
across all three data sources.
ACR Calculations
ACR calculations following OW and OPP methodologies are described below. All available
chronic malathion data are shown in Table 5. All available acute data for species that also have
chronic data are shown in Table 6. Table 7 lists all ACRs by species and calculation method.
Invertebrate ACRs
Daphnia magna
An ACR for D. magna could not be calculated following the Guidelines requirements, as there
were no acute and chronic tests for this species conducted in the same study or laboratory
(Stephan et al. 1985). However, invertebrates are the most sensitive taxonomic group to
malathion, and D. magna is the only invertebrate species with chronic malathion data. In
addition, the Guidelines requires ACR from at least three families; including at least one fish,
one invertebrate, and one acutely sensitive species. For these reasons, a D. magna ACR was
calculated for this analysis.
The "qualitative" OW D. magna ACR is 5.942, calculated as the geometric mean of the two
acute values identified as ECsos (Johnson 1980b, Kikuchi et al. 2000) divided by the geometric
mean of the two chronic tests with MATCs (Biesinger 1973, Blakemore and Burgess 1990). The
acceptable registrant submitted acute study by Burgess (1989) was not included in this
calculation because it was a formulation (57% active ingredient), and below the 80% purity
threshold recommended in the Guidelines (U.S. EPA 1985).
The ACR calculated following the OPP approach is 13.22, calculated as the geometric mean of
all 48-hour acute values divided by the geometric mean of the NOECs from all chronic studies.
The OPP ACR guidance offers flexibility when multiple acceptable acute and chronic values are
available for the same species (U.S. EPA 2005).
50
-------
Vertebrate (Fish) ACRs
Oncorhynchus mykiss
An ACR for this species could not be calculated following the OW approach. Cohle (1989)
reported test results following a 97-day ELS test in an unpublished report, but there are no acute
studies conducted in the same laboratory.
Following the rationale used for D. magna, the OPP ACR for 0. mykiss is 4.074, calculated as
the geometric mean of all acute tests listed in Table 2 (all of which were 96 hours), divided by
the NOEC reported by Cohle (1989).
Gila elegans
An ACR for this species could not be calculated following the OW approach. Beyers et al.
(1994) performed an early life stage (ELS) chronic test and a static-renewal acute test. Although
the acute and chronic tests were performed in the same laboratory, the Guidelines (U.S. EPA
1985) specifies that acute test data should also be from a flow-through study (except for
Daphnids, where static acute tests are acceptable). The ACR following the OPP approach is
15.46, calculated as the acute value of 15,300 ng/L from Beyers et al. (1994) divided by the
NOEC of 990 |ag/L from ELS test performed in the same laboratory.
Pimephales promelas
An ACR for this species could not be calculated following the OW approach. Mount and
Stephan (1967) performed an acute and chronic test in the same laboratory, but the acute test was
static. The OPP ACR fori5, promelas is 63.18, calculated as the geometric mean of the three
acute flow-through tests listed in Table 6 divided by the NOEC of the Mount and Stephan
(1967) chronic test.
Ptychocheilus lucius
An ACR for this species could not be calculated following the OW approach. Beyers et al.
(1994) performed an early life stage (ELS) chronic test and a static-renewal acute test. Although
the acute and chronic tests were performed in the same laboratory, the Guidelines (U.S. EPA
1985) states that acute test data must also be from a flow-through study (except for Daphnids,
where static acute tests are acceptable). Also worth noting is the study authors reported that the
water for the acute and chronic tests was inadvertently aged differently, with the acute tests
having higher dissolved oxygen and pH, and lower hardness and alkalinity, than the chronic
tests. The ACR following the OPP approach is 5.440, calculated as the acute value of 9,140 ng/L
from Beyers et al. (1994) divided by the NOEC of 1,680 ng/L from ELS test performed in the
same laboratory.
Jordanella floridae
The OW ACR for J. floridae is 15.98, calculated as the acute value from a flow-through test
conducted by Hermanutz (1978) divided by the MATC for the survival endpoint from a life
cycle test conducted by Hermanutz (1978). The OPP ACR for J. floridae is 40.58, calculated as
the acute value from a flow-through test conducted by Hermanutz (1978), divided by the NOEC
for the growth endpoint from a life cycle test conducted by Hermanutz (1978).
51
-------
Lepomis macrochirus
The OW ACR for L. macrochirus is 15.27, calculated as the geometric mean of two flow
through acute tests conducted by Eaton (1970) divided by the MATC of an ELS test conducted
in the same laboratory (Eaton 1970). The OPP ACR is 21.60, calculated as the geometric mean
of the Eaton (1970) acute tests divided by the NOEC of the Eaton (1970) ELS test.
Oryzias latipes
An OW ACR could not be calculated for O. latipes. An OPP ACR of 48.60 was calculated as the
ratio of the definitive acute value 9,700 |ag/L divided by the NOEC of 199.6 |ag/L from Beaman
et al. (1999). This ACR is considered qualitative and is not used to calculate a final ACR for this
chemical.
Oreochromis mossambica
An OW ACR could not be calculated because there were no paired acute and chronic tests. An
OPP ACR was also not calculated for this species because there was no definitive NOEC for the
chronic test. If a NOEC of <500 |ag/L is used as the denominator, the ACR would be >1.523,
calculated as the geometric mean of the two definitive acute values divided by the NOEC.
Because this is a small greater than value, it is not included in the final ACR calculations.
Channa punctata
An OW ACR could not be calculated for this species. An acute (Pandey et al. 2005) and chronic
(Pandey et al. 1981) test were conducted by the same author, but it could not be confirmed if the
tests were performed in the same laboratory. Because the chronic test duration was only 15 days,
an OW ACR would not have been calculated even if the acute and chronic tests were from the
same laboratory. An OPP ACR of 4.234 was calculated as the geometric mean of the four acute
tests divided by the NOEC from Pandey et al. (1981). This ACR is considered qualitative and is
not used to calculate a final ACR for this chemical.
Cyprinodon variegatus
The OW ACR is 8.5, calculated as the acute value of 51 |ig/L reported in Hansen and Parish
(1977) and Parish et al. (1977) divided by the paired chronic MATC of 6 |ig/L. The OPP ACR of
12.75 is calculated by the Hansen and Parish (1977) and Parish et al. (1977) acute value divided
by the paired NOEC of 4 |ig/L.
Final ACRs
The final ACRs (FACRs) for the two approaches, expressed as the geometric mean of all
available ACRs, is 10.54 following the OW approach, and 15.42 following the OPP approach.
The OW FACR consists of ACRs for J. jloridae, L. macrochirus, and C. variegatus. The OW
FACR also includes the qualitative ACR for D. magna that could not be calculated following the
OW methodology, but which is included because it is the only invertebrate species for which
chronic data are available. The OPP FACR consists of ACRs for the species listed above, as well
as 0. mykiss, G. elegans, P. promelas, and P. lucius. Qualitative ACRs for 0. latipes and C.
punctata were not included here because of chronic test duration. Table 7 lists all final and
invertebrate only ACRs.
52
-------
The Guidelines notes that a range of ACRs that is greater than 10-fold may indicate a potential
cause for concern. ACRs calculated following the OPP approach vary by a factor of 11.6. While
there is no clear relationship between the size of ACRs and acute sensitivity for this chemical,
the largest ACR is for the acutely insensitive fish species P. promelas. A second option would be
to exclude the P. promelas ACR of 63.18 from the OPP FACR calculation, which would result
in a FACR of 12.61 (Table 7).
Comparison of Freshwater Chronic Values for Malathion
OPP Chronic Benchmarks
For malathion, the freshwater invertebrate chronic benchmark is 0.06 |ig/L (Table 8), the NOEC
of a registrant submitted D. magna test (Blakemore and Burgess 1990). The freshwater fish
chronic benchmark is 8.6 |ig/L, the NOEC for the growth endpoint reported in Hermanutz
(1978).
OW Freshwater Chronic Values - All Taxa
Final chronic concentrations following the ACR methodology are calculated by dividing the final
acute value by a final ACR (FACR). For malathion, a freshwater FAV of 0.8927 |ig/L was
calculated from the 53 genera included in the 2010 ECOTOX update. The final chronic value
following the OW-ACR approach (including the D. magna ACR that deviated from the
Guidelines), is 0.0847 |ag/L (0.8927 |ag/L ^ 10.54), and the final chronic value following the
OPP-ACR approach is 0.0579 jig/L (0.8927 jig/L - 15.42). The OPP FACR following the
second option (excluding the ACR of 63.18 for P. promelas) is 0.0708 (0.8927 |ag/L 12.61).
OW Freshwater Chronic Values - Invertebrate Taxa
Final chronic concentrations for the invertebrate-only malathion dataset are calculated by
dividing the final invertebrate acute value by an ACR. This dataset was comprised of acute
invertebrate test data found in the 2010 ECOTOX update and the 2010 effects determination
report U.S. EPA (2010). The resulting acute HCos calculated from the 29 invertebrate genera
using the Guidelines methology was 0.8360 ng/L. The final invertebrate chronic value following
the OW-ACR approach (using the D. magna ACR that deviated from the Guidelines) is 0.1407
Hg/L (0.8360 |ag/L ^ 5.942), and the final chronic value following the OPP-ACR approach is
0.0632 |ag/L (0.8360 |ag/L ^ 13.22). Table 8 lists all chronic values calculated following the
different approaches.
53
-------
Table 5. Chronic test data for malathion.
All concentrations expressed as ng/L.
Genus
Species
NOEC
LOEC
MATC
Reference
Test data re
)ortcd in:
OPP
Classification
Notes"
2010
ECOTOX
Search
2007
OPP
2010 OPP
Invertebrates
Daphnia
magna
0.57
0.76
0.658
Biesinger 1973
X
OW,OPP
Daphnia
magna
0.06
0.1
0.077
Blakemore and
Burgess 1990
Table 23
Table 4-10
Acceptable
OW,OPP
Daphnia
magna
0.15
NR
0.150
Dortland 1980
Table 23
Qualitative
OPP
Vertebrates
Oncorhynchus
mykiss
21
44
30.40
Cohle 1989
Table 20
Table 4-7
Qualitative
ELS; OPP
Gila
elegans
990
2,000
1,407
Beyers et al.
1994
X
ELS; OPP
Pimephales
promelas
200
580
340.6
Mount and
Stephan 1967
X
LC; OPP
Ptychocheilus
lucius
1680
3,510
2,428
Beyers et al.
1994
X
ELS; OPP
Jordanella
floridaeh
19.3
25
21.83
Hermanutz 1978
X
LC; OW
Jordanella
floridaec
8.6
10.9
9.682
Hermanutz 1978
Table 20
Table 4-7
Quantitative
LC; OPP
Lepomis
macrochirus
5
10
7.071
Eaton 1970
X
ELS; OW,OPP
Oryzias
latipes
199.6
798
399.2
Beaman et al.
1999
Table 20
Table 4-7
Qualitative
14d; OPP
Oreochromis
mossambica
ND
500
Sweilum 2006
Table 20
Table 4-7
Qualitative
168d
Channa
punctata
500
ND
Pandey et al.
1981
Table 20
Table 4-7
Qualitative
15d; OPP
Cyprinodon
variegatus
4
9
6
Hansen and
Parrish 1977
X
ELS; OW,OPP
a LC-life cycle test, ELS-early life stage test, OW - used in OW-ACR calculation, OPP - used in OPP-ACR calculation
54
-------
Table 6. Acute malathion test data for species with chronic test data. All concentrations expressed as ng/L.
(iCIIIIS
Species
i:c 50
or
l.( 50
Reference
Tcsl riala reported in:
OPP
Classification
\o(cs;l
2010
i'.cotox
Search
200"7 ()l>l>
2010 OPP
Invertebrates
Daphnia
magna
1.0
Johnson 1980b
X
Table 22
Table 4-8
Acceptable
EC50; S,U; OW, OPP
Daphnia
magna
1.6
Maas 1982
X
LC50; S,U; OPP
Daphnia
magna
33
Hermensetal. 1984
X
LC50; S,M; OPP
Daphnia
magna
1.8
Kikuchi et al. 2000
X
EC50; S,U; OW,OPP
Daphnia
magna
0.90
Ren et al. 2007
X
LC50; S,U; OPP
Daphnia
magna
2.20
Burgess 1989
Table 22
Table 4-8
Acceptable
57% a.i.; OPP
Daphnia
magna
0.098
Raweshetal. 1975
Table 22
Qualitative -
2007; Invalid -
2010
Not used, 24hr.
Daphnia
magna
1.7
ECOREF 6449
Table 22
Qualitative
OPP
Daphnia
magna
2.35
Cano et al. 1999
Table 22
Qualitative
Not used, 24 hr.
Vertebrates
Oncorhynchus
mykiss
77
Cope 1965
X
S,U; OPP
Oncorhynchus
mykiss
68
Cope 1965
X
S,U; OPP
Oncorhynchus
mykiss
110
Cope 1965
X
S,U; OPP
Oncorhynchus
mykiss
170
Macek and McAllister
1970
X
Table 4-3
S,U; OPP
Oncorhynchus
mykiss
122
Post and Schroeder 1971
X
S,U; OPP
Oncorhynchus
mykiss
93.5
Schoettger 1970
X
S,U; OPP
Oncorhynchus
mykiss
200
Johnson 1980b; Mayer and
Ellersieck 1986
X
S,U; OPP
Oncorhynchus
mykiss
94
Mayer and Ellersieck 1986
X
S,U; OPP
Oncorhynchus
mykiss
4.1
Mayer and Ellersieck 1986
X
Table 19
Table 4-3
Qualitative
S,U; OPP
Oncorhynchus
mykiss
138
Mayer and Ellersieck 1986
X
S,U; OPP
Oncorhynchus
mykiss
100
Mayer and Ellersieck 1986
X
S,U; OPP
Oncorhynchus
mykiss
66
Mayer and Ellersieck 1986
X
S,U; OPP
Oncorhynchus
mykiss
80
Mayer and Ellersieck 1986
X
S,U; OPP
Oncorhynchus
mykiss
160
McKimetal. 1987
X
Table 19
Qualitative
S,U; OPP
Oncorhynchus
mykiss
250
Li and Fan 1996
X
S,U; OPP
Oncorhynchus
mykiss
32.8
Animal Biology Lab 1968
Table 4-3
Acceptable
OPP
Gila
elegans
15,300
Beyers etal. 1994
X
R,M; OPP
55
-------
(iCIIIIS
Species
i:c 50
or
l.( 50
Reference
Test diilii reported in:
OPP
Cliissiriciilion
Nolev'
2010
i'.cotox
Sesirch
200"7 ()l>l>
2010 OPP
Pimephales
promelas
16,000
Pickering et al. 1962
X
S,U
Pimephales
promelas
23,000
Pickering et al. 1962
X
s,u
Pimephales
promelas
9,000
Mount and Stephan 1967
X
s,u
Pimephales
promelas
13,500
Bender 1969a
X
F,U; OPP
Pimephales
promelas
9,700
Bender 1969b
X
s,u
Pimephales
promelas
8,650
Macek and McAllister
1970; Johnson 1980b;
Mayer and Ellersieck 1986
X
Table 19
Table 4-3
Acceptable
s,u
Pimephales
promelas
11,000
Mayer and Ellersieck 1986
X
s,u
Pimephales
promelas
14,100
Geigeretal. 1988
X
Table 19
Qualitative
F,M; OPP
Pimephales
promelas
10,600
Geigeretal. 1988
X
F,M; OPP
Pimephales
promelas
12,500
Henderson and Pickering
1958
Table 19
Qualitative
Ptychocheilus
lucius
9,140
Beyers etal. 1994
X
R,M; OPP
Jordanella
floridae
349
Hermanutz 1978
X
Table 19
Qualitative
F,M; OW,OPP
Jordanella
floridae
280
Hermanutz et al. 1985
Table 19
Qualitative
Lepomis
macrochirus
90
Pickering et al. 1962
X
S,U
Lepomis
macrochirus
120
Macek etal. 1969
X
S,U
Lepomis
macrochirus
55
Macek etal. 1969
X
S,U
Lepomis
macrochirus
46
Macek etal. 1969
X
S,U
Lepomis
macrochirus
131
Eaton 1970
X
F,U; OW,OPP
Lepomis
macrochirus
89
Eaton 1970
X
F,U; OW,OPP
Lepomis
macrochirus
103
Macek and McAllister
1970; Johnson 1980b;
Mayer and Ellersieck 1986
X
Table 4-3
Qualitative
s,u
Lepomis
macrochirus
20
Mayer and Ellersieck 1986
X
Table 19
Table 4-3
Qualitative
s,u
Lepomis
macrochirus
40
Mayer and Ellersieck 1986
X
Table 4-3
Qualitative
s,u
Lepomis
macrochirus
55
Mayer and Ellersieck 1986
X
Table 4-3
Qualitative
s,u
Lepomis
macrochirus
84
Mayer and Ellersieck 1986
X
s,u
Lepomis
macrochirus
87
Mayer and Ellersieck 1986
X
s,u
Lepomis
macrochirus
30
Mayer and Ellersieck 1986
X
Table 19
Table 4-3
Qualitative
s,u
Lepomis
macrochirus
110
Mayer and Ellersieck 1986
X
s,u
Lepomis
macrochirus
336.6
ECOTOX 77525
Table 19
Qualitative
56
-------
(iCIIIIS
Species
i:c 50
or
l.( 50
Reference
Test diilii reported in:
OPP
Cliissiriciilion
Nolev'
2010
i'.cotox
Sesirch
200"7 OPP
2010 OPP
Lepomis
macrochirus
48
Gries and Purghart 2001
Table 4-3
Acceptable
Oryzias
latipes
<2,800
ECOTOX 8977
Table 19
Qualitative
Oryzias
latipes
9,700
ECOTOX 89099
Table 19
Qualitative
OPP
Oreochromis
mossambica
<2,400
Mayer and Ellersieck 1986
X
s,u
Oreochromis
mossambica
2,000
Mayer and Ellersieck 1986
X
Table 19
Table 4-3
Qualitative
s,u
Oreochromis
mossambica
290.1
Liuetal. 1983
Table 19
Qualitative
Channa
punctata
3890
ECOTOX 11888
Table 19
Qualitative
Channa
punctata
894
Kaur and Toor 1995
Table 19
Qualitative
Channa
punctata
874
Kaur and Toor 1995
Table 19
Qualitative
Channa
punctata
6610
Pandey et al. 2005
Table 19
Qualitative
OPP
Cyprinodon
variegatus
51
Hansen and Parrish 1977
X
F,M; OW,OPP
Cyprinodon
variegatus
33
Bowman 1989
X
F,U
aF - flow through, R - renewal, S - static, M - measured, U - unmeasured, OW - used in OW-ACR calculation, OPP - used in OPP-ACR calculation
57
-------
Table 7. ACRs by species and calculation method.
Genus
Species
ACR
Notes
OW-ACR
OPP-ACR
Invertebrates
Daphnia
magna
5.942a
13.22
OW ACR following Guidelines could not be calculated.
Vertebrates
Oncorhynchus
mykiss
N/A
4.074
Gila
elegans
N/A
15.46
Pimephales
promelas
N/A
63.18
Ptychocheilus
lucius
N/A
5.440
Jordanella
floridae
15.98
40.58
Lepomis
macrochirus
15.27
21.60
Oryzias
latipes
N/A
48.60
OPP ACR should be considered qualitative due to chronic test duration (14-d)
Oreochromis
mossambica
N/A
N/A
ACR not calculated because no NOAEC was available
Channa
punctata
N/A
4.234
OPP ACR should be considered qualitative due to chronic test duration (15 -d)
Cyprinodon
variegatus
8.5
12.75
All Taxa FACR (OPP Option l)b
10.54
15.42
All Taxa FACR (OPP Option 2)c
10.54
12.61
All Invertebrates
5.942
13.22
a An ACR following the Guidelines could not be calculated, as there were no acute and chronic studies from same study/laboratory/test water.
The resulting qualitative ACR was included because no other ACRs for invertebrate taxa were available.
b ~ OPP all taxa ACR does not include qualitative ACRs for O. latipes or C. punctata. OW all taxa ACR does include the "qualitative" D. magna ACR.
0 - Does not include ACR for P. promelas ((>10x spread and acutely insensitive).
58
-------
Table 8. Summary and comparison of freshwater chronic values for malathion.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value.
Pesticide
OPP Most Sensitive
ALB
(Year published,
species)
OW Illustrative ALC
(# of ACRs filled, magnitude
relative to ALB)
OW Invertebrate-only HCos/2
(# of ACRs filled, magnitude
relative to ALB)
Malathion
0.06 ng/L
(2016, Daphnia magna)
0.08 ng/L
(illustrative ALC example calculated
for this analysis; 0.75X)
0.14 (ig/L
(See Table 7 for ACRs, 0.43X)
1.1.4.3 Malathion References
ECOREF 6449: Dortland, R.J. 1980. Toxicological Evaluation of Parathion and Azinphosmethyl
in Freshwater Model Ecosystems. Versl. Landbouwkd. Onderz., 898: 1-112.
ECOTOX 11888: Haider, S., andR.M. Inbaraj (1986). Relative Toxicity of Technical Material
and Commercial Formulation of Malathion and Endosulfan to a Freshwater Fish, Channel
punctatus (Bloch). Ecotoxicol. Environ. Saf., 11, (3), 347-351. doi: 10.1016/0147-
6513(86)90107-7. ECOREF#: 11888.
ECOTOX 77525: Van der Schalie, W.H., T.R. Shedd, M.W. Widder, and L.M. Brennan (2004).
Response Characteristics of an Aquatic Biomonitor Used for Rapid Toxicity Detection. J. Appl.
Toxicol. 24(5): 387-394. doi:10.1002/jat,1028.
ECOTOX 89099: Wolfe, M.F., D.E. Hinton, and J.N. Seiber (1995). Aqueous Sample
Preparation for Bioassay Using Supercritical Fluid Extraction. Environ. Toxicol. Chem. 14(6):
1001-1009. doi:10.1002/etc.5620140611.
ECOTOX 8977: Shim, J.C., and L.S. Self (1973). Toxicity of Agricultural Chemicals to
Larvivorous Fish in Korean Rice Fields. Trop. Med. 15(3): 123-130.
MRID 05009242; Sanders, H.O. 1969. Toxicity of Pesticides to the Crustacean Gammarus
lacustris. Tech.Pap.No.25, U.S.D.I., Bur. Sports Fish. Wildl., Fish Wildl. Serv., Washington, DC,
18 p.
MRID 40098001: Mayer, F.L. and M.R. Ellersieck. 1986. Manual of acute toxicity:
Interpretation and data base for 410 chemicals and 66 species of freshwater animals. Resour.
Publ. No. 160, U.S. Dep. Interior, Fish Wildl. Serv., Washington, DC. 505 p.
MRID 41029701: Burgess, D. 1989. Acute flow-through toxicity of Cythion 57% EC to Daphnia
magna: Report No. 37394. Unpublished study prepared by Analytical Bio-Chemistry Labs Inc.
197 p.
MRID 48078003: Anonymous. 1968. Malathion Technical Toxicity to Rainbow Trout; Test
Number 105. Project Number: MB/69. Unpublished study prepared by Animal Biology
Laboratory. 13 p.
Bailey, H.C., and D.H.W. Liu. 1980. Lumbriculus variegatus, a Benthic Oligochaete, as a
Bioassay Organism. ASTM Spec. Tech. Publ., 205-215.
59
-------
Beaman, J.R., R. Finch, H. Gardner, F. Hoffmann, A. Rosencrance, and J.T. Zelikoff 1999.
Mammalian Immunoassays for Predicting the Toxicity of Malathion in a Laboratory Fish Model.
J. Toxicol. Environ. Health Part A 56(8): 523-542. doi:l0.1080/00984109909350175.
Bender, M.E., 1969a. The Toxicity of the Hydrolysis and Breakdown Products of Malathion to
Fathead minnow - University of Michigan.
Bender, M.E. 196b. Uptake and Retention of Malathion by the Carp. Prog. Fish-Cult. 31(3): 155-
159.
Bender, M.E., and J.R. Westman. 1976. The Toxicity of Malathion and Its Hydrolysis Products
to the Eastern Mudminnow, Umbra pygmaea (DeKay). Chesapeake Sci. 17(2): 125-128.
Beyers, D.W., T.J. Keefe and C.A. Carlson. 1994. Toxicity of carbaryl and malathion to two
federally endangered fishes, as estimated by regression and ANOVA. Environ. Toxicol. Chem.
13(1): 101-107.
Biesinger, K.E. 1973. The Chronic Toxicity of Some Pesticides to Daphnia magna. Interim Rep.
No. ROAP 16AAK, Task 06, Natl. Water Qual. Lab., Duluth, MN, 5 p.
Birge, W.J., J.A. Black, and D.M. Bruser 1979. Toxicity of Organic Chemicals to Embryo-
Larval Stages of Fish. EPA-560/11-79-007, U.S.EPA, Washington, D.C., 60 p.
Blakemore, G.; Burgess, D. 1990. Chronic Toxicity of Cythion to Daphnia magna Under Flow-
through Test Conditions: Lab Project Number: 37399. Unpublished study prepared by Analytical
BioChemistry Laboratories, Inc. 391 p.
Bowman, J. 1989. Acute Flow-Through Toxicity of Cythion Technical to Sheepshead Minnow
(Cyprinodon variegatus): Report No. 37397. Unpublished study prepared by Analytical Bio-
chemistry Laboratories, Inc. 205 p.
Burgess, D. 1989. Acute flow-through toxicity of Cythion 57% EC to Daphnia magna: Report
No. 37394. Unpublished study prepared by Analytical Bio-Chemistry Labs Inc. 197 p.
Cano, E., A. Jimenez, J.A. Cabral, and M.E. Ocete (1999). Acute Toxicity of Malathion and the
New Surfactant "Genapol OXD 080" on Species of Rice Basins. Bull. Environ. Contam. Toxicol.
63(1): 133-138. doi:10.1007/s001289900958.
Cohle, P. 1989. Early Life Stage Toxicity of Cythion to Rainbow Trout (Oncorhynchus mykiss)
in a Flow-through System: Lab Report Number: 37400. Unpublished study prepared by
Analytical Bio-Chemistry Laboratories, Inc. 1068 p.
Cope, O.B. 1965. Sport Fishery Investigations. Fish and Wildlife Service Circular 226, Effects of
Pesticides on Fish and Wildlife. Washington, DC, 51-63.
Cope, O.B. 1966. Contamination of the Freshwater Ecosystem by Pesticides. J. Appl. Ecol., 3,
33-44. doi: 10.2307/2401442.
Dortland, R.J. 1980. Toxicological Evaluation of Parathion and Azinphosmethyl in Freshwater
Model Ecosystems. Versl. Landbouwkd. Onderz., 898: 1-112.
60
-------
Dwyer, F.J., L.C. Sappington, D.R. Buckler and S.B. Jones. 1995. Use of surrogate species in
assessing contaminant risk to endangered and threatened fishes. EPA/600/R-96/029, U.S. EPA,
Washington, D.C.
Eaton, J.G. 1970. Chronic Malathion Toxicity to the Bluegill (Lepomis macrochirus Rafinesque).
Water Res. 4(10): 673-684.
Federle, P.F., and W.J. Collins. 1976. Insecticide Toxicity to Three Insects from Ohio Ponds.
Ohio J. Sci. 76(1): 19-24.
Foster, S., M. Thomas, and W. Korth. 1998. Laboratory-Derived Acute Toxicity of Selected
Pesticides to Ceriodaphnia dubia. Australas. J. Ecotoxicol. 4(1): 53-59.
Gaufin, A.R., L.D. Jensen, A.V. Nebeker, T. Nelson, and R.W. Teel. 1965. Toxicity of Ten
Organic Insecticides to Various Aquatic Invertebrates. Water Sewage Works, 12: 276-279.
Geiger, D.L., D.J. Call, and L.T. Brooke. 1988. Acute Toxicities of Organic Chemicals to
Fathead Minnows (Pimephales promelas) Volume IV. Center for Lake Superior Environmental
Studies, University of Wisconsin, Superior, WI, 4, 355 p.
Gries, T. and V. Purghart. 2001. Malathion Technical: Acute Toxicity Test with Bluegill Sunfish
(Lepomis macrochirus) Under Flow-Through Conditions: Final Report. Project Number:
314/FYF, 1005/018/105. Unpublished study prepared by Springborn Laboratories (Europe) Ag.
58 p.
Hansen and Parrish Hansen: D.J., and P.R. Parrish. 1977. Suitability of Sheepshead Minnows
(Cyprinodon variegatus) for Life-Cycle Toxicity Tests. ASTM Spec. Tech. Publ., 117-126.
(ECOTOX#:5074).
Hansen, C.R., Jr., and J. A. Kawatski 1976. Application of 24-Hour Postexposure Observation to
Acute Toxicity Studies with Invertebrates. J. Fish. Res. Board Can. 33(5): 1198-1201.
doi: 10.1139/f76-153.
Henderson, C., and Q.H. Pickering. 1958. Toxicity of Organic Phosphorus Insecticides to Fish.
Trans. Am. Fish. Soc. 87: 39-51.
Hermanutz, R.O. 1978. Endrin and Malathion Toxicity to Flagfish (Jordanella floridae). Arch.
Environ. Contam. Toxicol. 7(2): 159-168.
Hermanutz, R. O., Eaton, J. G., and Mueller, L. H. 1985. Toxicity of Endrin and Malathion
Mixtures to Flagfish (Jordanella floridae). Arch. Environ. Contam. Toxicol. 14: 307-314.
Hermens, J., H. Canton, N. Steyger, and R. Wegman. 1984. Joint Effects of a Mixture of 14
Chemicals on Mortality and Inhibition of Reproduction of Daphnia magna. Aquat. Toxicol. 5(4):
315-322.
Hoick, A.R., and C.L. Meek (1987). Dose-Mortality Responses of Crawfish and Mosquitoes to
Selected Pesticides. Am. Mosq. Control Assoc. J. 3(3): 407-411.
Johnson, C.R. 1980. The Effects of Five Organophosphorus Insecticides on Thermal Stress in
Tadpoles of the Pacific Tree Frog, Hyla regilla. Zool. J. Linn. Soc. 69(2): 143-147.
61
-------
Kaur, H., and H.S. Toor. 1995. Toxicity of Some Insecticides to the Fingerlings of Indian Major
Carp Cirrhina mrigala (Hamilton). Indian J. Ecol. 22(2): 140-142.
Keller, A.E., and D.S. Ruessler. 1997. The Toxicity of Malathion to Unionid Mussels:
Relationship to Expected Environmental Concentrations. Environ. Toxicol. Chem. 16(5): 1028-
1033. doi: 10.1002/etc.5620160524.
Key, P.B., and M.H. Fulton. 2006. Correlation Between 96-h Mortality and 24-h
Acetylcholinesterase Inhibition in Three Grass Shrimp Larval Life Stages. Ecotoxicol. Environ.
Saf. 63(3): 389-392.
Kikuchi, M., Y. Sasaki, and M. Wakabayashi. 2000. Screening of Organophosphate Insecticide
Pollution in Water by Using Daphnia magna. Ecotoxicol. Environ. Saf. 47(3): 239-245.
doi: 10.1006/eesa.2000.1958.
Kumar, K., and B.A. Ansari. 1984. Malathion Toxicity: Skeletal Deformities in Zebrafish
(Brachydanio rerio, Cyprinidae). Pestic. Sci., 15, 107-111.
Li, S.N., and D.F. Fan. 1996. Correlation Between Biochemical Parameters and Susceptibility of
Freshwater Fish to Malathion. J. Toxicol. Environ. Health 48(4): 413-418.
Liong, P.C., W.P. Hamzah, and V. Murugan. 1988. Toxicity of Some Pesticides Towards
Freshwater Fishes. Fish. Bull. Dep. Fish. (Malays.) No. 57, 13 p.
Lui, O. S., M. A. Ambak, and A. K. M. Mohsin. 1983. A Comparison of Tolerance Level of
Tilapia to Malathion on Clear and Muddy Bottom. Malays. Appl. Biol., 12, (2), 25-29.
(ECOTOX#: 11603).
Maas, J.L. 1982. Toxicity of Pesticides. Report No. 82, Laboratory for Ecotoxicology, Institute
for Inland Water Management and Waste Water Treatment, 15, 4 p.
Macek, K.J. and W.A. McAllister. 1970. Insecticide susceptibility of some common fish family
representatives. Trans. Am. Fish. Soc. 99(1): 20-27.
Macek, K.J., C. Hutchinson, and O.B. Cope. 1969. The Effects of Temperature on the
Susceptibility of Bluegills and Rainbow Trout to Selected Pesticides. Bull. Environ. Contam.
Toxicol. 4(3): 174-183.
Mayer, F.L. and M.R. Ellersieck. 1986. Manual of acute toxicity: Interpretation and database for
410 chemicals and 66 species of freshwater animals. Resour. Publ. No. 160, U.S. Dep. Interior,
Fish Wildl. Serv., Washington, DC. 505 p.
McKim, J.M., P.K. Schmieder, G.J. Niemi, R.W. Carlson, and T.R. Henry. 1987. Use of
Respiratory-Cardiovascular Responses of Rainbow Trout (Salmo gairdneri) in Identifying Acute
Toxicity Syndromes in Fish: Part 2. Malathion, Carbaryl, Acrolein and Benzaldehyde. Environ.
Toxicol. Chem. 6: 313-328.
Mount, D.I., and C.E. Stephan. 1967. A Method for Establishing Acceptable Toxicant Limits for
Fish - Malathion and the Butoxyethanol Ester of 2,4-D. Trans. Am. Fish. Soc. 96(2): 185-193.
62
-------
Olvera-Hernandez, E., L. Martinez-Tabche, and F. Martinez-Jeronimo. 2004. Bioavailability and
Effects of Malathion in Artificial Sediments on Simocephalus vetulus (Cladocera: Daphniidae).
Bull. Environ. Contam. Toxicol. 73(1): 197-204.
Palawski, D., J.B. Hunn, and F.J. Dwyer. 1985. Sensitivity of Young Striped Bass to Organic
and Inorganic Contaminants in Fresh and Saline Waters. Trans. Am. Fish. Soc. 114(5): 748-753.
Pandey, P.K., N.K. Singh, B.P. Choudhary, and G.K. Thakur (1981). Effect of
Organophosphorus Insecticide, Malathion, on the Haematology of Channa punctatus (Bloch). J.
Inl. Fish. Soc. India, 13(2): 120-121.
Pandey, S., R. Kumar, S. Sharma, N.S. Nagpure, S.K. Srivastava, and M.S. Verma (2005). Acute
Toxicity Bioassays of Mercuric Chloride and Malathion on Air-Breathing Fish Channa punctatus
(Bloch). Ecotoxicol. Environ. Saf. 61(1): 114-120.
Pickering, Q.H., C. Henderson, and A.E. Lemke 1962. The Toxicity of Organic Phosphorus
Insecticides to Different Species of Warmwater Fishes. Trans. Am. Fish. Soc. 91: 175-184.
Post, G. and T.R. Schroeder. 1971. The toxicity of four insecticides to four salmonid species.
Bull. Environ. Contam. Toxicol. 6(2): 144-155.
Ren, Z., J. Zha, M. Ma, Z. Wang, and A. Gerhardt. 2007. The Early Warning of Aquatic
Organophosphorus Pesticide Contamination by On-Line Monitoring Behavioral Changes of
Daphnia magna. Environ. Monit. Assess. 134(1-3): 373-383.
Sanders, H.O. 1969. Toxicity of Pesticides to the Crustacean Gammarus lacustris.
Tech.Pap.No.25, U.S.D.I., Bur. Sports Fish. Wildl., Fish Wildl. Serv., Washington, DC, 18 p.
Sanders, H.O. 1970. Pesticide Toxicities to Tadpoles of the Western Chorus Frog Pseudacris
triseriata and Fowler's Toad Bufo woodhousii fowleri. Copeia, 2: 246-251.
Sanders, H.O. 1972. Toxicity of Some Insecticides to Four Species of Malacostracan
Crustaceans. Tech. Pap. Bur. Sport Fish. Wildl., 66, 19 p.
Sanders, H.O., and O.B. Cope. 1966. Toxicities of Several Pesticides to Two Species of
Cladocerans. Trans. Am. Fish. Soc. 95(2): 165-169.
Schoettger, R.A. 1970. Fish-Pesticide Research Laboratory. In: Prog, in Sport Fish. Res., U.S.
Dep. Interior, Bur. Sport Fish, and Wildl. Res., Publ. No. 106, 2-40.
Snawder, J.E., and J.E. Chambers. 1989. Toxic and Developmental Effects of Organophosphorus
Insecticides in Embryos of the South African Clawed Frog. J. Environ. Sci. Health Part B Pestic.
Food Contam. Agric. Wastes 24(3): 205-218.
Sparling, D.W., and G. Fellers. 2007. Comparative Toxicity of Chlorpyrifos, Diazinon,
Malathion and Their Oxon Derivatives to Larval Rana boylii. Environ. Pollut. 147(3): 535-539.
Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. 1985.
Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic
Organisms and their Uses. PB85-227049. Office of Research and Development. Duluth, MN,
Narragansett, RI, Corvallis, OR.
63
-------
Sulaiman, A.H., A.R. Abdullah, and S.K. Ahmad. 1989. Toxicity of Malathion to Red Tilapia
(Hybrid Tilapia mossambica x Tilapia nilotica): Behavioural, Histopathological and Anti-
cholinesterase Studies. Malays. Appl. Biol. 18(2): 163-170.
Sweilum, M.A. 2006. Effect of Sublethal Toxicity of some Pesticides on Growth Parameters,
Haematological Properties and Total Production of Nile Tilapia (Oreochromis niloticus L.) and
Water Quality of Ponds. Aquae. Res. 37(11): 1079-1089.
Ton, C., Y. Lin, and C. Willett 2006. Zebrafish as a Model for Developmental Neurotoxicity
Testing. Birth Defects Res. A Clin. Mol. Teratol. 76(7): 553-567.
U.S. EPA. 1976. Quality criteria for water. PB-263 943. Office of Water and Hazardous
Materials. Washington D.C. July 26, 1976.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2005. Use of acute-to-chronic ratios in support of ecological risk assessment of
pesticides. Memo to Steve Bradbury, Director, Environmental Fate and Effects Division. Office
of Prevention, Pesticides, and Toxic Substances. June 7, 2005.
U.S. EPA. 2007. Risks of malathion use to the federally-listed California red legged frog (Rana
aurora draytonii). Pesticide effects determination. Office of Pesticide Programs. Washington,
D.C. 20460. October 19, 2007.
U.S. EPA. 2010. Risks of malathion use to the federally threatened delta smelt (Hypomesus
transpacificus) and California tiger salamander (Ambystoma californiense), Central California
distinct population segment, and the federally endangered California tiger salamander, Santa
Barbara County and Sonoma County distinct population segments. Environmental Fate and
Effects Division, OPP. Washington, D.C. 20460. September 29, 2010.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
Vedamanikam, V.J. 2009. Formation of Resistance in the Chironomus plumosus to Four
Pesticides over 45 Generations. Toxicol. Environ. Chem. 91(1): 187-194.
Whitten, B.K., and C.J. Goodnight. 1966. Toxicity of Some Common Insecticides to Tubificids.
J. Water Pollut. Control Fed. 38(2): 227-235.
64
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1.1.5 Comparison of Aquatic Life Toxicity Values for Diazinon: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) for diazinon were obtained from the 2005 diazinon aquatic life criteria
(ALC) document (U.S. EPA 2005a), which serves as the based dataset, supplemented with an
update to this data from EPA ECOTOX Knowledgebase in 2010.
1.1.5.1 Diazinon Acute Toxicity Data
Acute data for diazinon were obtained from the 2005 diazinon aquatic life criteria (ALC)
document (U.S. EPA 2005a), which serves as the based dataset, supplemented with an update to
this data from ECOTOX in 2010. (See Table 1.) The ECOTOX 2010 update included additional
LCsos for Ceriodaphnia dubia, and one LC50 (and SMAV) for Chironomus riparius not in the
ALC document. The OPP pesticide effects determination document that served as the basis for
the invertebrate OPP benchmark concentration was also examined (U.S. EPA 2007). The
invertebrate (Ceriodaphnia dubia) and fish (Oncorhynchus my kiss) tests that served as the basis
for the OPP acute benchmarks were both included in the ALC document and/or the 2010
ECOTOX update.
The final diazinon acute dataset consisted of 27 SMAVs and 21 GMAVs, of which 14 SMAVs
and 11 GMAVs were for invertebrate taxa. Ranked species and genus mean acute values for all
invertebrates included in this analysis are listed in Table 2 below.
Table 1. Acute toxicity data of diazinon to freshwater aquatic organisms.
()\\
I.C50/
SMAV
(M8/U
<;may
(MS/'-)
MIJR
(lioup1
Species
l-X 50
(.uji/U
Reference
H
Planaria,
Dugesia tigrina
11,640
11,640
11,640
Phipps 1988
H
Ogliochate,
Lumbriculus variegates
9,980
-
Phipps 1988
H
Ogliochate (adult),
Lumbriculus variegates
9,700
-
Brooke 1989
H
Ogliochate,
Lumbriculus variegates
6,160
8,417
8,417
Ankley and Collyard 1995
G
Snail (2.4 g),
Gillia altilis
11,000
11,000
11,000
Robertson and Mazzella 1989
G
Apple snail (1 d),
Pomacea paludosa
2,950
-
Call 1993
G
Apple snail (7 d),
Pomacea paludosa
3,270
-
Call 1993
G
Apple snail (7 d),
Pomacea paludosa
3,390
3,198
3,198
Call 1993
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.57
Norberg-King 1987
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.66
Norberg-King 1987
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.57
Norberg-King 1987
65
-------
()\\
I.C50 /
S\1 AY
(MS/'-)
<;may
(MS/'-)
MIJR
(iroup'
Species
IX 50
(Mli/U
Reference
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
1
Norberg-King 1987
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.6
Norberg-King 1987
D
Cladoceran (<6 hr),
Ceriodaphnia dubia
0.66
Norberg-King 1987
D
Cladoceran (<48 hr),
Ceriodaphnia dubia
0.35
-
Norberg-King 1987
D
Cladoceran (<48 hr),
Ceriodaphnia dubia
0.35
-
Norberg-King 1987
D
Cladoceran (<6 hr),
Ceriodaphnia dubia
0.25
-
Norberg-King 1987
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.33
-
Norberg-King 1987
D
Cladoceran (<48 hr),
Ceriodaphnia dubia
0.35
-
Norberg-King 1987
D
Cladoceran (<48 hr),
Ceriodaphnia dubia
0.59
-
Norberg-King 1987
D
Cladoceran (<48 hr),
Ceriodaphnia dubia
0.43
-
Norberg-King 1987
D
Cladoceran (<48 hr),
Ceriodaphnia dubia
0.35
-
Norberg-King 1987
D
Cladoceran (<48 hr),
Ceriodaphnia dubia
0.36
-
Norberg-King 1987
D
Cladoceran (<48 hr),
Ceriodaphnia dubia
0.5
-
Ankley et al. 1991
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.58
-
Bailey et al. 1997
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.48
-
Bailey et al. 1997
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.26
-
Bailey et al. 1997
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.29
-
Bailey et al. 1997
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.38
-
Bailey et al. 2001
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.33
-
Bailey et al. 2001
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.45
-
Banks et al. 2003
D
Cladoceran (<24 hr),
Ceriodaphnia dubia
0.21
0.4248
0.4248
Banks et al. 2005
D
Cladoceran (<20 hr),
Daphnia magna
0.96
-
Vilkas 1976
D
Cladoceran (<24 hr),
Daphnia magna
1.5
-
Dortland 1980
D
Cladoceran (<48 hr),
Daphnia magna
0.8
1.048
Ankley et al. 1991
D
Cladoceran (1st instar),
Daphnia pulex
0.90
-
Cope 1965a; Sanders and Cope
1966
66
-------
()\\
MIJR
(iroup'
Species
I.C50/
IX 50
(Mli/U
S\1 AY
(MS/'-)
<;may
(MS/'-)
Reference
D
Cladoceran (1st instar),
Daphnia pulex
0.8
-
Johnson and Finley 1980;
Mayer and Ellersieck 1986
D
Cladoceran (<48 hr),
Daphnia pulex
0.65
0.7764
0.9022
Ankley et al. 1991
D
Cladoceran (1st instar),
Simocephalus serrulatus
1.8
-
Cope 1965a; Sanders and Cope
1966; Mayer and Ellersieck
1986
D
Cladoceran (1st instar),
Simocephalus serrulatus
1.4
1.587
1.587
Sanders and Cope 1966;
Johnson and Finley 1980;
Mayer and Ellersieck 1986
E
Amphipod (mature),
Gammarus fasciatus
2.04
2.04
Johnson and Finley 1980;
Mayer and Ellersieck 1986
E
Amphipod (mature),
Gammarus pseudolimnaeus
16.82
16.82
5.858
Hall and Anderson 2004
E
Amphipod (7-14 d),
Hyalella azteca
6.51
6.51
6.510
Ankley and Collyard 1995
F
Stonefly
(larva, 30-35 mm),
Pteronarcys californica
25
25
25.000
Cope 1965a; Sanders and Cope
1968; Johnson and Finley 1980;
Mayer and Ellersieck 1986
F
Midge (2nd-3rd instar),
Chironomus riparius
450
450
Brooke 1989
F
Midge (3rd instar),
Chironomus tentans
10.7
10.7
69.39
Ankley and Collyard 1995
A
Cutthroat trout (2.0 g),
Oncorhynchus clarki
1,700
-
Johnson and Finley 1980;
Mayer and Ellersieck 1986
A
Cutthroat trout (2.0 g),
Oncorhynchus clarki
2,760
2,166
Mayer and Ellersieck 1986
A
Rainbow trout (3.7 cm),
Oncorhynchus mykiss
400
-
Beliles 1965
A
Rainbow trout (1.20 g),
Oncorhynchus mykiss
90
-
Cope 1965a; Johnson and
Finley 1980; Mayer and
Ellersieck 1986
A
Rainbow trout (25-50 g),
Oncorhynchus mykiss
3,200
-
Bathe et al. 1975a
A
Rainbow trout,
Oncorhynchus mykiss
90
-
Ciba-Giegy 1976
A
Rainbow trout,
Oncorhynchus mykiss
1,350
425.8
Meier et al. 1979; Dennis et al.
1980
A
Chinook salmon (alevin),
Oncorhynchus tshawytscha
29,500
29,500
3,008
Pincetich 2004; Viant et al.
2006
A
Brook trout (1 yr),
Salvelinus fontinalis
800
-
Allison and Hermanutz 1977
A
Brook trout (1 yr),
Salvelinus fontinalis
450
-
Allison and Hermanutz 1977
A
Brook trout (1 yr),
Salvelinus fontinalis
1,050
723.0
Allison and Hermanutz 1977
A
Lake trout (3.20 g),
Salvelinus namaycush
602
602
659.8
Johnson and Finley 1980;
Mayer and Ellersieck 1986
B
Splittail (larva, 6 wk),
Pogonichthys macrolepidotus
8,900
8,900
8,900
Teh et al. 2004
67
-------
()\\
MDR
(iroup'
Species
I.C50/
IX 50
(Mli/U
SMAV
(MU/U
<;may
(MS/'-)
Reference
B
Zebrafish (0.4 g),
Danio rerio
8,000
8,000
8,000
Keizeretal. 1991
B
Fathead minnow (juvenile),
Pimephales promelas
6,600
-
Allison and Hermanutz 1977
B
Fathead minnow (juvenile),
Pimephales promelas
6,800
-
Allison and Hermanutz 1977
B
Fathead minnow (juvenile),
Pimephales promelas
10,000
-
Allison and Hermanutz 1977
B
Fathead minnow
(newly hatched larva),
Pimephales promelas
6,900
-
Jarvinen and Tanner 1982
B
Fathead minnow (juvenile),
Pimephales promelas
9,350
7,804
7,804
University of Wisconsin-
Superior 1988
B
Goldfish (2.5-6.0 cm),
Carassius auratus
9,000
9,000
9,000
Beliles 1965
B
Flagfish (6 wk),
Jordanella floridae
1,500
-
Allison and Hermanutz 1977
B
Flagfish (7 wk),
Jordanella floridae
1,800
1,643
1,643
Allison and Hermanutz 1977
B
Guppy (0.6 g),
Poecilia reticulata
800
800
800
Keizeretal. 1991
B
Bluegill (1 yr),
Lepomis macrochirus
480
-
Allison and Hermanutz 1977
B
Bluegill (1 yr),
Lepomis macrochirus
440
459.6
460
Allison and Hermanutz 1977
B
Bluegill (0.8 g),
Lepomis macrochirus
120°
-
Meier et al. 1979; Dennis et al.
1980
B
Bluegill (1.00 g),
Lepomis macrochirus
168.0°
Johnson and Finley 1980;
Mayer and Ellersieck 1986
C
Green frog (stage 8),
Rana clamitans
50
50
50
Harris etal. 1998
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The invertebrate OPP benchmark for diazinon is 0.105 |ig/L, which is V2 of the LC50 for the
cladoceran species C. dubia reported in a study by Banks et al. (2005). This test is the lowest of
24 LC50S that comprise the SMAV for C. dubia.
68
-------
The fish OPP benchmark for diazinon is 45 |ig/L, which is V2 of the LC50 of 90 |ig/L, the two
lowest LC50S for rainbow trout (Oncorhynchus mykiss), which is the second most sensitive fish
genera.
OW Acute Criterion
The acute criterion, or criterion maximum concentration (CMC) for diazinon in the 2005 ALC
document is 0.17 |ig/L.
Genus-Level Invertebrate-only HC05
The acute HC05 calculated from invertebrate genera shown in Table 2 above following the U.S.
EPA (1985) methodology is 0.1935 |ig/L (Table 3).
Table 2. Diazinon invertebrate SMAVs and GMAVs (^ig/L).
(Ionus
Species
S\1 AY
(IMAY
CMAY R;t 11k
Dugesia
tigrina
11,640
11,640
11
Gillia
altilis
11,000
11,000
10
Lumbriculus
variegatus
8,417
8,417
9
Pomacea
paludosa
3,198
3,198
8
Chironomus
riparius
450
69.39
7
Chironomus
tentans
10.7
Pteronarcys
californica
25
25
6
Hyalella
azteca
6.51
6.51
5
Gammarus
fasciatus
2.04
5.858
4
Gammarus
pseudolimnaeus
16.82
Simocephalus
serrulatus
1.587
1.587
3
Daphnia
pulex
0.7764
0.9022
2
Daphnia
magna
1.048
Ceriodaphnia
dubia
0.4248
0.4248
1
Table 3. HC05 calculated from the genus-level diazinon invertebrate-only data following the
U.S. EPA (1985) methodology.
N
Rank
(.MAY
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
11
4
5.858
1.768
3.13
0.3333
0.5774
3
1.588
0.462
0.21
0.2500
0.5000
2
0.9022
-0.103
0.01
0.1667
0.4082
1
0.4248
-0.856
0.733
0.0833
0.2887
Sum:
1.27
4.08
0.8333
1.7743
S2 =
79.414
L =
-3.635
A =
-1.642
hc05 =
0.1935
69
-------
Table 4. Summary and comparison of acute values for diazinon.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP
Invertebrate
ALB
(lowest LCso/2)
(Year published,
species)
OWALC (FAV/2)
(Year published, # of
genera, magnitude
relative to ALB)
OW Genus-level
Invertebrate-only
HCos/2
(# of genera, magnitude
relative to ALB)
Notes
Diazinon
0.105 ng/L
(2016; C. dubia)
0.170 ng/L
(2005, 20 genera,
0.61X)
0.097 (ig/L
(11 genera, 1.1X)
C. dubia is the most
sensitive species in the
invertebrate dataset and
FIFRA ALB is based on the
lowest of 24 LC50 values that
comprise the SMAV.
Figure 1 shows a genus-level sensitivity distribution for the diazinon dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the CMC, invertebrate HCos/2, and OPP benchmark values are also included.
70
-------
100,000.00
10,000.00
1,000.00
W> 100.00
c
o
c
10.00
fO
1.00
0.10
•
Arthropod
o
Other Invertebrate
A
Mollusk
¦
Salmonid Fish
~
Other Fish
~
Amphibian
CMC
Genus-level Invertebrate
OPP Invert. Benchmark
OPP Fish Benchmark
~-
(Pteronarcys
~
• Chironomus
Gammarus • • Hyalella
• Simocephalus
• Daphnia
Ceriodaphnia
Lumbriculus .
~ ~
~
Gilia
Dugesia
A
OPP Fish Benchmark = 45 ng/L
»FAV/2 = Criterion Maxmium Concentration = 0.17 pg/L
j^-OPP Invertebrate Benchmark = 0.105 [ig/L
0.01
•Genus-level Invertebrate HC05/2 = 0..0968 pg/L
0.0
0.1
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Diazinon genus-level SD.
Symbols represent GMAVs calculated using all quantitative data from the aquatic life criteria document for diazinon (U.S. EPA
2005), additional data from a 2010 ECOTOX update, and the OPP benchmark document for diazinon (U.S. EPA 2007).
71
-------
1.1.5.2 Diazinon Chronic Toxicity Data
For chemicals lacking sufficient chronic data to satisfy the minimum taxonomic data
requirements, such as diazinon, OW calculates the final chronic value (FCV) as the final acute
value (FAV) divided by the final acute-to chronic ratio (FACR). OPP will also apply ACRs to
acute data for sensitive taxonomic groups to calculate chronic benchmarks when chronic test
data are not available. Calculations of ACRs following OPP and OW methodologies were
conducted, and the effects of these ACRs on the resulting OPP and OW chronic values were
compared.
Data Sources
The data sources for this analysis include data originally reported in the 2005 aquatic life criteria
(ALC) document (U.S. EPA 2005a), supplemented by additional test data from a 2010 ECOTOX
search update for diazinon, as well as additional data obtained from OPP-authored pesticide
effects determination (U.S. EPA 2007) and problem formulation (U.S. EPA 2008) reports.
ACR Calculations
ACR calculations following OW and OPP methodologies are described below. All available
chronic diazinon data are shown in Table 5. All available acute data for species that also have
chronic data are shown in Table 6. Table 7 lists all ACRs by species and calculation method.
ACRs could be calculated for two invertebrate and four fish species following the OW approach,
and for three invertebrate and four fish species following the OPP approach (U.S. EPA 2005b).
Invertebrate ACRs
Ceriodaphnia dubia
The ACR following the OW approach was 1.112, which was the geometric mean of ten acute
values from the same laboratory (nine reported in Norberg-King 1987 and one reported in
Ankley et al. 1991) divided by the MATC from a chronic test performed in the same laboratory
(Norberg-King 1987). The ACR following the OPP approach was 1.709, using the same acute
test data and the NOEC from the paired chronic test.
Daphnia magna
An ACR could not be calculated following the OW approach, because none of the acute tests
were performed in the same laboratory using the same dilution water as any of the chronic tests.
The ACR following the OPP approach was 5.190, which was the geometric mean of the three
acceptable acute values divided by the geometric mean of the two acceptable NOECs.
Americamysis bahia
The ACR following the OW approach was 1.586, which was acute value reported in Nimmo et
al. (1981) divided by the corresponding MATC for the paired chronic test. The ACR following
the OPP approach was 2.295, which was acute value reported in Nimmo et al. (1981) divided by
the corresponding NOEC for the paired chronic test
72
-------
Vertebrate (Fish) ACRs
Salvelinus fontinalis
The ACR following the OW approach was >903.8, which was the geometric mean of three
acceptable acute values reported in Allison and Hermanutz (1977) divided by the paired OW-
calculated NOEC of <0.8 |ig/L. The ACR following the OPP approach was >1,315, which was
the geometric mean of three acceptable acute values reported in Allison and Hermanutz (1977)
divided by the paired OPP-calculated NOEC of <0.55 |ig/L.
Pimephales promelas
In both the OW- and OPP-approaches, two ACRs were calculated using paired data from
Jarvinen and Tanner (1982) and University of Wisconsin-Superior (1988) - Norberg-King
(1989). The final P. promelas ACRs, calculated as the geometric mean of the two paired tests,
was 196.2 following the OW approach and 279.6 following the OPP approach.
Jordanella floridae
The ACR following the OW approach was 23.84, which was the geometric mean of two acute
values reported in Allison (1977) divided by the paired MATC. The ACR following the OPP
approach was 30.43, which was the geometric mean of two acute values reported in Allison
(1977) divided by the paired NOEC.
Cyprinodon variegatus
The ACR following the OW approach was >2,979, which was the Goodman et al. (1979), Mayer
(1987) acute value divided by the OW-calculated paired NOEC of <0.47 |ig/L. The ACR
following the OPP approach was 3,590, which was the Goodman et al. (1979) - Mayer (1987)
acute value divided by the OPP-calculated paired NOEC of 0.36 |ig/L.
Final ACRs
The final ACRs (FACRs) for the two approaches, expressed as the geometric mean of all
available ACRs, is 53.01 following the OW approach, and 50.33 following the OPP approach.
The OW-calculated FACR is larger the OPP FACR because the OPP FACR includes a relatively
small ACR of 5.190 for D. magna that could not be calculated following the OW approach.
When the comparison is limited to those ACRs both approaches have in common, the OPP
FACR is 73.49.
FACRs following both approaches are comprised of two to three relatively small ACRs for
acutely sensitive invertebrate taxa, and four much larger ACRs for acutely insensitive fish
species. The Guidelines (U.S. EPA 1985) specify that if the ACRs appear to increase or decrease
as the species mean acute values (SMAVs) increase, the FACR should be calculated as the
geometric mean for those species whose SMAVs are close to the final acute value (FAV). This is
the case for diazinon, and following the approach used in the 2005 ALC, the FACR is calculated
as the geometric mean of the acutely sensitive invertebrate species. When limited to invertebrate
species, the FACR following the OW approach is calculated as the geometric mean of the ACRs
for C. dubia (1.112) and A. bahia (1.586). Because the final chronic value cannot be larger than
the final acute value, the calculated ACR of 1.328 is rounded up to 2. The invertebrate-only
73
-------
FACR following the OPP approach is the geometric mean of the ACRs for C. dubia (1.709), D.
magna (5.190), and A bahia (2.295), or 2.731.
Comparison of Freshwater Chronic Values for Diazinon
OPP Chronic Benchmarks
For diazinon, the freshwater invertebrate chronic benchmark is 0.17 |ig/L, which is a NOEC
from a registrant submitted test for Daphnia magna (Table 27 in U.S. EPA 2007); and the
freshwater fish chronic benchmark is <0.55 |ig/L, which a NOEC from Allison and Hermanutz
(1977) for Salvelinusfontinalis based on reduced growth (Table 27 in U.S. EPA 2007).
OW Freshwater Chronic Values - All Taxa
Final chronic concentrations following the ACR methodology are calculated by dividing the final
acute value by an ACR. For diazinon, the only available FAV calculated from all taxa is the
FAV of 0.3397 |ag/L reported in the diazinon ALC (U.S. EPA 2005a). The final chronic value
following the OW-ACR approach is 0.1699 ng/L (0.3397 ng/L -h 2), and the final chronic value
following the OPP-ACR approach is 0.1244 ng/L (0.3397 |ag/L 2.731).
OW Freshwater Chronic Values - Invertebrate Taxa
Final chronic concentrations for the invertebrate-only diazinon dataset are calculated by dividing
the final invertebrate acute value by an ACR. This dataset was comprised of acute invertebrate
test data found in the 2005 ALC and the 2010 ECOTOX update. The 2007 and 2008 OPP
documents were also examined but these did not include additional acute invertebrate test data.
The resulting acute HCos calculated from the 11 invertebrate genera using the Guidelines SSD
was 0.1935 ng/L. The final invertebrate chronic value following the OW-ACR approach is
0.09675 |ag/L (0.1935 ng/L -h 2), and the final chronic value following the OPP-ACR approach is
0.07085 |ag/L (0.1935 |ag/L ^ 2.731). Table 8 lists all chronic values calculated following the
different approaches.
74
-------
Table 5. Chronic test data for diazinon.
All concentrations expressed as ng/L. Bolded rows are chronic test results reported by OPP that differ from results reported by OW.
Genus
Species
NOEC
LOEC
MATC
Reference
Test data reported in:
Notes
2005
ALC
2010
ECOTOX
Search
2007
OPP
2008
OPP
Invertebrates
Ceriodaphnia
dubia
0.22
0.52
0.338
Norberg-King 1987
Table 2
X
Daphnia
magna
0.24
0.64
0.392
Biesinger 1973
X
Daphnia
magna
0.17
<0.32
0.233
Surprenant 1988
Table
27
Table 3
Americamysis
bahia
2.1
4.4
3.040
Nimmo et al. 1981
X
Table 3
Vertebrates
Salvelinus
fontinalis
<0.8
0.8
-
Allison and
Hermanutz 1977
Table 2
X
OW calculated value
Salvelinus
fontinalis
<0.55
0.55
-
Allison and
Hermanutz 1977
Table
27
Table 3
OPP calculated value
Pimephales
promelas
50
90
67.08
Jarvinen and Tanner
1982
Table 2
X
Pimephales
promelas
16.5
38
24.97
Norberg-King 1989
Table 2
X
Paired with University of
Wisconsin-Superior 1988
Jordanella
floridae
54
88
68.93
Allison 1977
Table 2
X
Cyprinodon
variegatus
<0.47
0.47
-
Goodman etal. 1979
Table 2
X
OW calculated value
Cyprinodon
variegatus
0.39
0.56
0.47
Goodman et al.
1979
Table 3
OPP calculated value
75
-------
Table 6. Acute diazinon test data for species with chronic test data.
All concentrations expressed as ng/L.
(Ion us
Species
I X 50
or
IX 50
<>\Y-
ACR
Acute
\ :ilue
()l»l»-
ACR
Acute
Ysiliie
Re Terence
lest iliitii reported in:
Notes
2005
Alt
2010
IX ()T()\
200S
()l»l»
Invertebrates
Ceriodaphnia
dubia
0.35
0.3760
0.3760
Norberg-King 1987
Table 1
X
OW, OPP-ACR acute value
Ceriodaphnia
dubia
0.35
Norberg-King 1987
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.25
Norberg-King 1987
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.33
Norberg-King 1987
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.35
Norberg-King 1987
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.59
Norberg-King 1987
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.43
Norberg-King 1987
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.35
Norberg-King 1987
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.36
Norberg-King 1987
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.5
Ankley et al. 1991
Table 1
X
OW, OPP -ACR acute value
Ceriodaphnia
dubia
0.58
Bailey et al. 1997
Table 1
X
Ceriodaphnia
dubia
0.48
Bailey et al. 1997
Table 1
X
Ceriodaphnia
dubia
0.26
Bailey et al. 1997
Table 1
X
Ceriodaphnia
dubia
0.29
Bailey et al. 1997
Table 1
X
Ceriodaphnia
dubia
0.38
Bailey et al. 2001
X
Ceriodaphnia
dubia
0.33
Bailey et al. 2001
X
Ceriodaphnia
dubia
0.45
Banks et al. 2003
X
Ceriodaphnia
dubia
0.21
Banks et al. 2005
X
Table 3
Ceriodaphnia
dubia
0.57
Norberg-King 1987
Table 1
X
Not used to calculate SMAV
Ceriodaphnia
dubia
0.66
Norberg-King 1987
Table 1
X
Not used to calculate SMAV
Ceriodaphnia
dubia
0.57
Norberg-King 1987
Table 1
X
Not used to calculate SMAV
Ceriodaphnia
dubia
>1.0
Norberg-King 1987
Table 1
X
Not used to calculate SMAV
Ceriodaphnia
dubia
>0.6
Norberg-King 1987
Table 1
X
Not used to calculate SMAV
Ceriodaphnia
dubia
0.66
Norberg-King 1987
Table 1
X
Not used to calculate SMAV
Ceriodaphnia
dubia
0.57
Norberg-King 1987
Table 1
X
Not used to calculate SMAV
Ceriodaphnia
dubia
0.66
Norberg-King 1987
Table 1
X
Not used to calculate SMAV
Daphnia
magna
0.96
n/a
1.048
Vilkas 1976
Table 1
X
OPP-ACR acute value
Daphnia
magna
1.5
Dortland 1980
Table 1
X
OPP-ACR acute value
Daphnia
magna
0.8
Ankley et al. 1991
Table 1
X
OPP-ACR acute value
Americamysis
bahia
4.82
4.82
4.82
Nimmo et al. 1981
Table 1
X
OW, OPP-ACR acute value
76
-------
Genus
Species
EC50
or
LC50
ow-
ACR
Acute
Value
OPP-
ACR
Acute
Value
Reference
Test data reported in:
Notes
2005
ALC
2010
ECOTOX
2008
OPP
Americamysis
bahia
4.2
Suprenant 1988
Table 3
Americamysis
bahia
8.5
Thursby and Berry 1988
Table 1
X
Not used to calculate SMAV
Americamysis
bahia
8.5
Cripe 1994
Table 1
X
Not used to calculate SMAV
Vertebrates
Salvelinus
fontinalis
800
723.0
723.0
Allison and Hermanutz 1977
Table 1
X
OW, OPP-ACR acute value
Salvelinus
fontinalis
450
Allison and Hermanutz 1977
Table 1
X
OW, OPP-ACR acute value
Salvelinus
fontinalis
1,050
Allison and Hermanutz 1977
Table 1
X
OW, OPP-ACR acute value
Pimephales
promelas
6,900
6,900
6,900
Jarvinen and Tanner 1982
Table 1
X
OW, OPP-ACR acute value
Pimephales
promelas
9,350
9,350
9,350
University of Wisconsin-
Superior 1988
Table 1
X
OW, OPP-ACR acute value.
Paired with Norberg-King
1989
Pimephales
promelas
6,600
Allison and Hermanutz 1977
Table 1
X
Pimephales
promelas
6,800
Allison and Hermanutz 1977
Table 1
X
Pimephales
promelas
10,000
Allison and Hermanutz 1977
Table 1
X
Pimephales
promelas
4,300
Jarvinen and Tanner 1982
Table 1
X
Not used to calculate SMAV
Pimephales
promelas
2,100
Jarvinen and Tanner 1982
Table 1
X
Not used to calculate SMAV
Pimephales
promelas
10,300
Meier et al. 1979; Dennis et al.
1980
Table 1
X
Not used to calculate SMAV
Jordanella
floridae
1,500
1,643
1,643
Allison 1977
Table 1
X
OW-ACR acute value
Jordanella
floridae
1,800
Allison 1977
Table 1
X
OW-ACR acute value
Cyprinodon
variegatus
1,400
1,400
1,400
Goodman et al. 1979; Mayer
1987
Table 1
X
OW-ACR acute value
77
-------
Table 7. ACI
ts by species and calculation method.
Genus
Species
ACR
Notes
OW-
ACR
OPP-
ACR
Invertebrates
Ceriodaphnia
dubia
1.112
1.709
Daphnia
magna
N/A
5.190
Americamvsis
bahia
1.586
2.295
Vertebrates
Salvelimis
fontinalis
>903.8
>1,315
Pimephales
promelas
196.2
279.6
Value in parentheses used lowest acute flow-through test.
Used in final "All Taxa" calculation.
Jordanella
floridae
23.84
30.43
Cvprinodon
variegatus
>2,979
3,590
All Taxa
53.01
50.33
All Invertebrates (FACR)
1.328
2.731
OW-FACR rounded up to 2.
Table 8. Summary and comparison freshwater chronic values for diazinon.
Magnitude relative to ALB is the OPP ALB/OW value; a ratio < 1 means the OPP ALB value is
lower than the OW value, a ratio >1 means the OPP ALB is higher than the OW value. Note: For
GLI Tier II values, a default ACR of 18 is used when empirically derived ACRs are not
available.
Pesticide
Most Sensitive OPP ALB
(Year published, species)
OWALC
(# of ACRs filled, magnitude
relative to ALB)
OW Invertebrate-only HCos
(# of ACRs filled, magnitude
relative to ALB)
Diazinon
0.17 ng/L
(2016, Daphnia magna)
0.17 ng/L
(ALC, IX)
0.097 (ig/L
(See Table 7 for ACRs, 1.8X)
1.1.5.3 Diazinon References
Allison, D.T. 1977. Use of Exposure Units for Estimating Aquatic Toxicity of Organophosphate
Pesticides. EPA-600/3-77-077, U.S.EPA, Duluth, MN, 25 p. ECOREF#:9931.
Allison, D.T. and R.O. Hermanutz. 1977. Toxicity of diazinon to brook trout and fathead
minnows. PB-269 293 or EPA-600/3-77-060. National Technical Information Service,
Springfield, VA.
Ankley, G.T. and S.A. Collyard. 1995. Influence of piperonyl butoxide on the toxicity of
organophosphate insecticides to three species of freshwater benthic invertebrates. Comp.
Biochem. Physiol. 11OC: 149-155.
Ankley, G.T., J.R. Dierkes, D.A. Jensen and G.S. Peterson. 1991. Piperonyl butoxide as a tool in
aquatic toxicological research with organophosphate insecticides. Ecotoxicol. Environ. Safety
21:266-274.
Bailey, H.C., J.L. Miller, M.J. Miller, L.C. Wiborg, L. Deanovic and T. Shed. 1997. Joint acute
toxicity of diazinon and chlorpyrifos to Ceriodaphnia dubia. Environ. Toxicol. Chem. 16:2304-
2308.
78
-------
Bailey, H.C., J.R. Elphick, R. Krassoi and A. Lovell, A. 2001. Joint acute toxicity of diazinon
and ammonia to Ceriodaphnia dubia. Environ. Toxicol. Chem. 20(12): 2877-2882.
Banks, K.E., S.H. Wood, C. Matthews and K.A. Thuesen. 2003. Joint acute toxicity of diazinon
and copper to Ceriodaphnia dubia. Environ. Toxicol. Chem. 22: 1562-1567.
Banks, K.E., D.H. Hunter and D.J. Wachal. 2005. Diazinon in surface waters before and after a
federally-mandated ban. Sci. Total Environ. 350: 86-93.
Banks, K.E., P.K. Turner, S.H. Wood and C. Matthews. 2005. Increased toxicity to Ceriodaphnia
dubia in mixtures of atrazine and diazinon at environmentally realistic concentrations.
Ecotoxicol. Environ. Safety 60(1): 28-36.
Bathe, R., K. Sachsse, L. Ullmann, W.D. Hormann, F. Zak and R. Hess. 1975a. The evaluation
of fish toxicity in the laboratory. Proc. Eur. Soc. Toxicol. 16:113-124.
Beliles, R. 1965. Diazinon safety evaluation on fish and wildlife: Bobwhite quail, goldfish,
sunfish and rainbow trout. U.S. Environmental Protection Agency, Office of Pesticide Programs
registration standard.
Biesinger, K.E. 1973. The Chronic Toxicity of Some Pesticides to Daphnia magna. Interim Rep.
No. ROAP 16AAK, Task 06, Natl. Water Qual. Lab., Duluth, MN, 5 p. ECOREF#: 117172.
Brooke, L. 1989. Results of Freshwater Exposures with the Chemicals 2,4-D and Diazinon to the
Larval Leopard Frog (Rana pipiens), Juvenile Fathead Minnows (Pimephales promelas), Larval
Midge (Chironomus riparius) and Adult Oligochaete W. February 15th Memo to R.Spehar,
U.S.EPA, Duluth, MN, 6 p.
Call, D.J. 1993. Validation study of a protocol for testing the acute toxicity of pesticides to
invertebrates using the apple snail (Pomacea paludosa). Final Report to U.S. EPA Cooperative
Agreement, No. CR 819612-01.
Ciba-Geigy Corporation. 1976. Reports of investigations made with respect to fish and wildlife
requirements for diazinon and its formualted products. U.S. Environmental Protection Agency,
Office of Pesticide Programs registration standard.
Cope, O.B. 1965a. Contamination of the freshwater ecosystem by pesticides. J. Appl. Ecol.
3 ( Suppl ement): 3 3 -44.
Cripe, G.M. 1994. Comparative Acute Toxicities of Several Pesticides and Metals to Mysidopsis
bahia and Postlarval Penaeus duorarum. Environ. Toxicol. Chem. 13(11): 1867-1872.
doi:10.1002/etc.5620131119. ECOREF#: 13513.
Dennis, W.H., A.B. Rosencrance, W.F. Randall and E.P. Meier. 1980. Acid hydrolysis of
military standard formulations of diazinon. J. Environ. Sci. Health B15:47-60.
Dortland, R.J. 1980. Toxicological evaluation of parathion and azinphosmethyl in freshwater
model ecosystems. Agric. Res. Rep. (Versl. landbouwk. Onderz.) 898:1-112.
Goodman, L.R., D.J. Hansen, D.L. Coppage, J.C. Moore, and E. Matthews. 1979. Diazinon:
Chronic Toxicity to, and Brain Acetylcholinesterase Inhibition in, the Sheepshead Minnow,
Cyprinodon variegatus. Trans. Am. Fish. Soc., 108(5): 479-488. ECOREF#:5604.
79
-------
Hall, L.W. and R.D. Anderson. 2004. Acute Toxicity of Diazinon to the Amphipod, Gammarus
pseudolimnaeus. (Data Report, April 8). University of Maryland, Agricultural Experiment
Station, Queenstown, MD.
Harris, M.L., C.A. Bishop, J. Struger, B. Ripley and J.P. Bogart. 1998. The functional integrity
of northern leopard frog (Rana pipiens) and green frog (Rana clamitans) populations in orchard
wetlands. II. Effects of pesticides and eutrophic conditions on early life stage development.
Environ. Toxicol. Chem. 17:1351-1363.
Jarvinen, A.W. and D.K. Tanner. 1982. Toxicity of selected controlled release and corresponding
unformulated technical grade pesticides to the fathead minnow Pimephales promelas. Environ.
Pollut. (Series A) 27:179-195.
Johnson, W.W. and M.T. Finley. 1980. Handbook of acute toxicity of chemicals to fish and
aquatic invertebrates. Resource Publication 137. U.S. Fish and Wildlife Service, U.S.
Department of Interior, Washington, DC.
Keizer, J., G. D'Agostino and L. Vittozzi. 1991. The importance of biotransformation in the
toxicity of xenobiotics to fish. I. Toxicity and bioaccumulation of diazinon in guppy (Poecilia
reticulata) and zebra fish (Brachydanio rerio). Aquat. Toxicol. 21:239-254.
Mayer, F.L., Jr. 1987. Acute toxicity handbook of chemicals to estuarine organisms. EPA/600/8-
87/017. 274 pp.
Mayer, F.L., Jr. and M.R. Ellersieck. 1986. Manual of acute toxicity: interpretation and data base
for 410 chemicals and 66 species of freshwater animals. Resource Publication No. 160, Fish and
Wildlife Service, U.S. Department of Interior, Washington, DC. 505 p.
Meier, E.P., W.H. Dennis, A.B. Rosencrance, W.F. Randall, W.J. Cooper and M.C. Warner.
1979. Sulfotepp, atoxic impurity in formulations of diazinon. Bull. Environ. Contam. Toxicol.
23:158-164.
Nimmo, D.R., T.L. Hamaker, E. Matthews, and J.C. Moore. 1981. An Overview of the Acute
and Chronic Effects of First and Second Generation Pesticides on an Estuarine Mysid. In: F.J.
Vernberg, A. Calabrese, F.P. Thurberg, and W.B. Vernberg (Eds.), Biological Monitoring of
Marine Pollutants, Academic Press, Inc., NY, 3-19. ECOREF#:4891.
Norberg-King, T.J. 1987. Toxicity Data on Diazinon, Aniline, 2,4-Dimethylphenol. U.S.EPA,
Duluth, MN:11 p. (Memorandum to C.Stephan, U.S.EPA, Duluth, MN; D.Call and L.Brooke,
Center for Lake Superior Environmental Studies, Superior, WI, August 31).
Norberg-King, T.J. 1989. An Evaluation of the Fathead Minnow Seven-Day Subchronic Test for
Estimating Chronic Toxicity. Environ. Toxicol. Chem. 8(11): 1075-1089. ECOREF#:5313.
Phipps, G.L. 1988. Diazinon acute tests for criteria development. (Memorandum to R. Spehar,
U.S. EPA, Duluth, MN. April 29).
Pincetich, C.A. 2004. Metabolic Effects of Pesticide Exposure During Embryogenesis in Medaka
(Oryzias latipes) and Chinook Salmon (Oncorhynchus tshawytscha). Ph.D. Thesis, University of
California, Davis, 139 p.
80
-------
Robertson, J.B. and C. Mazzella. 1989. Acute toxicity of the pesticide diazinon to the freshwater
snail Gillia altilis. Bull. Environ. Contam. Toxicol. 42:320-324.
Sanders, H.O. and O.B. Cope. 1968. The relative toxicities of several pesticides to naiads of
three species of stoneflies. Limnol. Oceanogr. 13:112-117.
Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. 1985.
Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic
Organisms and their Uses. PB85-227049. Office of Research and Development. Duluth, MN,
Narragansett, RI, Corvallis, OR.
Surprenant, D. C. 1988. The Chronic Toxicity of 14C-Diazinon to Daphnia magna Under Flow-
Through Conditions. Report No. 88-4-2644. Conducted by Springborn Life Sciences, Inc.,
Wareham, MA. Submitted by CIBA-GEIGY Corporation, Greensboro, NC. EPA Accession
[MRID] No. 407823-02.
Teh, S.J., G.H. Zhang, T. Kimball and F.C. Teh. 2004. Lethal and sublethal effects of
esfenvalerate and diazinon on splittail larvae. American Fisheries Society Symposium. 2004.
243-253.
Thursby, G.B., and W.J. Berry. 1988. Acute Toxicity of Diazinon to Saltwater Animals. Letter to
J. Scott and D.J. Hansen, Univ. of Rhode Island, Kingston, RI, 10 p. ECOREF#:73146.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2005a. Aquatic life ambient water quality criteria for diazinon. Office of Water. EPA-
822-R-05-006. December 2005.
U.S. EPA. 2005b. Use of acute-to-chronic ratios in support of ecological risk assessment of
pesticides. Memo to Steve Bradbury, Director, Environmental Fate and Effects Division. Office
of Prevention, Pesticides, and Toxic Substances. June 7, 2005.
U.S. EPA. 2007. Risks of diazinon use to the federally listed California red legged frog (Rana
aurora draytonii). Pesticide effects determination. Office of Pesticide Programs. Washington,
D C. 20460. July 20, 2007.
U.S. EPA. 2008. Problem formulation for the environmental fate and ecological risk, endangered
species and drinking water assessments in support of the registration review of diazinon. Office
of Pesticide Programs. Washington, D.C. 20460. March 26, 2008.
U.S. EPA. 2017. Aquatic life benchmarks for pesticide registration. Accessed July 11, 2017.
https://www.epa.gov/pesticide-science-and-assessing-pesticide-risks/aquatic-life-benchmarks-
pesti ci de-regi strati on.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
81
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University of Wisconsin-Superior. 1988. Acute toxicities of organic chemicals to fathead
minnows (Pimephales promelas). Vol. 4. Geiger, D.L., D.J. Call and L.T. Brooke (Eds.). Center
for Lake Superior Environmental Studies, University of Wisconsin-Superior Press, Superior, WI.
355 p.
Viant, M.R., C.A. Pincetich, and R.S. Tjeerdema 2006. Metabolic Effects of Dinoseb, Diazinon
and Esfenvalerate in Eyed Eggs and Alevins of Chinook Salmon (Oncorhynchus tshawytscha)
Determined by 1H NMR Metabolomics. Aquat. Toxicol. 77(4): 359-371.
Vilkas, A. 1976. Acute toxicity of diazinon technical to the water flea, Daphnia magna Straus.
U.S. Environmental Protection Agency, Office of Pesticide Programs registration standard.
82
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1.1.6 Comparison of Aquatic Life Toxicity Values for Chlorpyrifos: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) for chlorpyrifos were obtained from the 1986 OW criteria, which serves
as the base dataset, supplemented with an update to this data from the EPA's ECOTOX
Knowledgebase in 2010, and with additional data reported in the OPP's chlorpyrifos re-
registration eligibility assessment document U.S. EPA (2000). There was no comparative
analysis for chlorpyrifos chronic data.
1.1.6.1 Chlorpyrifos Acute Toxicity Data
Acceptable acute data for chlorpyrifos were obtained from the 1986 criteria, which serves as the
base dataset, supplemented with an update to this data from ECOTOX in 2010, and with
additional LCsos reported in the chlorpyrifos re-registration eligibility assessment document U.S.
EPA (2000). (See Table 1.) Four acute tests were included in U.S. EPA (2000) that were not in
the 2010 ECOTOX update: two LCsos (0.1 |ig/L, 1.7 |ig/L) for Daphnia magna, including the
value upon which the OPP invertebrate benchmark is based; an LCso of 8.2 |ig/L for the stonefly
species Classenia sabulosa, and an LCso of 150 |ig/L for Pimephalespromelas. The C. sabulosa
LCso of 8.2 |ig/L was considered for inclusion but ultimately not included. This was a the 24-hr
LC50 from a test reported in Mayer and Ellersieck (1986) that also reported a 96-hr LC50 of 0.57
|ig/L. The 96-hr LC50 was included in the 2010 ECOTOX update, but not the 24-hr LC50, due to
the shorter exposure duration. Because the 96-hr result from this test was already represented, the
24-hr LC50 of 8.2 |ig/L was not used in this evaluation.
The final dataset consisted of 94 acceptable LCsos for 32 SMAVs and 28 GMAVs, of which 18
SMAVs and 15 GMAVs were for invertebrates. Ranked invertebrate GMAVs are listed in Table
2.
83
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Table 1. Acute toxicity data of chlorpyrifos to freshwater aquatic organisms
()\\
I X 50/
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
MIJR
(ironp'1
(ionus
Species
I X 50
(MU/I-)
Reference
G
Amblema
phcata
1,200
1,200
1,200
Doranetal. 2001
G
Lampsilis
siliquoidea
250
250
250
Bringolf et al. 2007
G
Aplexa
hypnorum
806
806
806
Phipps and Holcombe 1985a; b
D
Ceriodaphnia
dubia
0.06
Bailey et al. 1996
D
Ceriodaphnia
dubia
0.06
Bailey et al. 1996
D
Ceriodaphnia
dubia
0.053
Bailey et al. 1997
D
Ceriodaphnia
dubia
0.055
Bailey et al. 1997
D
Ceriodaphnia
dubia
0.058
Bailey et al. 1997
D
Ceriodaphnia
dubia
0.078
Bailey et al. 1997
D
Ceriodaphnia
dubia
0.058
0.0627
0.0627
Bailey et al. 1997
D
Ceriodaphnia
dubia
0.064
Bailey et al. 1997
D
Ceriodaphnia
dubia
0.066
Bailey et al. 1997
D
Ceriodaphnia
dubia
0.079
Bailey et al. 1997
D
Ceriodaphnia
dubia
0.08
Foster etal. 1998
D
Ceriodaphnia
dubia
0.056
Harmon et al. 2003
D
Ceriodaphnia
dubia
0.050
El-Merhib et al. 2004
D
Ceriodaphnia
dubia
0.07
Pablo et al. 2008
D
Daphnia
ambigua
0.035
0.035
Harmon et al. 2003
D
Daphnia
magna
1.0
Kersting and Van Wijngaarden 1992
D
Daphnia
magna
0.325
Diamantino et al. 1998
D
Daphnia
magna
0.344
Diamantino et al. 1998
D
Daphnia
magna
0.19
0.4811
0.1298
Kikuchi et al. 2000
D
Daphnia
magna
1.074
Gaizick et al. 2001
D
Daphnia
magna
0.74
Palma et al. 2008
D
Daphnia
magna
0.10
MRID 40840902; Burgess 1988
D
Daphnia
magna
1.7
MRID 00102520; McCarthy 1977
D
Simocephalus
vetulus
0.09
0.09
0.09
Pablo et al. 2008
84
-------
()\\
MIJR
(iroup'1
(ionus
Species
I X 50/
I X 50
(MB/I.)
S\1 AY
(M8/U
(IMAY
(MS/'-)
Reference
F
Peltodytes
sp.
0.8
0.8
0.8
Federle and Collins 1976
F
Chironomus
plumosus
1.3
1.3
0.7817
Vedamanikam 2009
F
Chironomus
tentans
0.47
0.47
Ankley and Collyard 1995
F
Classenia
sabulosa
0.57
0.57
0.57
Sanders and Cope 1968; Johnson and Finley 1980;
Mayer and Ellersieck 1986
H
Pteronarcella
badia
0.38
0.38
0.38
Sanders and Cope 1968
H
Pteronarcys
californicus
10
10
10
Sanders and Cope 1968; Johnson and Finley 1980;
Mayer and Ellersieck 1986
E
Gammarus
fasciatus
0.32
0.32
0.1876
Sanders 1972
E
Gammarus
lacustris
0.11
0.11
Sanders 1969; Johnson and Finley 1980; Mayer and
Ellersieck 1986
E
Hyalella
azteca
0.04
0.0908
0.0908
Ankley and Collyard 1995
E
Hyalella
azteca
0.1192
Steevens 1999
E
Hyalella
azteca
0.2191
Steevens 1999
E
Hyalella
azteca
0.0651
Trimble andLydy 2006
E
Orconectes
immunis
6
6
6
Phipps and Holcombe 1985a; b
E
Procambarus
clarkii
21
21
21
Cebrianetal. 1992
E
Eriocheir
sinensis
22.9
63.91
63.91
Li et al. 2006
E
Eriocheir
sinensis
24.4
Li et al. 2006
E
Eriocheir
sinensis
75.9
Li et al. 2006
E
Eriocheir
sinensis
78.50
Li et al. 2006
E
Eriocheir
sinensis
142.2
Li et al. 2006
E
Eriocheir
sinensis
143.9
Li et al. 2006
B
Pimephales
promelas
170
194.1
194.1
Jarvinen and Tanner 1982
B
Pimephales
promelas
130
Jarvinen and Tanner 1982
B
Pimephales
promelas
122.2
Jarvinen et al. 1988
B
Pimephales
promelas
150
MRID 00154732; Jarvinen and Tanner 1982
B
Pimephales
promelas
140
Jarvinen and Tanner 1982; Office of Pesticide
Programs 2000
85
-------
()\\
MIJR
(iroup'1
(ionus
Species
I X 50/
I X 50
(MB/I.)
S\1 AY
(M8/U
(IMAY
(MS/'-)
Reference
B
Pimephales
promelas
120
Jarvinen and Tanner 1982; Office of Pesticide
Programs 2000
B
Pimephales
promelas
203.0
Holcombe et al. 1982; Office of Pesticide Programs
2000
B
Pimephales
promelas
542
Phipps and Holcombe 1985a; b
B
Pimephales
promelas
200
Geigeretal. 1988
B
Pimephales
promelas
506
Geigeretal. 1988
B
Gambusia
affinis
297.6
297.6
297.6
Rao et al. 2005
B
Pungitius
pungitius
4.7
4.7
4.7
Van Wijngaarden et al. 1993
B
Lepomis
macrochirus
2.4
3.281
3.281
Johnson and Finley 1980; Mayer and Ellersieck
1986
B
Lepomis
macrochirus
1.7
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
1.8
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
2.5
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
4.2
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
3
Alexander and Batchelder 1965; Office of Pesticide
Programs 2000
B
Lepomis
macrochirus
5.8
Bowman 1988b; Office of Pesticide Programs 2000
B
Lepomis
macrochirus
10
Phipps and Holcombe 1985a; b
B
Oreochromis
mossambica
4.8
11.12
11.12
Moorthy et al. 1982
B
Oreochromis
mossambica
25.78
Rao 2008
B
Tilapia
zillii
240
240
240
Shereif 1989
A
Oncorhynchus
clarkii
18.4
13.64
11.66
Johnson and Finley 1980
A
Oncorhynchus
clarkii
26
Mayer and Ellersieck 1986
A
Oncorhynchus
clarkii
5.4
Mayer and Ellersieck 1986
A
Oncorhynchus
clarkii
13.4
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
7.1
9.97
Macek et al. 1969; Johnson and Finley 1980; Mayer
and Ellersieck 1986
A
Oncorhynchus
mykiss
15
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
51
Mayer and Ellersieck 1986
86
-------
()\\
MDR
(iroup'1
(ionus
Species
I X 50/
I X 50
(MB/I.)
S\1 AY
(M8/U
(IMAY
(MS/'-)
Reference
A
Oncorhynchus
mykiss
1
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
25
Bowman 1988a; Office of Pesticide Programs 2000
A
Oncorhynchus
mykiss
8.0
Holcombe et al. 1982; Office of Pesticide Programs
2000
A
Oncorhynchus
mykiss
9
Phipps and Holcombe 1985a; b
A
Salvelinus
namaycush
98
150.0
150.0
Johnson and Finley 1980; Mayer and Ellersieck
1986
A
Salvelinus
namaycush
73
Mayer and Ellersieck 1986
A
Salvelinus
namaycush
140
Mayer and Ellersieck 1986
A
Salvelinus
namaycush
205
Mayer and Ellersieck 1986
A
Salvelinus
namaycush
227
Mayer and Ellersieck 1986
A
Salvelinus
namaycush
244
Mayer and Ellersieck 1986
B
Ictalurus
punctatus
280
475.1
475.1
Johnson and Finley 1980; Mayer and Ellersieck
1986
B
Ictalurus
punctatus
806
Phipps and Holcombe 1985a; b
B
Carassius
auratus
806
806
806
Phipps and Holcombe 1985a; b
B
Morone
saxatilis
1,000
1,000
1,000
Office of Pesticide Programs 2000
C
Xenopus
laevis
560
2,701
2,701
Richards 2000; Richards and Kendall 2002
C
Xenopus
laevis
14,600
Richards 2000; Richards and Kendall 2002
C
Xenopus
laevis
2,410
El-Merhibi et al. 2004
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish,
etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
87
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark for chlorpyrifos is 0.05 |ig/L, which is V2 the lowest LC50
for Daphnia magna reported in U.S. EPA (2000).
The OPP fish acute benchmark for chlorpyrifos is 0.9 |ig/L, which is V2 the LC50 of 1.8 |ig/L for
Lepomis macrochirus reported in U.S. EPA (2000).
OW Acute Criterion
The acute criterion, or criterion maximum concentration (CMC), for chlorpyrifos is 0.083 |ig/L
(U.S. EPA 1986). The acute criterion dataset was smaller than the 2010 ECOTOX updated
dataset, and was comprised of 15 total genera, including 8 invertebrate genera.
Genus Level Invertebrate-only HC05
The genus-level invertebrate acute HC05 was calculated following the U.S. EPA (1985)
methodology for the 15 invertebrate genera (Table 2) in the combined chlorpyrifos dataset was
0.0580 |ig/L (Table 3).
Table 2. Chlorpyrifos invertebrate SMAVs and GMAVs (^ig/L).
(Ion us
Species
S.MAN'
CMAY
CMAY kiink
. Imb/cnia
p/icata
1,200
1,200
15
Aplexa
hypnorum
806.0
806.0
14
Eriocheir
sinensis
63.91
63.91
13
Procambarus
clarkii
21.00
21.00
12
Pteronarcys
californicus
10.00
10.00
11
Orconectes
immunis
6.000
6.000
10
Peltodytes
sp.
0.8000
0.8000
9
Chironomus
plumosus
1.300
0.7817
8
Chironomus
tentans
0.4700
Classenia
sabulosa
0.5700
0.5700
7
Pteronarcella
badia
0.3800
0.3800
6
Gammarus
fasciatus
0.3200
0.1876
5
Gammarus
lacustris
0.1100
Daphnia
ambigua
0.0350
0.1298
4
Daphnia
magna
0.4811
Hyalella
azteca
0.0908
0.0908
3
Simocephalus
vetulus
0.0900
0.0900
2
Ceriodaphnia
dubia
0.0627
0.0627
1
88
-------
Table 3. Genus level invertebrate-only acute HCos for chlorpyrifos calculated following the
N
Rank
(.MAY
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
15
4
0.1298
-2.042
4.169
0.2500
0.5000
3
0.0908
-2.399
5.756
0.1875
0.4330
2
0.09
-2.408
5.798
0.1250
0.3536
1
0.0627
-2.769
7.670
0.0625
0.2500
Sum:
-9.618
23.39
0.6250
1.537
S2 =
7.621
L =
-3.465
A =
-2.848
hc05 =
0.0580
Table 4. Summary and comparison of acute values for chlorpyrifos.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP Invertebrate ALB
(lowest LCso/2) (Year published,
species)
OW ALC (FAV/2) (Year
published, # of genera,
magnitude relative to ALB)
OW Genus level
Invertebrate-only HCos/2
(# of genera, magnitude
relative to ALB)
Chlorpyrifos
0.05 ng/L
(2000; D. magna)
0.083 ng/L
(1986 15 genera, 0.60X)
0.029 (ig/L
(15 genera, 1.7X)
Figure 1 shows a genus level sensitivity distribution for the full chlorpyrifos dataset. Major
taxonomic groups are delineated by different symbols, and invertebrate genera are identified by
name. The CMC, OPP acute benchmark values, and genus-level invertebrate only acute HCos/2
are included.
89
-------
10,000.00
1,000.00
100.00
u>
3
«/>
o
>
Q.
i—
o
u
•
Arthropod
o
Mollusk
¦
Salmonid Fish
~
Other Fish
A
Amphibian
Genus-level Invertebrate
OPP Benchmark
CMC
OPP Fish Benchmark
10.00
1.00
0.10
0.01
Amblema
~ o
~
o
~
X
~
¦
Eriocheir •
• Procambarus
~ o
~
Aplexa
Pteronarcys ^ ~ l
Orconectes
~
~
Chironomus
OPP Fish Benchmark = 0.9 pg/L
v - *:
Hyalella
^ *DapP
Classenia * ~ "Peltodytes
• Pteronarcella
Gammarus
Daphnia
Simocephalus
FAV/2 = Criterion Maximum Concentration = 0.083 pg/L
OPP Invertebrate Benchmark = 0.05 pg/L
Genus-level Invertebrate HC05/2 = 0.0290 pg/L
Ceriodaphnia
o.o
o.i
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Chlorpyrifos acute genus-level SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from the chlorpyrifos ALC (U.S. EPA
1986), the Office of Pesticide Program's registration review document for chlorpyrifos (U.S. EPA 2000), and an ECOTOX search
conducted by Office of Water in 2010.
90
-------
1.1.6.2 Chlorpyrifos References
MRID 00102520: McCarty, W.M. 1977. Toxicity of chlorpyrifos to daphnids. Rep. ES-164. The
Dow Chemical Company. Midland, MI.
MRID 00154732: Jarvinen, A.W., and D.K. Tanner. 1982. Toxicity of Selected Controlled
Release and Corresponding Unformulated Technical Grade Pesticides to the Fathead Minnow
Pimephales promelas. Environ. Pollut. A. 27(3): 179-195. doi: 10.1016/0143-1471(82)90024-1.
MRID 40840902: Burgess, D. 1988. Acute flow-through toxicity of chlorpyrifos technical to
Daphnia magna. Report No. 37190. Prepared by Analytical Bio-Chemistry Laboratories, Inc.
Columbia, MO. Submitted by Makhteshim-Agan (America) Inc. New York, NY. Accession No.
408409-02.
Alexander, H.C.; Batchelder, T.L. 1965. Results of a Study on the Acute Toxicity of Dursban®
to Three Species of Fish. (Unpublished study received Jan 11, 1966 under 464-343; submitted by
Dow Chemical U.S.A., Midland, Mich.; CDL:003570-L).
Ankley, G.T., and S.A. Collyard. 1995. Influence of Piperonyl Butoxide on the Toxicity of
Organophosphate Insecticides to Three Species of Freshwater Benthic Invertebrates. Comp.
Biochem. Physiol. C Comp. Pharmacol. Toxicol. 110(2): 149-155.
Bailey, H.C., C. DiGiorgio, K. Kroll, J.L. Miller, D.E. Hinton, and G. Starrett. 1996.
Development of Procedures for Identifying Pesticide Toxicity in Ambient Waters: Carbofuran,
Diazinon, Chlorpyrifos. Environ. Toxicol. Chem. 15(6): 837-845. doi: 10.1002/etc.5620150604.
Bailey, H.C., J.L. Miller, M.J. Miller, L.C. Wiborg, L. Deanovic and T. Shed. 1997. Joint acute
toxicity of diazinon and chlorpyrifes to Ceriodaphnia dubia. Environ. Toxicol. Chem. 16:2304-
2308.
Bowman, J. 1988a. Acute Flow-Through Toxicity of Chlorpyrifos Technical to Bluegill
(Lepomis macrochirus): Project ID:37189. Unpublished study prepared by Analytical Bio-
Chemistry Laboratories, Inc. 188 p.
Bringolf, R.B., W.G. Cope, M.C. Barnhart, S. Mosher, P.R. Lazaro, and D. Shea. 2007. Acute
and Chronic Toxicity of Pesticide Formulations (Atrazine, Chlorpyrifos, and Permethrin) to
Glochidia and Juveniles of Lampsilis siliquoidea. Environ. Toxicol. Chem. 26(10): 2101-2107.
doi:10.1897/06-555R.l.
Cebrian, C., E.S. Andreu-Moliner, A. Fernandez-Casalderrey, andM.D. Ferrando. 1992. Acute
Toxicity and Oxygen Consumption in the Gills of Procambarus clarkii in Relation to
Chlorpyrifos Exposure. Bull. Environ. Contam. Toxicol. 49(1): 145-149.
doi:10.1007/BF00193353.
Diamantino, T.C., R. Ribeiro, F. Goncalves, and A.M.V.M. Soares. 1998. METIER (Modular
Ecotoxicity Tests Incorporating Ecological Relevance) for Difficult Substances. 5. Chlorpyrifos
Toxicity to Daphnia magna in Static, Semi-Static, and Flow-Through Conditions. Bull. Environ.
Contam. Toxicol. 61(4): 433-439. doi:10.1007/s001289900781.
Doran, W.J., W.G. Cope, R.G. Rada, and M.B. Sandheinrich. 2001. Acetylcholinesterase
Inhibition in the Threeridge Mussel (Amblema plicata) by Chlorpyrifos: Implications for
Biomonitoring. Ecotoxicol. Environ. Saf. 49(1): 91-98. doi:10.1006/eesa.2000.2036.
91
-------
El-Merhibi, A., A. Kumar, and T. Smeaton. 2004. Role of Piperonyl Butoxide in the Toxicity of
Chlorpyrifos to Ceriodaphnia dubia and Xenopus laevis. Ecotoxicol. Environ. Saf. 57(2): 202-
212. doi: 10.1016/S0147-6513(03)00082-4.
Federle, P.F., and W.J. Collins. 1976. Insecticide Toxicity to Three Insects from Ohio Ponds.
Ohio J. Sci. 76(1): 19-24.
Foster, S., M. Thomas, and W. Korth. 1998. Laboratory-Derived Acute Toxicity of Selected
Pesticides to Ceriodaphnia dubia. Australas. J. Ecotoxicol. 4(1): 53-59.
Gaizick, L., G. Gupta, and E. Bass 2001. Toxicity of Chlorypyrifos to Rana pipiens Embryos.
Bull. Environ. Contam. Toxicol. 66(3): 386-391. doi:10.1007/s00128-001-0017-y.
Geiger, D.L., D.J. Call, and L.T. Brooke. 1988. Acute Toxicities of Organic Chemicals to
Fathead Minnows (Pimephales promelas) Volume IV. Center for Lake Superior Environmental
Studies, University of Wisconsin, Superior, WI, 4, 355 p.
Harmon, S.M., W.L. Specht, and G.T. Chandler 2003. A Comparison of the Daphnids
Ceriodaphnia dubia and Daphnia ambigua for Their Utilization in Routine Toxicity Testing in
the Southeastern United States. Arch. Environ. Contam. Toxicol. 45(1): 79-85.
doi: 10.1007/s00244-002-0116-8.
Holcombe, G.W., G.L. Phipps and O.K. Tanner. 1982. The acute toxicity of kelthane, Oursban,
disulfoton, pydrin, and permethrin to fathead minnows Pimephales promelas and rainbow trout
Salmo gairdneri. Environ. Pollut. (Ser. A.) 29:167-178.
Johnson, W.W. and M.T. Finley. 1980. Handbook of acute toxicity of chemicals to fish and
aquatic invertebrates. Resource Publication 137.U.S. Fish and Wildlife Service, Washington,
DC. p. 21.
K. Li, L. Q. Chen, E. C. Li and Z. K. Zhou. 2006. Acute Toxicity of the Pesticides Chlorpyrifos
and Atrazine to the Chinese Mitten-handed Crab, Eriocheir sinensis. Bull. Environ. Contam.
Toxicol. 77:918-924.
Kersting, K., and R. Van Wijngaarden (1992). Effects of Chlorpyrifos on a Microecosystem.
Environ. Toxicol. Chem. 11 (3): 365-372. doi:10.1002/etc.5620110310.
Kikuchi, M., Y. Sasaki, and M. Wakabayashi. 2000. Screening of Organophosphate Insecticide
Pollution in Water by Using Daphnia magna. Ecotoxicol. Environ. Saf., 47, (3), 239-245.
doi: 10.1006/eesa.2000.1958.
Macek, K.J., C. Hutchinson and O.B. Cope. 1969. The effects of temperature on the
susceptibility of bluegills and rainbow trout to selected pesticides. Bull. Environ. Contam.
Toxicol. 4:174-183.
Mayer, F.L., Jr., and M.R. Ellersieck.1986. Manual of Acute Toxicity: Interpretation and Data
Base for 410 Chemicals and 66 Species of Freshwater Animals. USDI Fish and Wildlife Service,
Publication No. 160, Washington, DC, 505 p.
Moorthy, M.V., S. Chandrasekhar and V.R. Chandran. 1982. A note on acute toxicity of
chlorpyrifos to the freshwater fish Thilapia mossambica. Pesticides 16:32.
92
-------
Pablo, F., F.R. Krassoi, P.R.F. Jones, A.E. Colville, G.C. Hose, and R.P. Lim. 2008. Comparison
of the Fate and Toxicity of Chlorpyrifos - Laboratory Versus a Coastal Mesocosm System.
Ecotoxicol. Environ. Saf. 71(1): 219-229.
Palma, P., V.L. Palma, R.M. Fernandes, A.M.V.M. Soares, and I.R. Barbosa. 2008. Acute
Toxicity of Atrazine, Endosulfan Sulphate and Chlorpyrifos to Vibrio fischeri, Thamnocephalus
platyurus and Daphnia magna, Relative to Their Concentrations in Surface Waters from the
Alentejo Region of Portugal. Bull. Environ. Contam. Toxicol. 81(5): 485-489.
doi: 10.1007/s00128-008-9517-3.
Phipps, G.L. and G.W. Holcombe. 1985a. A method for aquatic multiple species toxicant testing.
Acute toxicity of 10 chemicals to 5 vertebrates and 2 invertebrates. Environ. Pollut. (Series A)
38:141-157.
Phipps, G.L. and G.W. Holcombe. 1985b. U.S. EPA, Duluth, MM. (Memorandum to C.E.
Stephan, U.S. EPA, Duluth, MH. October 22.
Rao, J. V. 2008. Brain Acetylcholinesterase Activity as a Potential Biomarker for the Rapid
Assessment of Chlorpyrifos Toxicity in a Euryhaline Fish, Oreochromis mossambicus. Environ.
Bioindic. 3(1): 11-22.
Richards, S.M. 2000. Chlorpyrifos: Exposure and Effects in Passerines and Anurans. Ph.D
Thesis, Texas Tech University, Lubbock, TX, 147 p.
Richards, S.M., and R.J. Kendall. 2002. Biochemical Effects of Chlorpyrifos on Two
Developmental Stages of Xenopus laevis. Environ. Toxicol. Chem. 21(9): 1826-1835.
Sanders, H.O. 1969. Toxicity of Pesticides to the Crustacean Gammarus lacustris.
Tech.Pap.No.25, U.S.D.I., Bur. Sports Fish. Wildl., Fish Wildl. Serv., Washington, DC, 18 p.
Sanders, H.O. 1972. Toxicity of some insecticides to four species of malacostracan crustaceans.
Technical Paper No. 66. U.S. Fish and Wildlife Service, Washington, DC.
Sanders, H.O. and O.B. Cope. 1968. The relative toxicities of several pesticides to naiads of
three species of stoneflies. Limnol. Oceanogr. 13:112-117
Shereif, M.M. 1989. Acute and Chronic Effects of Chlorpyrifos on Tilapia zillii. Ph.D. Thesis,
Michigan State University, East Lansing, MI, 114 p.
Steevens, J.A. 1999. Chemical Mixture Interactions: Toxicity of Chlorpyrifos, Dieldrin, and
Methyl Mercury to the Amphipod Hyalella azteca. Ph.D Thesis, University of Mississippi,
University, MS, 183 p.
Trimble, A.J., and M.J. Lydy (2006). Effects of Triazine Herbicides on Organophosphate
Insecticide Toxicity in Hyalella azteca. Arch. Environ. Contam. Toxicol. 51(1): 29-34.
doi: 10.1007/s00244-005-0176-7.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
93
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U.S. EPA. 1986. Ambient water quality criteria for chlorpyrifos - 1986. Office of Water
Regulations And Standards Criteria and Standards Division. Washington, DC. EPA 440/5-86-
005. September 1986.
U.S. EPA 2000. Reregi strati on eligibility science chapter for chlorpyrifos. Fate and
environmental risk assessment chapter. June 2000.
U.S. EPA. 2001. Office of Pesticide Programs Annual Report 2000. Office of Chemical Safety
and Pollution Prevention formerly the Office of Prevention, Pesticides and Toxic Sustances,
Washington DC. EPA 735-R-00-002. August 2001.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
Van Wijngaarden, R., P. Leeuwangh, W.G.H. Lucassen, K. Romijn, R. Ronday, and R. Van der
Velde. 1993. Acute Toxicity of Chlorpyrifos to Fish, a Newt, and Aquatic Invertebrates. Bull.
Environ. Contam. Toxicol. 51(5): 716-723.
Vedamanikam, V.J. 2009. Formation of Resistance in the Chironomus plumosus to Four
Pesticides over 45 Generations. Toxicol. Environ. Chem. 91(1): 187-194.
94
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1.1.7 Comparison of Aquatic Life Toxicity Values for Dichlorvos: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA) (U.S. EPA 2024) for dichlorvos were gathered from the OPP
registration review document for dichlorvos (U.S. EPA 2009) and an EPA ECOTOX
Knowledgebase search conducted in 2013. There was no comparative analysis for dichlorvos
chronic data.
1.1.7.1 Dichlorvos Acute Toxicity Data
Acute data were gathered from the Office of Pesticide Programs (OPP) registration review
document for dichlorvos (U.S. EPA 2009) and an ECOTOX search conducted in 2013 (see Table
1).
The dichlorvos acute dataset consisted of 27 acceptable acute effect LCsos for 15 total species
across 12 genera, of which eight were vertebrate species across six invertebrate genera. Ranked
invertebrate GMAVs are listed in Table 4.
Table 1. Acute toxicity data of dichlorvos to freshwater at
()\\
MI)R
(iroiip-1
(ion us
Species
I X 50/
I X 50
(MS/'-)
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
Reference
G
Lumbriculus
variegatus
2,180
2,180
2,180
Brooke 1991
G
Physa
sp.
170
170
170
Brooke 1991
D
Daphnia
magna
0.266
0.266
0.1333
Brooke 1991
D
Daphnia
pulex
0.0668
0.0668
Mayer and Ellersieck 1986
D
Simocephalus
serrulatus
0.28
0.2698
0.2698
Mayer and Ellersieck 1986
D
Simocephalus
serrulatus
0.26
Mayer and Ellersieck 1986
F
Pteronarcys
californica
0.1
0.1
0.1
Mayer and Ellersieck 1986
E
Gammarus
fasciatus
0.4
0.4
0.4472
Sanders 1972
E
Gammarus
lacustris
0.5
0.5
Mayer and Ellersieck 1986
B
Pimephales
promelas
4,000
5,234
5,234
Pickering and Henderson 1966
B
Pimephales
promelas
11,600
Mayer and Ellersieck 1986
B
Pimephales
promelas
3,090
Brooke 1991
B
Gambusia
affinis
5,270
5,270
5,270
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
869
445.6
445.6
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
480
Cope 1965
B
Lepomis
macrochirus
350
Pickering and Henderson 1966
B
Lepomis
macrochirus
270
Pickering and Henderson 1966
B
Tilapia
mossambica
1,934
1,671
1,671
Rath and Misra 1979
B
Tilapia
mossambica
1,710
Rath and Misra 1979
B
Tilapia
mossambica
1,410
Rath and Misra 1979
A
Oncorhynchus
clarki
170
199.8
141.4
Mayer and Ellersieck 1986
uatic organisms.
95
-------
OW
MIJR
(ironp'1
(ion us
Species
l .( 50/
IX 50
(M8/U
SMAV
(MS/'-)
(IMAY
(MS/'-)
Reference
A
Oncorhynchus
clarki
170
Mayer and Ellersieck 1986
A
Oncorhynchus
clarki
170
Mayer and Ellersieck 1986
A
Oncorhynchus
clarki
213
Mayer and Ellersieck 1986
A
Oncorhynchus
clarki
304
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
100
100
Stalin and Johnson 1977
A
Salvelinus
namaycush
187
185.0
185.0
Mayer and Ellersieck 1986
A
Salvelinus
namaycush
183
Mayer and Ellersieck 1986
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 0.0334 |ig/L, which is V2 of the D. pulex LC50 of
0.0668 |ig/L reported in Mayer and Ellersieck (1986).
The OPP fish acute benchmark is 50 |ig/L, which is V2 of the 0. mykiss LC50 of 100 |ig/L
reported in Stalin and Johnson (1977).
OW Acute Criterion
There is no acute criterion, or criterion maximum concentration (CMC), for dichlorvos. An
illustrative example was calculated for this analysis, using all available data (Table 2). The
illustrative FAV calculated calculated following the U.S. EPA (1985) methodology for the 12
genera in the dichlorvos dataset was 0.06330 |ig/L (Table 3).
Table 2. Dichlorvos Ranked Species Mean Acute Values (SMAV) and Genus Mean Acute
Values (GMAV).
(icmis
Species
SMAV
(Mli/U
(IMAY
(Mli/U
CMAY kiink
(jamb u si a
affinis
s,-"0
s,-"0
i:
Pimephales
promelas
5,234
5,234
11
Lumbriculus
variegatus
2,180
2,180
10
Tilapia
mossambica
1,671
1,671
9
Lepomis
macrochirus
445.6
445.6
8
Salvelinus
namaycush
185.0
185.0
7
Physa
sp.
170.0
170.0
6
Oncorhynchus
clarki
199.8
141.3
5
Oncorhynchus
mykiss
100
96
-------
(Jen lis
Species
S\1 AY
(nii/U
(IMAY
(uii/l.)
(IMAY kiink
Gammarus
fasciatus
0.4000
0.4472
4
Gammarus
lacustris
0.5000
Simocephalus
serrulatus
0.2698
0.2698
3
Daphnia
magna
0.2660
0.1333
2
Daphnia
pulex
0.0700
Pteronarcys
californica
0.1000
0.1000
1
Table 3. Dichlorvos Illustrat
ive FAV/2
.V
Kiink
(;m ay
ln((;\l.\Y)
lii((i MAN )"
P=R/(\+l)
S(|I|(P)
12
4
0.4472
-0.805
0.648
0.3077
0.5547
3
0.2698
-1.310
1.716
0.2308
0.4804
2
0.1333
-2.015
4.061
0.1538
0.3922
1
0.1000
-2.303
5.302
0.0769
0.2774
Sum:
-6.433
11.73
0.769
1.705
s2 =
32.326
L =
-4.031
A =
-2.760
FAV =
0.06330
FAV/2
0.032
Genus Level Invertebrate-only HCos
The genus level invertebrate-only acute HCos calculated following the U.S. EPA (1985)
methodology for the six invertebrate genera (Table 4) in the dichlorvos dataset was 0.04513 |ig/L
(Table 5).
Table 4. Dichlorvos invertebrate SMAVs and GMAVs
(¦onus
Species
SM AY
(IMAY
(i.MAY K;ink
Lumbriculus
variegatus
2,180
2,180
6
Physa
sp.
170.0
170.0
5
Gammarus
fasciatus
0.4000
0.4472
4
Gammarus
lacustris
0.5000
Simocephalus
serrulatus
0.2698
0.2698
3
Daphnia
magna
0.2660
0.1365
2
Daphnia
pulex
0.0668
Pteronarcys
californica
0.1000
0.1000
1
Hg/L)-
97
-------
Table 5. Genus-level invertebrate acute HCos for dichlorvos calculated using following the
U.S. EPA (1985) methodology.
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
6
4
0.4472
-0.805
0.648
0.5714
0.7559
3
0.2698
-1.310
1.716
0.4286
0.6547
2
0.1333
-2.015
4.061
0.2857
0.5345
1
0.1000
-2.303
5.302
0.1429
0.3780
Sum:
-6.433
11.73
1.429
2.323
S2 =
17.406
L =
-4.031
A =
-3.098
hc05 =
0.04513
Table 6. Summary and comparison of acute values for dichlorvos.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(lowest LCso/2) (Year
published, species)
OW Illustrative ALC (FAV/2)
(Year published, # of genera,
magnitude relative to ALB)
OW Genus-level
Invertebrate-only HCos/2
(# of genera, magnitude
relative to ALB)
Dichlorvos
0.0334 ng/L
(2021; D. pulex)
0.032 ng/L
(illustrative example calculated for
this analysis, 12 genera, 1.1X)
0.023 ng/L
(6 genera, 1.5X)
Figure 1 shows a genus level sensitivity distribution for the dichlorvos dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values, illustrative ALC example, and invertebrate-only
acute HC05/2 are included.
98
-------
10,000.00
1,000.00
100.00
QUO
3
(/>
o
>
_o
u
b
10.00
1.00
0.10
o
¦
~
A
Arthropod
Mollusk
Salmonid Fish
Other Fish
Other Invertebrate
FAV/2 = "Criterion Maximum Concentration"
•Genus-level Invertebrate HC05/2
OPP Invertebrate Benchmark
OPP Vertebrate Benchmark
~
~ ~
^ Lumbriculus
~
o
OPP Vertebrate Benchmark = 50 ng/L
• Gammarus
• Simocephalus
Pteronarcys
• Daphnia
OPP Invertebrate Benchmark = 0.035 [ig/L'
0.01
Genus-level Invertebrate FIC05/2 = 0.023 |ig/L '
FAV/2 = "Criterion Maximum Concentration" = 0.032 ng/L
/
0.0
0.1
0.2
0.3
0.4
0.5
0.6
0.7
0.8
0.9
1.0
Sensitivity Centile
Figure 1. Dichlorvos genus-level acute SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from the Office of Pesticide Program's
registration review document for dichlorvos (U.S. EPA 2009) and an ECOTOX search conducted by Office of Water in 2013.
Dichlorvos does not have a recommended 304(a) aquatic life criteria. The "Criterion Maximum Concentration" is an illustrative
example calculated for these analyses.
99
-------
1.1.7.2 Dichlorvos References
Brooke, L.T. 1991. Results of Freshwater Exposures with the Chemicals Atrazine, Biphenyl,
Butachlor, Carbaryl, Carbazole, Dibenzofuran, 3,3'-Dichlorobenzidine, Dichlorvos, 1,2-
Epoxyethylbenzene (Styrene Oxide), Isophorone, Isopropalin, Ox. Center for Lake Superior
Environmental Studies, University of Wisconsin, Superior, WI, 110 p. ECOREF#: 17138.
Cope, O.B. 1965. Sport Fishery Investigations. Fish and Wildlife Service Circular 226, Effects of
Pesticides on Fish and Wildlife. Washington, DC, 51-63. ECOREF#: 2871.
Mayer, F.L., Jr., and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data
Base for 410 Chemicals and 66 Species of Freshwater Animals. USDI Fish and Wildlife Service,
Publication No. 160, Washington, DC, 505 p. ECOREF#: 6797.
Pickering, Q.H., and C. Henderson. 1966. The Acute Toxicity of Some Pesticides to Fish. Ohio
J. Sci., 66, (5), 508-513. ECOREF#: 8096.
Rath, S., and B.N. Misra. 1979. Relative Toxicity of Dichlorvos (DDVP) to Tilapia mossambica,
Peters of 3 Different Age Groups. Exp. Gerontol., 14, 307-309. doi: 10.1016/0531 -
5565(79)90042-1. ECOREF#: 17133.
Sanders, H.O. 1972. Toxicity of Some Insecticides to Four Species of Malacostracan
Crustaceans. Tech. Pap. Bur. Sport Fish. Wildl., 66, 19 p. ECOREF#: 887.
Stalin, A.M. and W.W. Johnson. 1977. Static Toxicity Tests, Fish Toxicity. Pesticide Research
Laboratory, Columbia, MO (undated) (111-39 - 111-44).
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2009. Registration review. Ecological risk assessment problem formulation for:
dichlorvos (DDVP). Office of Pesticide Programs. May 14, 2009.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
100
-------
1.1.8 Comparison of Aquatic Life Toxicity Values for Acrolein: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) for acrolein were obtained from Table 1 of the acrolein freshwater
aquatic life criteria (ALC) document (U.S. EPA 2009a). There was no comparative analysis for
chronic acrolein values.
1.1.8.1 Acrolein Acute Toxicity Data
Acceptable acute data for acrolein were obtained from Table 1 of the acrolein freshwater aquatic
life criteria (ALC) document (U.S. EPA 2009a). Data were available for 36 acute tests
encompassing 15 species and 14 genera. Data for invertebrate taxa were available for 12 acute
tests encompassing seven species and seven genera. The OPP benchmark document (2009b) was
examined to determine whether any additional acute tests were available that were not included
in the criteria document. All values in the OPP benchmark document were included in Table 1 of
the acrolein ALC. Ranked invertebrate GMAVs are listed in Table 2.
Table 1. Acute toxicity da
a of acrolein to freshwater aquatic organisms.
()\\
MIJR
(iroup'1
(ion us
Species
l .( 50/
I X 50
(M8/I-)
S\1 AY
(M8/U
(IMAY
(MJi/l)
Reference
G
Aplexa
hypnorum
>151
>151
>151
Holcomb et al. 1987
G
Physa
heterostropha
368
368
368
Home and Oblad 1983
D
Daphnia
magna
57
61.79
61.79
Maceketal. 1976
D
Daphnia
magna
80
USEPA 1978
D
Daphnia
magna
93
Randall and Knopp 1980
D
Daphnia
magna
83
LeBlanc 1980
D
Daphnia
magna
51
Holcomb et al. 1987
D
Daphnia
magna
<31
Blakemore 1990
E
Gammarus
minus
180
180
180
Home and Oblad 1983
H
Peltoperla
maria
5,920
5,920
5,920
Home and Oblad 1983
F
Chironomus
riparius
510
510
510
Home and Oblad 1983
F
Tanytarsus
dissimilis
>151
>151
>151
Holcomb et al. 1987
A
Oncorhynchus
kisutch
68
68
57.05
Lorz et al. 1979
A
Oncorhynchus
mykiss
74
47.86
Birge et al. 1982
A
Oncorhynchus
mykiss
180
Home and Oblad 1983
A
Oncorhynchus
mykiss
38
Venturino et al. 2007
A
Oncorhynchus
mykiss
<31
Bowman 1990a
A
Oncorhynchus
mykiss
16
Holcomb et al. 1987
B
Pimephales
promelas
320
35.79
35.79
Union Carbide Corp. 1974
B
Pimephales
promelas
45
Birge et al. 1982
B
Pimephales
promelas
14
Geigeretal. 1986
B
Pimephales
promelas
19.5
Geigeretal. 1986
B
Pimephales
promelas
61
Birge et al. 1982
101
-------
OW
MIJR
Group-'
(ion us
Species
IX 50/
I X 50
(Mii/U
S\1 AY
(M8/U
GMAY
(MS/'-)
Reference
B
Pimephales
promelas
29.7
Sabourin 1986
B
Pimephales
promelas
27
Spehar 1989
B
Pimephales
promelas
14
Holcometal. 1987
B
Catostomus
commersoni
14
14
14
Holcomb et al. 1987
B
Jordanella
floridae
60
55.32
55.32
Spehar 1989
B
Jordanella
floridae
51
Spehar 1989
B
Lepomis
macrochirus
100
56.94
56.94
Louder and McCoy 1962
B
Lepomis
macrochirus
90
USEPA 1978
B
Lepomis
macrochirus
90
Buccafusco et al. 1981
B
Lepomis
macrochirus
33
Holcomb et al. 1987
B
Lepomis
macrochirus
22.4
Bowman 1990b
B
Micropterus
salmoides
160
160
160
Louder and McCoy 1962
C
Xenopus
laevis
7
7
7
Holcomb et al. 1987
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark for acrolein is <15.5 |ig/L, which is V2 the lowest LC50
for Daphnia magna. This is also the lowest LC50 for D. magna reported in Table 1 of the ALC
document.
The OPP vertebrate acute benchmark for acrolein is 3.5 |ig/L, which is V2 the lowest LC50 for the
African clawed frog, Xenopus laevis.
OW Acute Criterion
The criterion maximum concentration (CMC) for acrolein is 3.0 |ig/L.
Genus Level Invertebrate-only HC05
The genus level invertebrate-only acute HC05 calculated following the U.S. EPA (1985)
methodology for the seven invertebrate genera (Table 2) in the acrolein dataset was 45.74 |ig/L
(Table 3).
Table 2. Acrolein Invertebrate SMAVs and GMAVs (^ig/L).
Genus
Species
SMAV
GMAV
GMAV Rank
Tallaperla"
maria
5,920
5,920
7
102
-------
Genus
Species
SMAV
GMAV
GMAV Rank
Chironomus
ripar ins
510.0
510.0
6
Phvsa
heterostropha
368.0
368.0
5
Gammarus
minus
180.0
180.0
4
Aplexa
hvpnorum
151.0
151.0
3
Tanvtarsus
dissimilis
151.0
151.0
2
Daphnia
magna
61.79
61.79
1
a - Genus changed from Peltoperla
Table 3. Genus level invertebrate-only acute HCos for acrolein calculated following the U.S.
EPA (1985) methodology.
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
7
4
180
5.193
26.97
0.5000
0.7071
3
151
5.017
25.17
0.3750
0.6124
2
151
5.017
25.17
0.2500
0.5000
1
61.79
4.124
17.01
0.1250
0.3536
Sum:
19.35
94.3
1.250
2.173
S2 =
10.08
L =
3.113
A =
3.823
hc05 =
45.74
Table 4. Summary and comparison of acute values for acrolein.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates the OPP value is hig
ier than the OW value.
Pesticide
OPP Most Sensitive ALB
(lowest LCso/2) (Year
published, species)
OW ALC (FAV/2)
(Year published, # of
genera, magnitude relative
to ALB)
OW Genus-level Invertebrate-
only HCos/2
(# of genera, magnitude relative
to ALB)
Acrolein
(contact
herbicide)
3.5 ng/L
(2023; Xenopus laevis)
3.0 ng/L
(2009, 14 genera, 1.2X)
22.87 ng/L
(7 genera, 0.68X)
Note the magnitude comparison is
with the invertebrate ALB of
<15.5 ng/L.
Figure 1 shows a genus-level sensitivity distribution for the full acrolein dataset. Major
taxonomic groups are delineated by different symbols, and invertebrate genera are identified by
name. The CMC, OPP invertebrate and vertebrate acute benchmark values, and invertebrate-only
acute HC05/2 are included.
103
-------
10,000
1,000
bO
3
c
Jj
o
k_
u
<
100
•
Arthropod
o
Mollusk
¦
Salmonid Fish
~
Other Fish
A.
Amphibian
Genus-level Invertebrate
OPP Invert. Benchmark
CMC
OPP Vertebrate Benchmark
Peltoperla •
• Chironomus
~
~
Tanytarsus • o
Aplexa
• Daphnia
~
O Physa
• Gammarus
~
Genus-level invertebrate HC05/2= 22.87 |ig/L
~
10
OPP Invertebrate Benchmark = <15.5 |ig/L
OPP Vertebrate Benchmark = 3.5 |ig/L
FAV/2 = Criterion Maximum Concentration = 2.96 |ig/L
0.0
0.1
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Acrolein genus-level acute SD.
Symbols represent GMAVs calculated using all available data from Table 1 of the 2009 acrolein ALC.
104
-------
1.1.8.2 Acrolein References
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2009a. Ambient aquatic life water quality criteria for acrolein. Office of Water.
Washington D.C. EPA 822R0819. July 1, 2009.
U.S. EPA. 2009b. Environmental fate and ecological risk assessment for the reregi strati on of
acrolein. Office of Pesticide Programs. Washington, D.C. 20460.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
105
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1.2 Data-Limited Pesticides
1.2.1 Comparison of Aquatic Life Toxicity Values for Oxamyl: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) are described below. Toxicity data for oxamyl were gathered by OW in
2015 and combined with data from OPP's registration review document for oxamyl (U.S. EPA
2009).
1.2.1.1 Oxamyl Acute Toxicity Data
The oxamyl acute data include nine LCsos representing six species in six genera that were
classified as "quantitative" data, and two 96-hour LCsos for the amphipod species Gammarus
italicus and Echinogammarus tibaldii (classified as qualitative, but included in this analysis to
increase the number of invertebrate genera to four), thereby enabling calculation of an
invertebrate only genus-level HCos. Tests were classified as qualitative because both the G.
italicus andE. tibaldi studies were conducted with field-collected organisms, and the G. italicus
study was not replicated.
The final acute oxamyl dataset consisted of 11 LCsos for eight species across eight genera, of
which four were invertebrate species and four were invertebrate genera. Acute data for oxamyl
are shown in Table 1. Ranked invertebrate GMAVs are listed in Table 2.
106
-------
Table 1. Acute toxicity of oxamyl to freshwater aquatic organisms.
()\\
MDR
(iroup1
(Ionus
Species
IX 50/
I X 50
(Mli/U
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
Reference
Comment
D
Daphnia
magna
320.0
387.8
387.8
MRID 45067801; Boeri and Ward. 2000
Quantitative
D
Daphnia
magna
470.0
ECOTOX 6797; Mayer and Ellersieck. 1986
Quantitative
F
Chironomus
plumosus
180.0
180.0
180.0
ECOTOX 6797; Mayer and Ellersieck. 1986
Quantitative
E
Echinogammarus
tibaldii
297.0
297.0
297.0
ECOTOX 18621; Pantani et al. 1997
Qualitative
E
Gammarus
italicus
217.8
217.8
217.8
ECOTOX 18621; Pantani et al. 1997
Qualitative
B
Carassius
auratus
27,500
27,500
27,500
MRID 66915; Knott and Johnston. 1969
Quantitative
C
Lepomis
macrochirus
5,600
7,483
7,483
MRID 66914; Knott and Johnston. 1969
Quantitative
C
Lepomis
macrochirus
10,000
ECOTOX 6797; Mayer and Ellersieck. 1986
Quantitative
A
Oncorhynchus
mykiss
4,200
4,200
4,200
MRID 66916; Knott and Johnston. 1969
Quantitative
A
Oncorhynchus
mykiss
4,200
ECOTOX 6797; Mayer and Ellersieck. 1986
Quantitative
B
Ictalurus
punctatus
19,400
19,400
19,400
ECOTOX 6797; Mayer and Ellersieck. 1986
Quantitative
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish,
etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
107
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark for oxamyl is 90 |ig/L, which is V2 of the Chironomus
plumosus acute effect LC50 of 180 |ig/L.
The OPP fish acute benchmark is 2,100 |ig/L, which is V2 of one of the two Oncorhynchus
mykiss acute LC50S of 4,200 |ig/L.
GLI Tier II Acute Value Calculation
The acceptable dataset for oxamyl fulfills six of the eight OW MDRs, corresponding to the use
of a Secondary Acute Factor (SAF) of 5.2. Applying the SAF to the lowest (most sensitive)
GMAV (i.e., 180 |ig/L for midge (Chironomuspulmosus)) yields the calculated Secondary Acute
Value (SAV) of34.6 |ig/L. Half of the SAV is 17.3 |ig/L.
Detailed calculations are shown below:
SAV =
Lowest GMAV
SAF
180
SAV = — = 34.6 |xg/L
SMC =
5.2
SAV
34.6
SMC =—-= 17.3 \ig/L
Genus-Level Invertebrate-only HC05
The genus level invertebrate-only acute HC05 calculated following the U.S. EPA (1985)
methodology for the four invertebrate genera in the oxamyl dataset (Table 2) is 114.7 |ig/L
(Table 3).
Table 2. Oxamyl invertebrate SMAVs and GMAVs (ng/L).
(Ion us
Species
S\1 AY
(IMAY
CMAY kiink
Daphnia
magna
387.8
387.8
4
Echinogammarus
tibaldii
297.0
297.0
3
Gammarus
italicus
217.8
217.8
2
Chironomus
plumosus
180.0
180.0
1
Note: The G. italicus and E. tibaldii GMAVs are based on data classified as qualitative that were included to allow
for sufficient sample size to calculate an invertebrate genus-level HC05.
108
-------
Table 3. Genus-level invertebrate-only acute HCos for oxamyl calculated following the U.S.
EPA (1985) methodology.
N
Rank
(.MAY
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
s qrt(P)
4
4
387.8
5.961
35.53
0.8000
0.8944
3
297
5.694
32.42
0.6000
0.7746
2
217.8
5.384
28.98
0.4000
0.6325
1
180
5.193
26.97
0.2000
0.4472
Sum:
22.23
123.9
2.000
2.749
S2 =
3.095
L =
4.349
A =
4.742
hc05
114.7
Table 4. Comparison of acute values for oxamyl.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP
Invertebrate
ALB
(lowest LCso/2)
(Year published,
species)
OW GLI Tier
II value (# of
MDRs filled,
magnitude
relative to
ALB)
OW Genus-level
Invertebrate-only
HCos/2
(# of genera,
magnitude relative
to ALB)
Notes
Oxamyl
90 (ig/L
(2016;
Chironomus
plumosus)
17.3 ng/L
(6 MDRs filled,
5.2X)
57.35 (ig/L
(4 genera*, 1.6X)
* Two GMAVs included are
based on data classified as
qualitative were included to
allow for sufficient sample size
to calculate an invertebrate
genus-level HCos. Tests were
classified as qualitative because
they were conducted with field-
collected organisms.
Figure 1 shows a genus-level sensitivity distribution for the oxamyl dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values, GLI Tier II calculated acute value, and invertebrate-
only acute HC05/2 are included.
109
-------
100,000
10,000
• Arthropod
O Arthropod (Qualitative)
¦ Salmonid Fish
~ Other Fish
GL1 Tier II Acute Value
Genus-level Invertebrate
OPP Invertebrate Benchmark
— * • OPP Fish Benchmark
1,000
W
=L
>
E
s
o
100
10
0.0
OPP Fish Benchmark = 2,100 pg/L
• Chironomus
O Gammarus
• Daphnia
° Echinogammarus
OPP Invertebrate Benchmark = 90 pg/L
Genus-level Invertebrate HCO5/2 = 57.35 pg/L
GLI Tier II Acute Value = 17.3 pg/L
0.1
0.2
0.3
0.4
0.5
0.6
0.7
0.8
0.9
1.0
Sensitivity Centile
Figure 1. Oxamyl genus-level acute SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from an EPA literature search in 2015,
supplemented the Office of Pesticide Programs (OPP) registration review document for oxamyl (U.S. EPA 2009).
110
-------
1.2.1.2 Oxamyl Chronic Toxicity Data
Chronic Data Sources and Considerations
Chronic toxicity data for oxamyl were consolidated by OW in 2015 and combined with data
from OPP's registration review document for oxamyl (U.S. EPA 2009). The final chronic
oxamyl dataset consisted of three NOECs/LOECS for three species across three genera, of which
one was an invertebrate genus and two were vertebrate genera (Table 5).
Table 5. Chronic toxicity data of oxamyl to freshwater aquatic organisms.
OW
MIJR
(i rou p'1
(Ionus
Species
NOW
(MS/'-)
I.OKC
(MS/I-)
Lnclpoint
Reference
Comment
D
Daphnia
magna
27
50
Growth (adult length),
time to first brood and
number of offspring
MRID 45067801;
Boeri and Ward.
2000
Acceptable
A
Oncorhynchus
mykiss
770
1,500
Embryo hatching and
larval swim-up
MRID 40901101;
Hutton. 1988
Acceptable
B
Pimephales
promelas
500
1,000
Larval survival
MRID 94663;
Muska and Driscoll.
1982
Acceptable
t MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark for oxamyl is 27 |ig/L, which is the NOEC for
Daphnia magna. The OPP fish chronic benchmark is 500 |ig/L, which is the NOEC for
Pimephales promelas.
GLI Tier II Chronic Value Calculation
Per the 1985 Tier I Guidelines, ACRs can be calculated for a given species only if the acute and
chronic studies were conducted in the same laboratory and using test water of the same physical
and chemical characteristics. The OW approach for calculating an ACR involves the use of the
MATC, which is the geometric mean of the NOAEC and LOAEC obtained from the chronic
tests for that species. Only one ACR (for the water flea, Daphnia magna) could be calculated
using the OW approach because the chronic study for rainbow trout (iOncorhynchus mykiss) was
not performed in the same laboratory or with water of the same physical characteristics as the
water used in the analogous acute test. Per the GLI Tier II methodology, the default ACR value
of 18 was used for the remaining two ACRs.
Ill
-------
Detailed calculations for the SC V are shown below:
= Geometric Mean of the ACRs
= V8.71 * 18 * 18 = 14.1
SACR
34.6
iU = 24 w/l
Table 6. Comparison of chronic values for oxamyl.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OWGLI Tier II value
(# of ACRs filled,
magnitude relative to ALB)
OW Invertebrate-only
HCos
(# of ACRs filled,
magnitude relative to
ALB)
Notes
Oxamyl
27 (ig/L
(2016; Daphnia
magna)
2.4 (ig/L
(GLI Tier II; 1 ACR, 11X)
NA
Two default ACRs
of 18 used to derive
GLI Tier II value
1.2.1.3 Oxamyl References
ECOTOX 18621. Pantani, C., Pannunzio, G., De Cristofaro, M., Novelli, A. A., and Salvatori,
M. 1997. Comparative Acute Toxicity of Some Pesticides, Metals, and Surfactants to Gammarus
italicus Goedm. and Echinogammarus tibaldii Pink, and Stock (Crustacea: Amphipoda). Bull.
Environ. Contam. Toxicol. 59: 963-967.
ECOTOX 6797. Mayer, F. L. J., and Ellersieck, M. R. 1986. Manual of Acute Toxicity:
Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals. Resour.
Publ. No. 160, U.S. Department of Interior, Fish and Wildlife Services, Washington, DC 505 p.
MRID 40901101. Hutton, D. 1988. Early Life Stage Toxicity of IN D1410-196 (Oxamyl) to
Rainbow Trout: Medical Research Project No. 4581-573: Haskell Laboratory Report No. 468-88.
Unpublished study prepared by E. I. du Pont de Nemours and Co., Inc. 24 p.
MRID 45067801. Boeri, R., and Ward, T. 2000. Oxamyl Technical: 21-Day Chronic, Flow-
Through Toxicity to Daphnia magna: Lab Project Number: 3 10: 1757-DU: 2554. Unpublished
study prepared by T.R. Wilbury Labs. 60 p.
MRID 66914. Knott, W. B., and Johnston, C. D. 1969. Insecticide 1410: Evaluation of Acute
LC150A for Bluegill Sunfish. (Unpublished study received Nov 29, 1972 under 361316;
prepared by Woodard Research Corp., submitted by E.I. du Pont de Nemours & Co., Inc.,
Wilmington, Del.; CDL:092249-AA).
SACR :
SACR :
SCV =
SCV =
112
-------
MRID 66915. Knott, W. B., and Johnston, C. D. 1969. Insecticide 1410: Evaluation of Acute
LC150A for Goldfish. (Unpublished study received Nov 29, 1972 under 3G1316; prepared by
Woodard Research Corp., submitted by E.I. du Pont de Nemours & Co., Inc., Wilmington, Del.;
CDL: 092249-AB).
MRID 66916. Knott, W. B., and Johnston, C. D. 1969. Insecticide 1410: Evaluation of Acute
LC150A for Rainbow Trout. (Unpublished study received Nov 29, 1972 under 3613 16;
prepared by Woodard Research Corp., submitted by E.I. du Pont de Nemours & Co., Inc.,
Wilmington, Del.; CDL:092249-AC).
MRID 94663. Muska, C.F., and Driscoll, R.R. 1982. Early Life Stage Toxicity of Oxamyl to
Fathead Minnow: Haskell Laboratory Report No. 877-81. (Unpublished study received Jan 29,
1982 under 352-372; submitted by E.I. du Pont de Nemours & Co., Inc., Wilmington, Del.;
CDL:246726-D).
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2009. Risks of oxamyl use to federally threatened California red-legged frog (Rana
aurora draytonii). Office of Pesticide Programs. Washington, D.C. February 12, 2009.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
113
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1.2.2 Comparison of Aquatic Life Toxicity Values for Acephate: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) are described below. Toxicity data for acephate were gathered by OW
in 2015 and combined with data from OPP's registration review document for acephate (U.S.
EPA 2007).
1.2.2.1 Acephate Acute Toxicity Data
The acephate data include twelve LCsos representing seven species in seven genera that were
classified as "quantitative" data and twenty-six LCsos representing eight species in eight genera
classified as "qualitative" that appear to be acceptable tests given the available information. The
final acute acephate dataset consisted of 45 LCsos for 18 total species across 16 genera, of which
seven were invertebrate species across seven invertebrate genera. Ranked invertebrate GMAVs
from all data sources are listed in Table 2. Acute data for acephate are shown in Table 1.
114
-------
Table 1. Acute toxicity of acephate to freshwater aquatic organisms.
()\\
MIJR
(iroup'1
(Ionus
Species
IX 50/
IX 50
(Mli/U
S\1 AY
(MS/I-)
(IMAY
Reference
Comment
F
Ephemeridaeb
-
3,136
3,136
3,136
ECOTOX 37219. Hussain et al.
1985
24hr. No species name
F
Pteronarcella
badia
21,200
10,883
10,883
ECOTOX 6797. Mayer and
Ellersieck. 1986
F
Pteronarcella
badia
6,400
ECOTOX 6797. Mayer and
Ellersieck. 1986
F
Pteronarcella
badia
9,500
ECOTOX 6797. Mayer and
Ellersieck. 1986
F
Isogenus
sp.
11,700
11,700
11,700
ECOTOX 6797. Mayer and
Ellersieck. 1986
F
Skwala
sp.
12,000
12,000
12,000
MRID 40094602. Johnson, W. and
M. Finley. 1980
D
Daphnia
magna
71,800
8,927
8,927
MRID 00014565. Wheeler. 1978.
D
Daphnia
magna
1,110
MRID 40098001. McCann 1978
OPP Benchmark value,
75% formulation
E
Gammarus
pseudolimneaus
>50,000
>62,996
>62,996
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
E
Gammarus
pseudolimneaus
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
E
Gammarus
pseudolimneaus
>100,000
Schotteger 1970
F
Chironomus
plumosus
>1,000,000
>135,721
>135,721
Johnson and Finley 1980
No endpoint or duration
reported
F
Chironomus
plumosus
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
48hr EC50
F
Chironomus
plumosus
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
A
Oncorhynchus
mykiss
110,000
530,010
>185,523
ECOTOX 6797. Mayer and
Ellersieck. 1986
A
Oncorhynchus
mykiss
1,100,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
A
Oncorhynchus
mykiss
783,840
ECOTOX 7317. Duangsawasdi.
1977.
115
-------
()\\
MIJR
(iroup'1
(Ionus
Species
IX 50/
IX 50
(MS/1-)
S\1 AY
(IMAY
(MS/'-)
Reference
Comment
A
Oncorhynchus
mykiss
832,000
MRID 40094602. Johnson, W. and
M. Finley. 1980
OPP Benchmark value
A
Oncorhynchus
clarkii
>50,000
>64,940
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Oncorhynchus
clarkii
>60,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Oncorhynchus
clarkii
>100,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Oncorhynchus
clarkii
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Oncorhynchus
clarkii
>100,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Oncorhynchus
clarkii
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salmo
salar
>50,000
>50,000
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salmo
salar
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salmo
salar
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salmo
salar
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salmo
salar
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salmo
salar
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salmo
salar
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salmo
salar
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salvelinus
fontinalis
>50,000
>70,711
>70,711
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
A
Salvelinus
fontinalis
>100,000
MRID 40094602. Johnson, W. and
M. Finley. 1980
Qualitative
B
Lepomis
macrochirus
>50,000
>91,028
>91,028
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
116
-------
()\\
MDR
(iroup'1
(Ionus
Species
IX 50/
IX 50
(MS/1-)
S\1 AY
(IMAY
(MS/'-)
Reference
Comment
B
Lepomis
macrochirus
>1,000,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
B
Lepomis
macrochirus
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
B
Lepomis
macrochirus
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
B
Lepomis
macrochirus
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
B
Ictalurus
punctatus
>1,000,000
>1,000,000
>1,000,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
B
Perca
flavescens
>50,000
>50,000
>50,000
ECOTOX 6797. Mayer and
Ellersieck. 1986
Qualitative
B
Pimephales
promelas
>1,000,000
>1,000,000
>1,000,000
MRID 40094602 Johnson 1980
C
Amby stoma
gracile
8,816,000
8,816,000
8,816,000
Geen 1984
C
Rana
catesbelana
>5,000
>5,000
>179,346
MRID 44042901. Hall & Kolbe.
1980
Qualitative
C
Rana
clamitans
6433000
6,433,000
Lyons et al. 1976
24hr, 90% formulation
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented,
b No species name provided; only Family provided
117
-------
OPP Acute Benchmark Values
The invertebrate OPP acute benchmark is 550 ng/L, which is V2 of the D. magna LC50 of 1,110
|ig/L cited in U.S. EPA (2007). The fish OPP acute benchmark is 416,000 ng/L, which is V2 of an
O. mykiss LC50 of 832,000 |ig/L cited in U.S. EPA (2007).
GLI Tier II Acute Value Calculation
The acceptable acute dataset for acephate fulfills seven of the eight MDRs, corresponding to the
use of a Secondary Acute Factor (SAF) of 4.3. Applying the SAF to the lowest, most sensitive
GMAV (i.e., 3,136 |ig/L for mayfly (Ephemeridae family)), the calculated Secondary Acute
Value (SAV) is 729.3 |ig/L. The Secondary Maximum Criterion (SMC), which is calculated as
half the SAV, is 364.7 |ig/L. Detailed calculations for the SMC are shown below:
Lowest GMAV
3,136
SAV = = 729.3 ag/L
4.3
SAV
SMC= —
729.3
SMC = —= 364.7 |xg/L
Genus-Level Invertebrate-only HC05
The genus-level invertebrate acute HC05 following the U.S. EPA (1985) methodology for the
seven invertebrate genera in the acephate dataset (Table 2) was 2,138 |ig/L (Table 3). The second
most sensitive GMAV is for Daphnia and includes the OPP benchmark LC50 of 1,110 ng/L
tested in a 75% formulation. Excluding the OPP acute benchmark LC50 above yields a genus-
level invertebrate HC05 of 2,117 |ig/L, calculated entirely from quantitative data.
Table 2. Acephate invertebrate SMAVs and GMAVs (ng/L).
(Ion us
Species
S\1 AY
GMAV
(iMAY kiink
Chironomus
plumosus
>135,721d
>135,72 ld
7
Gammarus
pseudolimneaus
>62,996°
>62,996°
6
Skwala
sp.
12,000
12,000
5
Isogenus
sp.
11,700
11,700
4
Pteronarcella
badia
10,883
10,883
3
Daphnia
magna
8,927b
8,927b
2
Ephemeridae"
-
3,136
3,136
1
a Family. Species name not reported.
b Geometric mean of quantitative value and OPP invertebrate benchmark value from test with 75% formulation,
c Geometric mean of two qualitative values from U.S. EPA (2015) and third value from U.S. EPA (2007).
d Geometric mean of three values from U.S. EPA (2007).
118
-------
Table 3. Genus-level invertebrate acute HCos for acephate calculated following the U.S.
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
1
4
11,700
9.367
87.75
0.5000
0.7071
3
10,833
9.290
86.31
0.3750
0.6124
2
8,927
9.097
82.75
0.2500
0.5000
1
3,136
8.051
64.81
0.1250
0.3536
Sum:
35.81
321.6
1.250
2.173
S2 =
16.12
L =
6.770
A =
7.668
FAV =
2,138
Table 4. Comparison of acute values for acephate.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP Invertebrate
ALB
(lowest LCso/2)
(Year published,
species)
OW GLI Tier
II value (# of
MDRs filled,
magnitude
relative to
ALB)
OW Genus-level
Invertebrate-
only HCos/2
(# of genera,
magnitude
relative to ALB)
Notes
Acephate
550 ng/L
(2007; Daphnia
magna)
364.7 ng/L
(7 MDRs filled,
1.5X)
1,069 ng/L
(7 genera, 0.5 IX)
The FIFRA ALB was based on an acute
toxicity test that used 75% pure acephate
in a wettable powder formulation,
producing an EC50 value of 1,100 |ig/L for
water flea (I). magna). This acute toxicity
test was not used in the GLI Tier II
because the chemical purity was <90%.
Figure 1 shows a genus-level sensitivity distribution for the acephate dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values, GLI Tier II calculated value and invertebrate-only
acute HC05/2 are also included.
119
-------
10,000,000
1,000,000
100,000
CUD
H.10,000
01
re
Q. 1,000
01
u
<
100
10
0.0
o
¦
~
~
o
A
Arthropod
Arthropod (Qualitative)
Salrnonid Fish
Salmonid Fish (Qualitative)
Other Fish
Other Fish (Qualitative)
Amphibian
¦ Genus-level arthropod
OPP Invertebrate Benchmark
¦ OPP Fish Benchmark
Tier II Acute Value
~
O — 1=1
Gamma rus
Chironomusb
Daphnia3
• __ • Skwala
^"•Isogenus
O Ephermeridae Pteronarcella
(Family)
Genus-level invertebrate FIC05/2= 1,069 ng/L
OPP Invertebrate Benchmark = 550 ng/L
GLI Tier II = 364.7 ng/L
Notes:
a - Geometric mean of quantitative LC50 and an LC50 for a 70% formulation
used as the invertebrate benchmark value,
b - Listed in OPP benchmark document but not in the Tier II benchmark document,
c - Geometric mean of R. catesbelanaqualitative SMAVand
R. clamitans SMAV representing as the OPP amphibian benchmark,
d - Geometric mean of quantitative SMAV for O. mykiss and
0.1
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Acephate genus-level acute SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from an EPA literature search in 2015,
supplemented the Office of Pesticide Programs (OPP) registration review document for acephate (U.S. EPA 2007).
120
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1.2.2.2 Acephate Chronic Toxicity Data
Chronic Data Sources and Considerations
Chronic toxicity data for acephate were consolidated by OW in 2015 and combined with data
from OPP's registration review document for acephate (U.S. EPA 2007). The final chronic
acephate dataset consisted of one NOECs/LOEC for one invertebrate species (Table 5).
Table 5. C
ironic toxicity data o
'acephate to freshwater aquatic organisms.
OW MDR
Croup'1
(Ion us
Species
NOEC
(MS/1-)
I.OEC
(MS/U
Liulpoinl
Re Terence
Comment
D
Daphnia
magna
150
375.0
Reduction in
offspring
MRID
44466601;
McCain. 1978
Supplemental
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark for acephate is 150 |ig/L, which is the NOEC for
Daphnia magna.
The OPP fish chronic benchmark is 5,760 |ig/L, which is the estimated NOEC for Oncorhynchus
mykiss, extrapolated using most sensitive acute 96-h LC50 for rainbow trout (832,000 |ig/L)
divided by 144.44 (highest rainbow trout ACR for organophosphates).
GLI Tier II Chronic Value Calculation
Quantitative chronic tests are not available for acephate. Therefore, per the GLI Tier II
methodology, all three ACRs are the default value of 18, the geometric mean of which (i.e., the
SACR) is 18. The calculated Secondary Chronic Value (SCV) for acephate is 40.52 |ig/L.
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = V18 * 18 * 18 = 18
SCV =
SCV =
SACR
729.3
18
= 40.52 [ig/L
121
-------
Table 6. Summary and comparison of chronic values for acephate.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II value
(# of ACRs filled,
magnitude relative to ALB)
OW Invertebrate-
only HCos
(# of ACRs filled,
magnitude relative
to ALB)
Notes
Acephate
150 ng/L
(2007, Daphnia
magna)
40.52 ng/L
(GLI Tier II; 0 ACRs, 3.7X)
NA
Three default ACRs
of 18 used to derive
GLI Tier II value.
1.2.2.3 Acephate References
ECOTOX 37219. Hussain M.A.; Mohamad R.B.; Oloffs P.C. 1985. Studies on the Toxicity,
Metabolism, and Anticholinesterase Properties of Acephate and Methamidophos. J. Environ. Sci.
Health Part B: Pestic. Food Contam. Agric. Wastes 20(1): 129-147.
ECOTOX 51716. Lyons D.B.; Buckner C.H.; McLeod B.B.; Sundaram K.M.S. 1976. The
Effects of Fenitrothion, Matacil and Orthene on Frog Larvae. Rep. No. CC-X-129, Chemical
Control Research Institute, Department of the Environment Canada, Ottawa, Ontario : 86 p.
ECOTOX 6797. Mayer, F. L. J. and Ellersieck, M. R. 1986. Manual of Acute Toxicity:
Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals. Resour.
Publ. No. 160, U.S. Department of Interior, Fish and Wildlife Services, Washington, DC 505 p.
ECOTOX 7317. Duangsawasdi, M. 1977. Organophosphate Insecticide Toxicity in Rainbow
Trout (Salmo gairdneri). Effects of Temperature and Investigations on the Sites of Action. Ph.D
Thesis, University of Manitoba, Canada, Ph.D. Thesis, University of Manitoba, Manitoba,
Canada : 138 p.
MRID 00014565. Wheeler, R. E., 1978. 48 Hour Acute Static Toxicity of Orthene (SX911) to
1st Stage Nymph Water Fleas (Daphnia magna Straus). Unpublished study conducted by
Agricultural Research Laboratory, Richmond, California. Sponsored by Chevron Chemical
Company, Ortho Division. Study completed August 25, 1978.
MRID 40094602 Johnson, W. and M. Finley. 1980. Handbook of Acute Toxicity of Chemicals
to Fish and Aquatic Invertebrates: Resource Publication 137. US Fish and Wildlife Service,
Washington, D.C. 106 p.
MRID 40098001 Mayer, F. and M. Ellersieck. 1986 Manual of Acute Toxicity: Interpretation
and Data Base for 410 Chemicals and 66 Species of Freshwater Animals. US Fish & Wildlife
Service, Resource Publication 160. 579 p.
MRID 44042901. Hall, R. J. and E. Kolbe. 1980. Bioconcentration of Organophosphorus
Pesticides to Hazardous Levels by Amphibians. Journal of Toxicology and Environmental
Health 6: 853 -860.
MRID 44466601. McCann, J.A. 1978. U.S. Environmental Protection Agency, Pesticides
Regulation Div., Agricultural Research Center, Animal Biology Laboratory, unpublished report.)
122
-------
Geen, G.H., B.A. McKeown, T.A. Watson, and D.B. Parker. 1984. Effects of Acephate
(Orthene) on Development and Survival of the Salamander, Ambystoma gracile (Baird). J.
Environ. Sci. Health Part B Pestic. Food Contam. Agric. Wastes, 19, (2), 157-170.
ECOREF#:l 1134
Johnson, W. and M. Finley. 1980. Handbook of Acute Toxicity of Chemicals to Fish and
Aquatic Invertebrates: Resource Publication 137. US Fish and Wildlife Service, Washington,
D C. 106 p.
Mayer, F. L. J. and Ellersieck, M. R. 1986. Manual of Acute Toxicity: Interpretation and Data
Base for 410 Chemicals and 66 Species of Freshwater Animals. Resour. Publ. No. 160, U.S.
Department of Interior, Fish and Wildlife Services, Washington, DC 505 p.Mayer and Ellersiek
1986
Schoettger, R.A., and W.L. Mauck. 1978 . Toxicity of Experimental Forest Insecticides to Fish
and Aquatic Invertebrates. In: D.I.Mount, W.R.Swain, and N.K.Ivanikiw (Eds.), Proceedings of
the First and Second USA-USSR Symposia on the Effects of Pollutants Upon Aquatic
Ecosystems, 11-27.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2007. Risks of acephate use to the federally-listed California red legged frog (Rana
aurora draytonii). Pesticide effects determination. Office of Pesticide Programs. Washington,
D C. July 19, 2007.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and the Clean Water Act
(CWA). EPA-820-D-24-002.
123
-------
1.2.3 Comparison of Aquatic Life Toxicity Values for Dimethoate: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) are described below. Toxicity data for dimethoate were gathered by
OW in 2015 and combined with data from OPP's registration review document for dimethoate
(U.S. EPA 2008).
1.2.3.1 Dimethoate Acute Toxicity Data
The dimethoate acute data include six LCsos representing five species in five genera that were
classified as "quantitative" data, two 96-hour LCsos for the species Poecilia reticulata classified
as "qualitative" that appear to be acceptable tests given the available information; and two
"qualitative" 48-hour LCsos for species within the genus Chironomus included in order to
calculate an invertebrate-only HCos.
The final acute dimethoate dataset consisted of eight quantitative LCsos and two "qualitative"
LCsos for eight total species across seven genera, of which five were invertebrate species across
four invertebrate genera. Acute data for dimethoate are shown in Table 1. Ranked invertebrate
GMAVs (both quantitative and qualitative) are listed in Table 2.
Table 1. Acceptable acute toxicity t
ata of dimethoate to freshwater aquatic organisms
OW
M l)K
(1 rou p1'
(Ion us
Species
l.( 50/
IX 50
(Mii/U
S\1 AY
(MS/1->
(IMAY
(MS/'-)
Reference
Comment
F
Chironomus
riparius
481
481
345.4
ECOTOX 102849.
Domingues et al.
2007
Duration, 48hr
F
Chironomus
dilutus
248
248
ECOTOX 74947.
Anderson and Zhu
2004
Duration, 48hr
D
Daphnia
magna
3,154
3,154
3,154
ECOTOX 18476.
Song et al. 1997
Represents 8
tests
F
Pteronarcys
californica
43
43
43
MRID 00003503.
Johnson and Finley.
1980
Represents 3
tests
E
Gammarus
lacustris
200
200
200
ECOTOX 6797.
Mayer and Ellersieck
1986
Represents 2
tests
B
Poecilia
reticulata
548,800
429,798
429,798
ECOTOX 5180.
Canton etal. 1980
OECD test-
not publicly
available
B
Poecilia
reticulata
336,600
ECOTOX 5370.
Maas 1982
OECD test-
not publicly
available
B
Lepomis
macrochirus
6,000
6,000
6,000
ECOTOX 6797.
Mayer and Ellersieck
1986
Represents 2
tests
A
Oncorhynchus
mykiss
8,600
7,302
7,302
ECOTOX 6797.
Mayer and Ellersieck
1986
124
-------
o\\
MDR
Croup'
(Ion us
Species
I X 50/
I X 50
(Mli/I.)
S\1 AY
(MS/'-)
GMAV
(MS/'-)
Reference
Comment
A
Oncorhynchus
mykiss
6,200
ECOTOX 6797.
Mayer and Ellersieck
1986
Represents 7
tests
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 21.5 |ig/L, which is V2 of the Pteronarcys californica
LC50 of 43 |ig/L cited in U.S. EPA (2008).
The OPP fish acute benchmark is 3,100 |ig/L, which is V2 of the Oncorhynchus mykiss LC50 of
6,200 |ig/L cited in U.S. EPA (2008).
GLI Tier II Acute Value Calculation
The acceptable dataset for dimethoate represents five of the eight MDRs, corresponding to the
use of a SAF of 6.1. Applying the SAF to the lowest, most sensitive GMAV (i.e., 43.0 |ig/L for
stonefly (Pteronarcys californica)), the calculated SAV is 7.0 |ig/L. Half of the SAV is 3.5 |ig/L
The SMC of 3.5 |ig/L is lower than the most sensitive GMAV. Detailed calculations are shown
below:
Lowest GMAV
SAV = —
SAF
43.0
SAV = — = 7.0 \ig/L
SAV
SMC = ——
7.0
SMC = — = 3.5 |xg/L
Genus-Level Invertebrate-Only HC05
The genus-level invertebrate-only acute HC05 following the U.S. EPA (1985) methodology for
the four invertebrate genera in the dimethoate dataset (Table 2) was 4.296 |ig/L (Table 3).
125
-------
Table 2. Dimethoate invertebrate SMAVs and GMAVs (iig/L).
(Ion us
Species
SM AY
(IMAY
(iMAY Kiink
Daphnia
magna
3,154
3154
4
Chironomus
riparius
481.0*
345.4
3
Chironomus
dilutus
248.0*
Gammarus
lacustris
200.0
200.0
2
Pteronarcys
californica
43.00
43.00
1
* Qualitative values (48-hour LCsos).
Note: SMAVs and GMAVs for Chironomus sp. are 48-hour tests that were classified as qualitative in but
are added here to meet minimum requirements to calculate a genus-level invertebrate HC05.
Table 3. Genus-level invertebrate acute HC05 for dimethoate calculated following the U.S.
EPA (1985) methodology.
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
4
4
3154
8.056
64.906
0.8000
0.8944
3
345.4
5.845
34.161
0.6000
0.7746
2
200.0
5.298
28.072
0.4000
0.6325
1
43.00
3.761
14.147
0.2000
0.4472
Sum:
22.96
141.3
2.000
2.749
S2 =
85.34
L =
-0.608
A =
1.458
hc05 =
4.296
126
-------
Table 4. Summary and comparison of acute values for dimethoate.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP
Invertebrate
ALB
(lowest LCso/2)
(Year published,
species)
OW GLI Tier
II values(# of
MDRs filled,
magnitude
relative to
ALB)
OW Genus-level
Invertebrate-
only HCos/2
(# of genera,
magnitude
relative to ALB)
Notes
Dimethoate
21.5 ng/L
(2016;
Pteronarcys
californica)
3.5 ng/L
(5 MDRs filled,
6. IX)
2.15 ng/L
(4 genera*, 10X)
The FIFRA ALB is half the LC50 reported for
stonefly (P. californica), which was used as
the basis for the GLI Tier II acute value.
The genus-level invertebrate value is lower
than the FIFRA ALB because of the relatively
steep slope and small sample size calculated
from the Guidelines algorithm, while the
FIFRA ALB is half of the most sensitive
GMAV.
* GMAV for Chironomus sp. is based on data
classified as qualitative that were included to
allow for sufficient sample size to calculate a
genus-level invertebrate value. Tests were
classified as qualitative because it was for a
non-standard duration (48-hours).
Figure 1 shows a genus-level sensitivity distribution for the dimethoate dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values, GLI tier II calculated acute value, and invertebrate-
only acute HC05/2 are included.
127
-------
1,000,000
100,000
10,000
—I
tJJO
3;
01
ro 1,000
o
-C
-------
1.2.3.2 Dimethoate Chronic Toxicity Data
Chronic Data Sources and Considerations
Chronic toxicity data for dimethoate were consolidated by OW in 2015 and combined with data
from OPP's registration review document for dimethoate (U.S. EPA 2008). The final chronic
dimethoate dataset consisted of two NOECs/LOECS for two species across two genera, of which
one was an invertebrate and one was a vertebrate (Table 5).
Table 5. Chronic toxicity data of dimethoate to freshwater aquatic organisms
OW
MI)R
(il'OII|):l
(Ion us
Species
\()IX
(jig/U
LOIX
(MS/'-)
Knclpoinl
Reference
Comment
D
Daphnia
magna
40
100
Reproduction,
survival and growth
MRID 42864701
Quantitative
A
Oncorhynchus
mykiss
430
840
Impaired growth
MRID 43106301,
43106302,
43106303
Quantitative
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 0.5 |ig/L, which is the estimated NOEC for
Pteronarcys californica using the ACR for D. magna. P. California LC50 (43 |ig/L) ^ I), magna
ACR (83) = 0.5 |ig/L.
The OPP fish chronic benchmark is 430 |ig/L, which is the NOEC for Oncorhynchus mykiss.
GLI Tier II Chronic Value Calculation
Quantitative dimethoate chronic and acute toxicity data were available for water flea (Daphnia
magna) and rainbow trout (Oncorhynchus mykiss), allowing for the calculation of two ACRs.
The default value of 18 was used to fulfill the third ACR per the GLI Tier II methodology. ACRs
were calculated using the test with the lowest acute endpoint. The rainbow trout (Oncorhynchus
mykiss) test with the lowest acute endpoint (i.e., 6,200 |ig/L) was therefore used in the
calculations.
The acute and chronic tests for water flea (Daphnia magna) and for rainbow trout
(iOncorhynchus mykiss) were conducted in different laboratories, using water of different
physical characteristics; therefore, the ACRs were calculated using the OPP methodology, which
involves using the NOAEC as the chronic value. The calculated SCV is 0.3 |ig/L. Detailed
calculations for the SCV are shown below:
129
-------
SACR = Geometric Mean of the ACRs
SACR = Vl4.4#79#18 = 27.4
SCV =
SACR
SCV = ^ = 0.3 \ig/L
Table 6. Summary and comparison of chronic values for dimethoate.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP va
ue is higher than t
ie OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II
value
(# of ACRs
filled, magnitude
relative to ALB)
OW Invertebrate-
only HCos
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Dimethoate
0.5 ng/L
(2016, estimated
NOAEC value for
Pteronarcys
californica calculated
using the ACR for
Daphnia magna)
0.3 ng/L
(GLI Tier II; 2
ACRs, 1.7X)
NA
One default ACR of 18
used to derive GLI Tier II
value.
1.2.3.3 Dimethoate References
ECOTOX 102849. Domingues, I., Guilhermino, L., Soares, A. M. V. M., and Nogueira, A. J.A.
2007. Assessing Dimethoate Contamination in Temperate and Tropical Climates: Potential Use
of Biomarkers in Bioassays with Two Chironomid Species. Chemosphere 69(1): 145-154.
ECOTOX 18476. Song, M. Y., Stark, J. D., and Brown, J. J. 1997. Comparative Toxicity of Four
Insecticides, Including Imidacloprid and Tebufenozide, to Four Aquatic Arthropods. Environ.
Toxicol. Chem. 16(12): 2494-2500.
ECOTOX 5180. Canton, J. H., Wegman, R. C. C., Van Oers, A., Tammer, A. H. M., Mathijssen-
Spiekman, E. A. M., and Van den Broek, H. H. 1980. Environmental Toxicological Research
with Dimethoate and Omethoate, Rep.No. 121/80, Natl. Inst. Public Health Environ. Hyg.: 6 p.
ECOTOX 5370. Maas, J.L. 1982. Toxicity of Pesticides. Rep.No.82, Lab.for Ecotoxicol., Inst.for
Inland Water Manag.and Waste Water Treatment 15: 4 p.
ECOTOX 6797. Mayer, F. L., and Ellersieck, M. R. 1986. Manual of Acute Toxicity:
Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals.
Resour.Publ.No.160, U.S.Dep.Interior, Fish Wildl.Serv., Washington, DC : 505 p.
ECOTOX 74947. Anderson, T. D., and Zhu, K. Y. 2004. Synergistic and Antagonistic Effects of
Atrazine on the Toxicity of Organophosphorodithioate and Organophosphorothioate Insecticides
to Chironomus tentans (Diptera: Chironomidae). Pestic. Biochem. Physiol. 80(1): 54-64.
130
-------
MRID 00003503. Johnson, W. and M. Finley. 1980. Handbook of Acute Toxicity of Chemicals
to Fish and Aquatic Invertebrates: Resource Publication 137. US Fish and Wildlife Service,
Washington, D.C. 106 p.
MRID 42864701. Wuthrich, V. 1990. Influence of Dimethoate on the Reproduction of Daphnia
magna. Unpublished study conducted by RCC UMWELTCHEMIE AG, Itingen, Switzerland.
Study number 264464. Sponsored by Dimethoate Task Force, Ingelheim, Germany and
submitted by Cheminova Agro A/S, Harbonone-Lenmark, DK. Study completed December 20,
1990.
MRID 43106301 Strawn, T. and M. Muckerman. 1994. Early Life-stage Toxicity of Dimethoate
to the Rainbow Trout (Oncorhynchus mykiss) Under Flow-through Conditions: Final Report:
Lab Project Number: 40864. Unpublished study prepared by ABC Labs, Inc. 436.
MRID 43106302 Strawn, T. L., and M. Muckerman. 1994. Early Life-Stage Toxicity of
Dimethoate to the Rainbow Trout (Oncorhynchus mykiss) under Flow-Through Conditions.
Unpublished study conducted by ABC Laboratories, Inc., Columbia, Missouri. Report No
40864R. Sponsored by Cheminova Agro A/S, Lemvig, Denmark. Study submitted January 25,
1994.
MRID 43106303 Mahalik, R. and J. B Bussard. 1993. Method Validation for the Analysis of
Dimethoate in Aquatic Test Water. Unpublished study conducted by ABC Laboratories, Inc.,
Columbia, Missouri. Report No. 40863. Sponsored by Cheminova Agro A/S, Lemvig,
Denmark. Study submitted July 21, 1993.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2008. Risks of dimethoate use to the federally-listed California red legged frog (Rana
aurora draytonii). Pesticide effects determination. Office of Pesticide Programs. Washington,
D.C. January 31, 2008.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and the Clean Water Act
(CWA). EPA-820-D-24-002.
131
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1.2.4 Comparison of Aquatic Life Toxicity Values for Phosmet: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) are described below. Toxicity data for phosmet were gathered by OW
in 2015 and combined with data from OPP's registration review document for phosmet (U.S.
EPA 2009).
1.2.4.1 Phosmet Acute Toxicity Data
Acute data for phosmet include thirty-four LCsos representing ten species in eight genera that
were classified as "quantitative" data and one 48-hour LCso for the fairy shrimp Streptocephalus
sealii classified as qualitative, but included here to increase the number of invertebrate genera to
four, thereby allowing the calculation of an invertebrate genus-level HCos. This test was
classified as qualitative because it was for a non-standard duration (48-hours).
The final acute phosmet dataset consisted of 35 LCsos for 11 species across nine genera, of
which four were invertebrate species representing four different genera. Acute data for phosmet
are shown in Table 1. The ranked invertebrate GMAVs are listed in Table 2.
Table 1. Acute toxicity data of phosmet to freshwater aquatic organisms.
OW
MI)R
(iroup'1
(ionus
Species
l .( 50/
IX 50
(Mli/U
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
Reference
D
Streptocephalus
sealii
170
170.0
170.0
MRID 40094602
D
Daphnia
magna
5.6
5.6
5.6
Mayer and Ellersieck 1986
E
Gammarus
fasciatus
2.4
2.4
2.4
MRID 00063193; Sanders 1972
E
Caecidotea
brevicauda
72
Mayer and Ellersieck 1986
E
Caecidotea
brevicauda
90
80.50
80.50
Mayer and Ellersieck 1986
B
Pimephales
promelas
7,300
7,300
7,300
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
1,000
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
1,400
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
1,000
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
640
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
200
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
22
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
60
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
70
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
180
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
560
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
200
Mayer and Ellersieck 1986
B
Lepomis
macrochirus
70
231.2
231.2
MRID 00063194; Julinand
Sanders 1977
B
Micropterus
dolomieu
150.0
150.0
-
Mayer and Ellersieck 1986
B
Micropterus
salmoides
160.0
160.0
154.9
Mayer and Ellersieck 1986
A
Oncorhynchus
tshawytscha
150.0
150.0
-
Mayer and Ellersieck 1986
132
-------
()\\
MDR
(iioup1
(ionus
Species
IX 50/
I X 50
(Mii/U
S\1 AY
(MB/'-)
(IMAY
(MB/'-)
Reference
A
Oncorhynchus
mykiss
280.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,200
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
1,600
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
420.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
130.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
105.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
480.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
240.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
560.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
120.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
300.0
Mayer and Ellersieck 1986
A
Oncorhynchus
mykiss
513.9
352.5
229.9
Julin and Sanders 1977
B
Ictalurus
punctatus
10,600
Mayer and Ellersieck 1986
B
Ictalurus
punctatus
11,000
10,798
10,798
MRID 00063194; Julin and
Sanders 1977
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Benchmark Acute Values
The OPP invertebrate acute benchmark is 4.32 |ig/L, which is V2 of the Daphnia magna EC50 of
8.64 |ig/L.
The OPP fish acute benchmark is 35 |ig/L, which is V2 of the Lepomis macrochirus LC50 of 70
Hg/L.
GLI Tier II Acute Value Calculation
The acceptable dataset for phosmet represents five of the eight MDRs, corresponding to the use
of an SAF of 6.1. Applying the SAF to the lowest, most sensitive GMAV (i.e., 2.4 |ig/L for scud
(Gammarus fasciatus)), yields the SAV of 0.39 |ig/L. Half of the SAV is 0.20 |ig/L. The SMC of
0.20 |ig/L. Detailed calculations for the SMC are shown below:
Lowest GMAV
2.4
SAV = — = 0.39 ag/L
6.1
133
-------
SMC =
SAV
~2~
0.39
SMC = —- = 0.20|ig/L
Genus-Level Invertebrate-only HCos
The genus-level invertebrate-only acute HCos calculated following the U.S. EPA (1985)
methodology for the four invertebrate genera in the phosmet dataset (Table 2) is 0.1480 |ig/L
(Table 3).
Table 2. Phosmet invert
tebrate SMAVs and GMAVs (jug/L).
(iI'll IIS
Species
SM AY
(;ma\
CMAY R;tilk
Strep to cephalus
sealii
170.0
170.0
4
Caecidotea
brevicauda
80.50
80.50
3
Daphnia
magna
5.600
5.600
2
Gammarus
fasciatus
2.400
2.400
1
Note: The S. sealii GMAV is based on data classified as qualitative that were included to allow for a sufficient
sample size to calculate an invertebrate genus-level HCos.
Table 3. Genus-level invertebrate acute HCos for phosmet calculated following the U.S.
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
4
4
170
5.136
26.38
0.8000
0.8944
3
80.50
4.388
19.26
0.6000
0.7746
2
5.6
1.723
2.968
0.4000
0.6325
1
2.4
0.8755
0.7664
0.2000
0.4472
Sum:
12.12
49.37
2.000
2.749
S2 =
113.6
L =
-4.294
A =
-1.910
hc05 =
0.1480
Note: The fourth most sensitive GMAV was classified as qualitative for the reason explained under Data Sources
and Considerations.
134
-------
Table 4. Summary and comparison of acute values for phosmet.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 inc
icates the OPP value is higher than the OW value.
Pesticide
OPP
Invertebrate
ALB
(lowest LCso/2)
(Year published,
species)
OPP GLI Tier II
values (# of
MDRs filled,
magnitude
relative to ALB)
OW Genus-
level
Invertebrate-
only HCos/2
(# of genera,
magnitude
relative to ALB)
Notes
Phosmet
4.32 ng/L
(2023; Daphnia
magna)
0.20 ng/L
(5 MDRs filled,
22X)
0.074 (ig/L
(4 genera*, 58X)
The FIFRA ALB is based on an acute
toxicity test that used 51% TEP, producing
an EC50 value of 8.64 |ig/L for water flea (I),
magna). This acute toxicity test was not used
in the GLI Tier II or genus-level invertebrate
value calculations as per the Guidelines.
The genus-level invertebrate value is lower
than the FIFRA ALB because the most
sensitive SMAV is an EC50 of 2.4 |ig/L for
scud (G. fasciatus). This study was not used
to derive the FIFRA ALB because it was
categorized as "qualitative" as the raw data
was not available.
* GMAV for the spiny-tail fairy shrimp
Streptocephalus sealii is based on data
classified as qualitative that were included to
allow for sufficient sample size to calculate a
genus-level invertebrate value. The test was
classified as qualitative because it was for a
non-standard duration (48-hours).
Figure 1 shows a genus-level sensitivity distribution for the phosmet dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP benchmark acute values, the GLI Tier II calculated value, and invertebrate-
only acute HC05/2 are included.
135
-------
100,000.00
10,000.00
1,000.00 -
M 100.00
a;
E
O 10.00
1.00
0.10
0.01
• Arthropod
O Arthropod (Qualitative)
¦ Salmonid Fish
~ Other Fish
GLI Tier II Value
Genus-level Invertebrate HC05/2
OPP Invertebrate Benchmark
— • • OPP Fish Benchmark
• Caecidotea
Streptocepahlus
Daphn.ia
OPP Fish Benchmark = 35 |ig/L
OPP Invertebrate Benchmark = 4.32 |ig/L
• Gammarus
GLI Tier II Acute Value = 0.20 |ig/L
Genus-level Invertebrate FIC05/2 = 0.0740 ng/L
0.0
0.1
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Phosmet genus-level SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from an EPA literature search in 2015,
supplemented the Office of Pesticide Programs (OPP) registration review document for phosmet (U.S. EPA 2009).
136
-------
1.2.4.2 Phosmet Chronic Toxicity Data
Chronic Data Sources and Considerations
Chronic toxicity data for phosmet were gathered from by OW in 2015 for phosmet and combined
with data from OPP's registration review document for phosmet (U.S. EPA 2009). The final
chronic phosmet dataset consisted of four NOECs/LOECS for four species across four genera.
One test was an invertebrate genus and three were vertebrate genera (Table 5).
Table 5. Chronic toxicity data of phosmet to freshwater aquatic organisms
OW
MI)R
(il'OII|):l
(Ion us
Species
\oi:c
(MU/I)
LOW
(MS/'-)
Liulpoinl
Reference
Comment
D
Daphnia
magna
0.75
1.0
Reduced number of
offspring
MRID 40652801;
Burgess. 1988
Quantitative
A
Oncorhynchus
mykiss
3.2
6.1
Reduction in growth
MRID 40938701;
Cohle. 1988
Quantitative
B
Pimephales
promelas
1.0
9.3
Survival and
fertilization success
MRID 48673002;
York. 2012
Acceptable
C
Xenopus
laevis
8.1
9.6
Metamorphosis
MRID 48673001;
Lee. 2012
Acceptable
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 0.75 |ig/L, which is the NOEC for Daphnia magna.
The OPP fish chronic benchmark is 1.0 |ig/L, which is the NOEC for Pimephalespromelas.
GLI Tier II Chronic Value Calculation
Quantitative phosmet chronic and acute toxicity data were available for rainbow trout
{Oncorhynchus mykiss) and water flea (Daphnia magna), allowing for the calculation of two
ACRs. The default value of 18 was used to fulfill the third ACR per the GLI Tier II
methodology. The quantitative acute and chronic tests for the water flea (Daphnia magna) and
rainbow trout (Oncorhynchus mykiss) were conducted in different laboratories, using water of
different physical characteristics; therefore the ACRs were calculated using the OPP
methodology, which involves using the NOAECs as the chronic values. Detailed calculations for
the SCV, which was calculated as 0.02 |ig/L, are shown below:
SACR = Geometric Mean of the ACRs
SACR = a/7 * 32.8 * 18 = 16.0
137
-------
SCV =
SACR
0.39
SCV = — = 0.02 [ig/L
Table 6. Comparison of chronic values for phosmet.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II value
(# of ACRs filled,
magnitude
relative to ALB)
OW Invertebrate-
only HCos
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Phosmet
0.75 ng/L
(2023, Daphnia
magna)
0.02 ng/L
(GLI Tier II; 2
ACRs, 38X)
NA
One default ACR of 18
used to derive GLI Tier II
value.
1.2.4.3 Phosmet References
ECOTOX 6797. Mayer, F. L. J., and Ellersieck, M. R. 1986. Manual of Acute Toxicity:
Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals. Resour.
Publ. No. 160, U.S. Department of Interior, Fish and Wildlife Services, Washington, DC 505 p.
MRID 00063193. Sanders, H.O. 1972. Toxicity of some insecticides to four species of
Malacostracan crustaceans. U.S. Fish and Wildlife Service, Fish-Pesticide Research Laboratory.
Washington, D.C.: USFWS. Technical papers of the Bureau of Sport Fisheries and Wildlife 66;
published study; CDL:232666-T.
MRID 00063194 and ECOTOX 857. Julin, A. M., and Sanders, H.O. 1977. Toxicity and
accumulation of the insecticide imidan in freshwater invertebrates and fishes. Transactions of the
American Fisheries Society. 106(4):386-392.
MRID 40652801. Burgess, D. 1988. Chronic toxicity of 14C-Imidan to Daphnia magna under
flow-through test conditions. Analytical bio-chemistry laboratories, Inc.; Report No. 35778.
(Unpublished report received August 10, 1988; submitted by ICI Americas, Inc. under EPA
Accession No. 406528-01).
MRID 40938701. Cohle, P. 1988. Early life stage toxicity of C14-Phosmet to rainbow trout
(Salmo gairdneri), in a flow through system. Prepared by ABC Laboratories, Inc. Columbia,
MO. Submitted by ICI Agrochemicals, England.
MRID 48673001. Lee, M. 2012. Phosmet - Amphibian Metamorphosis Assay with African
Clawed Frog (Xenopus laevis). Project Number: 12791/6142. Unpublished study prepared by
Smithers Viscient Laboratories. 127 p. Relates to L0001444.
MRID 48673002. York, D. 2012. Phosmet - Short-Term Reproduction Assay with Fathead
Minnow (Pimephales promelas). Project Number: 12791/6143. Unpublished study prepared by
Smithers Viscient Laboratories. 161 p. Relates to L0001444.
138
-------
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2009. Problem formulation for the environmental fate and ecological risk, endangered
species, and drinking water assessments in support of the registration review of phosmet. Office
of Pesticide Programs. Washington, D.C. April 16, 2009.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and the Clean Water Act
(CWA). EPA-820-D-24-002
139
-------
1.2.5 Comparison of Aquatic Life Toxicity Values for Terbufos: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) for terbufos are described below. Toxicity data for terbufos were
gathered by OW in 2015 and combined with data from OPP's registration review document for
terbufos (U.S. EPA 2015).
1.2.5.1 Terbufos Acute Toxicity Data
The final acute terbufos dataset consisted of 33 LCsos for nine species representing nine genera,
of which five were invertebrate species representing five invertebrate genera. Acute data for
terbufos are shown in Table 1. The invertebrate GMAVs are listed in Table 2.
140
-------
Table 1. Acute toxicity data of terbufos to freshwa
er aquatic organisms.
()\\
MI)R
(iroup'1
(Ion us
Species
LC50/
IX 50
(MU/I-)
S\1 AY
(MJi/l)
(IMAY
(MS/'-)
Reference
Comment
D
Ceriodaphnia
dubia
0.139
0.1286
0.1286
ECOTOX 153854. Choung et al. 2011
Quantitative, >98% a.i.
D
Ceriodaphnia
dubia
0.119
ECOTOX 153854. Choung et al. 2012
Quantitative, >98% a.i.
E
Daphnia
magna
0.400
0.2608
0.2608
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
E
Daphnia
magna
0.170
MRID 00101495
E
Gammarus
pseudolimnaeus
0.200
0.2000
0.2000
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
E
Procambaras
clarkii
5.782
6.801
6.801
ECOTOX 18475. Fornstrom et al. 1997
Qualitative, control mortality;
organisms fed during experiment
E
Procambaras
clarkii
8.0
MRID 00085176
F
Chironomus
plumosus
1.4
1.400
1.400
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
10.00
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
13.00
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
7.600
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
8.400
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
10.00
10.45
10.45
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
13.20
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
15.30
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
8.600
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
A
Oncorhynchus
mykiss
11.50
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
141
-------
()\\
MDR
(i rou |):|
(Ion us
Species
IX 50/
IX 50
(Mli/I )
S\1 AY
(M8/U
(IMAY
(M8/I-)
Reference
('omnicnl
A
Oncorhynchus
mykiss
9.400
MRID 00037483. Sleight. 1972
Quantitative, 86.3% a.i.
A
Salmo
trutta
20
20.00
20.00
MRID 00087718
B
Pimephales
promelas
12.870
70.85
70.85
ECOTOX 14097. Call et al. 1989
Qualitative, Source of test
species unknown; dechlorinated
tap water used; no replicate
B
Pimephales
promelas
390.0
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
1.700
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
2.400
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
2.000
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
1.600
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
1.500
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
1.800
1.569
1.569
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
1.500
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
1.500
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
1.100
ECOTOX 6797. Mayer and Ellersieck.
1986
Quantitative, 88% a.i.
C
Lepomis
macrochirus
0.770
MRID 00087718. Roberts and Wineholt.
1976
Quantitative, 86% a.i.
C
Lepomis
macrochirus
3.80
MRID 00037483
C
Lepomis
macrochirus
0.87
MRID 00085176
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish,
etc.)
142
-------
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
143
-------
OPP Benchmark Acute Values
The OPP invertebrate acute benchmark is 0.085 |ig/L, which is V2 of the Daphnia magna acute
test value of 0.17 |ig/L.
The OPP fish acute benchmark is 0.385 |ig/L, which is V2 of the Lepomis macrochirus acute LC50
of 0.770 |ig/L.
GLI Tier II Acute Value Calculation
The Method B acute dataset for terbufos fulfills five of the eight MDRs, corresponding to the use
of a Secondary Acute Factor (SAF) of 6.1. Applying the SAF to the lowest, most sensitive
GMAV (i.e., 0.128 |ig/L for water flea (Ceriodaphnia dubia)), yields the calculated Secondary
Acute Value (SAV) of 0.021 |ig/L. The Secondary Maximum Criterion (SMC), which is
calculated as half the SAV, is 0.011 |ig/L.
Detailed calculations for the SMC are shown below:
Lowest GMAV
0.128
SAV = —— = 0.021 ag/L
6.1
SAV
SMC= —
0.021
SMC = —= 0.0111xg/L
Genus-Level Invertebrate-only Acute HC05
The genus-level invertebrate-only acute HC05 calculated following the U.S. EPA (1985)
methodology for the five invertebrate genera (Table 2) in the terbufos dataset is 0.0283 ng/L
(Table 3).
Table 2. Terbufos invcrlebrale SMAV and GMAV (iig/I.).
(Ion us
Species
SMAV
GMAV
GMAV kit 11k
Procambarus
clarkii
6.801
6.801
5
Chironomus
plumosus
1.400
1.400
4
Daphnia
magna
0.2608
0.2608
3
Gammarus
pseudolimnaeus
0.2000
0.2000
2
Ceriodaphnia
dubia
0.1268
0.1268
1
Note: The Procambarus clarkii SMAV and GMAV is the geometric mean of a qualitative LC50 used to fill an MDR
group and an acceptable LC50 listed in the OPP registration review document.
144
-------
Table 3. Genus-level invertebrate-only acute HCos for terbufos calculated following the
N
Rank
(.MAY
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
s qrt(P)
5
4
1.400
0.336
0.11
0.6667
0.8165
3
0.2608
-1.344
1.81
0.5000
0.7071
2
0.2000
-1.609
2.59
0.3333
0.5774
1
0.1286
-2.051
4.206
0.1667
0.4082
Sum:
-4.67
8.72
1.6667
2.5092
S2 =
35.285
L =
-4.893
A =
-3.565
hc05 =
0.0283
Table 4. Comparison of acute values for terbufos.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates the OPP value is higher t
ian the OW value.
OPP Invertebrate ALB
OPP GLI Tier II value (#
of MDRs filled,
magnitude relative to
ALB)
OW Genus-level
Invertebrate-only HCos/2
(# of genera, magnitude
relative to ALB)
Pesticide
(lowest LCso/2) (Year
published, species)
Terbufos
0.085 ng/L
(2023; Daphnia magna)
0.011 ng/L
(5 MDRs filled, 1 .IX)
0.014 (ig/L
(4 genera, 6. IX)
Figure 1 shows a genus-level sensitivity distribution for the terbufos dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values, GLI Tier II calculated acute value and invertebrate-
only acute HC05/2 are included.
145
-------
1,000.000
100.000
10.000
tuo
3
SA
£
3
-Q
1—
.01
1.000
0.100
0.010
0.001
•
Arthropod
o
Arthropod (Qualitative)
¦
Salmonid Fish
~
Other Fish
Genus-level Invertebrate
OPP Invert. Benchmark
OPP Fish Benchmark
GLI Tier II (Method B)
Gammarus •
Ceriodaphnia
0.0
0.1
0.2
Chironomus
Daphnia
Procambarus o
OPP Fish Benchmark = 0.385 ng/L
OPP Invertebrate Benchmark = 0.085 ^ig/L
Genus-level Invertebrate HC05/2 = 0..0141 ur/L
GLI Tier II Acute Value = 0.011 pg/L
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Terbufos genus-level acute SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from an EPA literature search in 2015,
supplemented the Office of Pesticide Programs (OPP) registration review document for terbufos (U.S. EPA 2015).
146
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1.2.5.2 Terbufos Chronic Toxicity Data
Chronic Data Sources and Considerations
Chronic toxicity data for terbufos were gathered by OW in 2015 for terbufos and combined with
data from OPP's registration review document for terbufos (U.S. EPA 2015). The final chronic
terbufos dataset consisted of two NOECs/LOECS for two species across two genera, of which
one was an invertebrate and one was a vertebrate (Table 5).
Table 5. Chronic toxicity data of terbufos to freshwater aquatic organisms.
OW
MIJR
(iioup'
(Ion us
Species
\oi:c
(Mii/U
LOIX
(MS/'-)
Knilpoinl
Reference
D
Daphnia
magna
0.030
0.076
Reductions in length
and number of
offspring
MRID 00162525; Forbis et
al. 1986
A
Oncorhynchus
mykiss
0.640
1.400
Reduced length and
wet weight
MRID 41475801; Tank et al.
1990;
MRID 41475802; Rhodes
and McCallister 1990
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 0.03 |ig/L, which is the NOEC for Daphnia magna.
The OPP fish chronic benchmark is 0.10 |ig/L, which is the estimated NOEC for Lepomis
macrochirus. Bluegill sunfish sensitivity to terbufos on a chronic basis was estimated using an
acute to chronic ratio (ACR) because it is the most acutely sensitive species. The ACR was based
on rainbow trout (acute and chronic toxicity) and bluegill sunfish (acute toxicity) data.
GLI Tier II Chronic Value Calculation
Paired quantitative acute and chronic toxicity data were available for water flea (Daphnia
magna) and rainbow trout (Oncorhynchus mykiss) allowing for the calculation of two ACRs.
While the chronic tests used >90% pure terbufos, the acute tests did not. Per the GLI Tier II
methodology, the default value of 18 was used to fulfill the remaining ACR. The acute and
chronic tests for water flea (Daphnia magna) and rainbow trout (Oncorhynchus mykiss) were
conducted in different laboratories, using water of different physical characteristics. Therefore,
the OPP approach was used to calculate the SACR, which involves the use of the NOAEC value.
The calculated SCV for terbufos is 0.0014 |ig/L.
Detailed calculations for the SCV are shown below:
147
-------
= Geometric Mean of the ACRs
= V 13.33 * 14.69 * 18 = 15.22
SACR
0.021
— = 0.0014 w/i
Table 6. Summary and comparison of chronic values for terbufos.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II value
(# of ACRs filled,
magnitude
relative to ALB)
OW Invertebrate-
only HCos
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Terbufos
0.03 ng/L
(2023, Daphnia
magna)
0.0014 (ig/L
(GLI Tier II; 2
ACRs, 2IX)
NA
One default ACR of 18
used to derive GLI Tier II
value.
1.2.5.3 Terbufos References
ECOTOX 14097. Call D.J., Poirier S.H., Lindberg C.A., Harting S.L., Markee T.P., Brooke L.T.,
Zarvan N., and Northcott C.E. 1989. Toxicity of Selected Uncoupling and Acetylcholinesterase-
Inhibiting Pesticides to the Fathead Minnow (Pimephales promelas). In: D.L.Weigmann (Ed.),
Pesticides in Terrestrial and Aquatic Environments, Proc.Natl.Res.Conf., Virginia Polytechnic
Inst.and State Univ., Blacksburg, VA : 317-336.
ECOTOX 153854. Choung C.B., Hyne R.V., Stevens M.M., and Hose G.C. 2011. Toxicity of
the Insecticide Terbufos, Its Oxidation Metabolites, and the Herbicide Atrazine in Binary
Mixtures to Ceriodaphnia cf dubia. Arch. Environ. Contam. Toxicol. 60(3): 417-425.
ECOTOX 18475. Fornstrom C.B., Landrum P.F., Weisskopf C.P, and LaPoint T.W. 1997.
Effects of Terbufos on Juvenile Red Swamp Crayfish (Procambarus clarkii): Differential Routes
of Exposure. Environ. Toxicol. Chem. 16(12): 2514-2520.
ECOTOX 6797. Mayer F.L.J, and Ellersieck M.R. 1986. Manual of Acute Toxicity:
Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals. Resour.
Publ. No. 160, U.S. Department of Interior, Fish and Wildlife Services, Washington, DC 505 p.
MRID 00037483. Sleight B.H., III. 1972. The Acute Toxicity of CycocelA(R)4 and Experimental
Insecticide AC 92,100 to Bluegill (-Lepomis mac~[j,-[j~rochirus~[j,) and Rainbow Trout (-Salmo
gairdneri~[j,). (Unpublished study received Apr 9, 1973 under 3G1340; prepared by Bionomics,
Inc., submitted by American Cyanamid Co., Princeton, N.J.; CDL:093584-U).
MRID 00085176. Bentley, R. E., and K. J. Macek. 1973. Acute Toxicity of Counter to Bluegill
{Lepomis macrochirus), Channel Catfish (Ictaluruspimctatus) and crayfish {Procambarus
SACR :
SACR :
SCV =
SCV =
148
-------
clarkii). Unpublished study conducted by Bionomic, Inc, Wareham, MA. Sponsored by
American Cyanamid Company, Princeton, NJ. Completed September 1973.
MRID 00087718. Roberts S., and WineholtR.L. 1976. Static 96-hour Toxicity Study of
Terbufos in Bluegill Sunfish and Brown Trout: Laboratory No. 6E-3166. (Unpublished study
received Nov 24, 1976 under 2749-427; prepared by Cannon Laboratories, Inc., submitted by
Aceto Chemical Co., Inc., Flushing, N.Y.; CDL:226951-A).
MRID 00101495. Boudreau, P., A. D. Forbis, and L. Franklin. 1982. Acute Toxicity of
COUNTER® terbufos to Daphnia magna. Unpublished study conducted by Analytical Bio-
Chemistry Laboratories, Inc, Columbia Missouri. Report No. 28686. Sponsored by American
Cyanimid Company, Princeton, NJ. Completed March 16, 1982.
MRID 00162525. Forbis A., Land C., and Bunch B. 1986. Chronic Toxicity of CL 92, 100 to
Daphnia magna Under Flow-Through Test Conditions: ABC Final Rept. #32891. Unpublished
study prepared by Analytical Bio-Chemistry Laboratories, Inc. 164 p.
MRID 41475801.Tank S., Brewer L., Cobb G. et al. 1990. Third Year Investigation of the
Response of Selected Wildlife Populations to Planting Time Application of Counter 15G
Systemic Insecticide-nematicide in an Iowa Corn Agroecosystem: Project Number 107.
Unpublished study prepared by The Institute of Wildlife & Environmental Toxicology. 753 p.
MRID 41475802. Rhodes J., and McAllister W. 1990. Early Life Stage Toxicity of [Carbon 14]-
AC 92,100 to the Rainbow Trout (Oncorhynchus mykiss) under Flow-through Conditions: Final
Report # 37913. Unpublished study prepared by Analytical Bio-Chemistry Laboratories, Inc. 648
P-
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2015. Registration review: Ecological risk assessment for terbufos. Office of Pesticide
Programs. Washington, D.C. September 15, 2015.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and the Clean Water Act
(CWA). EPA-820-D-24-002.
149
-------
1.3 Data Insufficient Pesticides
1.3.1 Comparison of Aquatic Life Toxicity Values for Methamidophos: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) for methamidophos Data were gathered by the EPA in 2015 and were
also obtained from the OPP registration review document for methamidophos (U.S. EPA 2008).
1.3.1.1 Methamidophos Acute Toxicity Data
Acute data were gathered by the EPA in 2015 and were also obtained from the OPP registration
review document for methamidophos (U.S. EPA 2008; See Table 1). The data review identified
five LCsos for three species representing three genera that were classified as "quantitative" data.
Four additional 48-hour LC50S for Daphnia magna were classified as qualitative. Three LCsos
had standard duration (48-hr) and higher purity (>99% a.i. vs. 72-74% a.i. for the quantitative
tests), and were classified as qualitative because water chemistry was not reported, control
mortality was unknown, and specific test concentrations were not reported. The fourth (27 |ig/L)
was classified as qualitative because it was tested at 24°C but included here because it was a
standard duration test included in the OPP document. Two additional 96-hour LC50 for bluegill
(Lepomis macrochirus) were classified as qualitative. One was a static test with insufficient
information, and the other used polyethylene liners in test chambers. Both were included in the
OPP document. A 96-hour LC50 for the common carp (Cyprinus carpio) was classified as
qualitative because "chronic impacts observed by 48 hours", but included here because it was
used to fulfill an MDR group.
The final acute methamidophos dataset consisted of 12 LCsos for four species across four genera,
of which one was an invertebrate species. The invertebrate SMAV and GMAV for (Daphnia
magna) is listed in Table 2.
150
-------
Table 1. Acute toxicity data of methamidophos to fres
lwater aquatic organisms.
()\\
MIJR
(iroup'1
(Ion us
Species
I.C50/
IX 50
(M8/I-)
S\1 AY
(MB/I-)
(IMAY
(fili/l)
Reference
Comment
D
Daphnia
magna
26.00
MRID 00041311. Nelson
andRoney. 1979
Quantitative, 74% a.i.
D
Daphnia
magna
50.00
MRID 00014110. Wheeler.
1978
Quantitative, 72% a.i.
D
Daphnia
magna
33.66
ECOTOX 99572. Lin et al.
2006.
Qualitative, >99.0 a.i., Basic water chemistry not
reported; control mortality unknown; chemical
application rates not reported; monitoring of
concentrations not reported; test solution not
described
D
Daphnia
magna
33.46
32.74
32.74
ECOTOX 99572. Lin et al.
2006.
Qualitative, >99.0 a.i., Basic water chemistry not
reported; control mortality unknown; chemical
application rates not reported; monitoring of
concentrations not reported; test solution not
described
D
Daphnia
magna
235.5
ECOTOX 99572. Lin et al.
2006.
Qualitative, >99.0 a.i., Basic water chemistry not
reported; control mortality unknown; chemical
application rates not reported; monitoring of
concentrations not reported; test solution not
described
D
Daphnia
magna
27.00
MRID 00014305. Nelson
and Burke. 1977.
Qualitative, 74% a.i., Classified by OPP. Test
temperature 24°C
A
Oncorhynchus
mykiss
25,000
35,707
35,707
MRID 00041312. Nelson
andRoney. 1979.
Quantitative, 74% a.i.
A
Oncorhynchus
mykiss
51,000
MRID 00014063. Schoenig.
1968.
Quantitative, 75% a.i.
C
Cyprinus
carpio
68,000
68,000
68,000
MRID 05008361. Further
reference information is not
available.
Qualitative, 75% a.i., Classified by OPP. Chronic
impacts observed by 48 hours
B
Lepomis
macrochirus
34,000
MRID 00041312. Nelson
andRoney. 1979.
Quantitative, 74% a.i.
B
Lepomis
macrochirus
45,000
41,287
41,287
MRID 44484402. USEPA.
1977.
Qualitative, 75.4% a.i., Classified by OPP. Static
jar study with insufficient environmental
information
B
Lepomis
macrochirus
46,000
MRID 00014063. Schoenig.
1968.
Qualitative, 75% a.i., Classified by OPP.
Polyethylene liners used in test
151
-------
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish,
etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
152
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 13 |ig/L, which is V2 of the Daphnia magna LC50 of 26
Hg/L.
The OPP fish acute benchmark is 12,500 |ig/L, which is V2 of the Oncorhynchus mykiss LC50 of
25,000 |ig/L.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for methamidophos fulfills four MDRs, corresponding to the use of
a Secondary Acute Factor (SAF) of 7. Applying the SAF to the lowest, most sensitive GMAV
(i.e., 36.06 |ig/L for water flea (Daphnia magna), the calculated Secondary Acute Value (SAV)
is 5.151 |ig/L. The Secondary Maximum Criterion (SMC), which is calculated as half the SAV,
is 2.575 |ig/L.
Detailed calculations for the SMC are shown below:
Lowest GMAV
SAF
36.06
—- = 5.151 \ig/L
SAV
~2~
5.151
—— = 2.575 |xg/L
Genus-Level Invertebrate-Only Acute HC05
No genus-level invertebrate acute HC05 could be calculated following the USEPA (1985)
methodology because there was only one invertebrate genus (Table 2).
Table 2. Methamidophos inverte
irate SMAV and GMAV (jug/L)
(Ion us
Species
S\1 AY
(IMAY
CMAY kiink
Daphnia
magna
32.74
32.74
1
SAV =
SAV =
SMC =
SMC =
153
-------
Table 3. Summary and comparison of acute values for methamidophos.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates the OPP value is
ligher than the OW value.
Pesticide
OPP Invertebrate
ALB
(lowest LCso/2)
(Year published,
species)
OW GLI Tier II
value
(# of MDRs filled,
magnitude
relative to ALB)
OW Genus-
level
Invcrtcbratc-
onlv H Cos/2
Notes
Methamidophos
13 ng/L
(2016; Daphnia
magna)
2.58 ng/L
(4 MDRs filled,
5X)
NA
(1 genus)
The Tier II value is approximately
20% of the FIFRA ALB despite both
being based on the same species.
This is because of the Tier II
adjustment factor of 7 was applied to
this dataset, which satisfied 4/8
MDRs.
Figure 1 shows a genus-level sensitivity distribution for the methamidophos dataset. Major
taxonomic groups are delineated by different symbols, and invertebrate genera are identified by
name. Lines denoting the OPP acute benchmark values and GLI Tier II calculated value are
included.
154
-------
100,000.00
10,000.00
QUO
3
l/l
0
-C
Q.
*E
(0
-C
4->
01
1,000.00
100.00
10.00
1.00
• Arthropod
~
¦ Salmonid Fish
¦ D
~ Other Fish
~ Other Fish (Qualitative)
OPP Fish Benchmark= 12,500 pg/L
OPP Invert. Benchmark
- ¦ - OPP Fish Benchmark
GLI Tier II
i Daphnia
0.0
0.1
0.2
0.3
Genus-level Invertebrate HC05/2 could not be calculated
OPP Invertebrate Benchmark = 13 pg/L
GLI Tier II Acute Value =2.58 pg/L
0.4
0.5
0.6
0.7
0.8
0.9
1.0
Sensitivity Centile
Figure 1. Methamidophos genus-level acute SD.
Symbols represent GMAVs calculated using all available data from the 2015 EPA literature search, supplemented with the OPP
registration review document for methamidophos (U.S. EPA 2008).
155
-------
1.3.1.2 Methamidophos Chronic Toxicity Data
Chronic data were gathered by the EPA in 2015 and combined with the OPP registration review
document for methamidophos (U.S. EPA 2008). The final chronic methamidophos dataset
consisted of one NOEC and one LOEC for a single species, which was an invertebrate (Table 4).
Table 4. Chronic toxicity data of methamidophos to freshwater aquatic organisms.
o\\
MDR
Croup'
(Ion us
Species
NOW
(M8/U
I.OIX
Knilpoinl
Reference
Comment
D
Daphnia
magna
4.490
5.320
Dry weight,
immobility and
reproduction
MRID
46554501. Kern
et al. 2005
Quantitative /
Supplemental
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 4.5 |ig/L, which is the NOEC for Daphnia magna.
The OPP fish chronic benchmark is 173.6 |ig/L, which is the estimated NOEC for Oncorhynchus
mykiss. The 0. mykiss NOEC was extrapolated by dividing the most sensitive acute 96-h LC50
for rainbow trout (25,000 |ig/L) by 144 (highest rainbow trout ACR for organophosphates).
GLI Tier II Chronic Value Calculation
Paired quantitative chronic and acute toxicity data for methamidophos were available for the
water flea, Daphnia magna. The paired acute and chronic D. magna data enabled the calculation
of one ACR. The remaining two ACRs were fulfilled by the default value of 18. The acute and
chronic tests were conducted in different laboratories using water of different physical
characteristics; therefore, OPP's approach was used to calculate the ACR. OPP's approach
involves the use of the NOAEC in the calculations. The calculated Secondary Chronic Value
(SCV) for methamidophos is 0.418 |ig/L.
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = a/5.791 * 18 * 18 = 12.33
SCV =
SACR
5.151
scv=im=0AlsM/L
156
-------
Table 6. Summary and comparison of chronic values for methamidophos.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates the OPP value is hig
ier than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II
value
(#of ACRs
filled, magnitude
relative to ALB)
OW Invertebrate-
only HCos
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Methamidophos
4.5 (ig/L
(2016, Daphnia
magna)
0.42 (ig/L
(GLI Tier II; 1
ACR, 11X)
NA
Two default ACRs of 18
used to derive GLI Tier
II value.
1.3.1.3 Methamidophos References
ECOTOX 99572. Lin K., Zhou S., Xu C., Liu W. 2006. Enantiomeric Resolution and Biotoxicity
of Methamidophos. J Agric Food Chem 54(21): 8134-8138.
MRID 00014063. Schoenig, G. 1968. Report to Chevron Chemical Company, Ortho Division:
Four-Day Fish Toxicity Study on Monitor (RE-9006) 75% Technical SX-171:IBT No. A6482.
(Unpublished study received Mar 5, 1970 under 0F0956; prepared by Industrial Bio-Test
Laboratories, Inc., submitted by Chevron Chemical Co., Richmond, Calif.; CDL:093265-W).
MRID 00014110. Wheeler, R.E. 1978. 48 Hour Acute Static Toxicity of Monitor (SX887) to 1st
Stage Nymph Water Fleas (Daphnia magna Straus). (Unpublished study received Sep 15, 1978
under 239-2404; submitted by Chevron Chemical Co., Richmond, Calif.; CDL:235153-A).
MRID 00014305. Nelson, D.L.; Burke, M.A. 1977. Acute Toxicity of Vi(R) Monitor Technical
to Daphnia magna: Report No. 54045. (Unpublished study received Mar 27, 1978 under 3125-
280; submitted by Mobay Chemical Corp., Agricultural Div., Kansas City, Mo.; CDL: 238096-
C.
MRID 00041311. Nelson, D.L.; Roney, D.J. 1979 Acute Toxicity of Monitor Vi(R) Technical to
Bluegill and Rainbow Trout: Report No. 67739. (Unpublished study received Mar 19, 1980
under 3125-280; submitted by Mobay Chemical Corp., Kansas City, Mo.; CDL:242410-C).
MRID 00041312. Nelson, D.L.; Roney, D.J. 1979 Acute Toxicity of Monitor Vi(R) Technical to
Bluegill and Rainbow Trout: Report No. 67739. (Unpublished study received Mar 19, 1980
under 3125-280; submitted by Mobay Chemical Corp., Kansas City, Mo.; CDL:242410-C).
MRID 05008361. Chin, Y. N. and K. I. Sudderuddin. 1979. Effect of methamidaphos on the
growth rate and esterase activity of the common carp Cyprimts carpio. Environmental Pollution
18(3): 213-220.
MRID 44484402. United States Environmental Protection Agency. 1977. Biological Report of
Analysis: Bluegill: Monitor 75.39%: Lab Project Number: TSD 1.206. Unpublished study. 6 p.
MRID 46554501. Kern, M.E., and C.V. Lam. 2005. Chronic Toxicity of Methamidophos to the
Daphnia magna Under Flow-Through Conditions. Unpublished study performed by Bayer Crop
157
-------
Science, Stilwell, KS. Laboratory Study No. EBTAX016. Study submitted by Bayer
CropScience, Research Triangle Park, NC. Study initiated November 3, 2004 and submitted
April 6, 2005.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2008. Registration review. Ecological risk assessment problem formulation for:
methamidophos. Office of Pesticide Programs. Washington, D.C. September 29, 2008.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
158
-------
1.3.2 Comparison of Aquatic Life Toxicity Values for Profenofos: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) for profenofos were gathered by the EPA in 2015 and were also
obtained from the OPP registration review document for profenofos (U.S. EPA 2008).
1.3.2.1 Profenofos Acute Toxicity Data
Acute data were gathered by the EPA in 2015 and were also obtained from the OPP registration
review document for profenofos (U.S. EPA 2008; See Table 1). Six LCsos for five species
representing five genera that were classified as "quantitative" data. Five LCsos for four
invertebrate species across three genera were classified as qualitative and are included here to
allow for a sufficient sample size to calculate an invertebrate genus-level HCos.
One 48-hour LCso for Chironomusplumosus classified as qualitative because of duration used to
fulfill an MDR group. One 48-hour LCso for Ceriodaphnia dubia classified as qualitative
because water quality characteristics were not reported and potential exposure from feeding may
have occurred. Three 24-hour LCsos for two species of Culex classified as qualitative because of
duration. One 96-hour LCsos for fathead minnow Pimephalespromelas classified as qualitative
because control mortality was not reported and feeding may have occurred. One 96-hour LCso
for the Western mosquitofish Gambusia affinis classified as qualitative because source water was
unknown and control mortality was not reported.
The final acute profenofos dataset consisted of 13 LCsos for 11 species representing 10 genera, of
which six were invertebrate species representing five invertebrate genera. Ranked invertebrate
GMAVs are listed in Table 2.
159
-------
Table 1. Acute toxicity data of profenofos to freshwater aquatic organisms.
()\\
MDR
(iroup-1
(Ion us
Species
IX 50/
I X 50
(Mli/I.)
S\1 AY
(M8/U
(IMAY
(M8/U
Reference
Comment
D
Ceriodaphnia
dubia
0.039
0.039
0.04
ECOTOX 158195; Woods et al.
2002
Qualitative, water quality characteristics
not reported; potential exposure from
feeding; source water type unknown
D
Daphnia
magna
1.400
1.14
1.14
ECOTOX 6797; Mayer and
Ellersieck. 1986
Quantitative
D
Daphnia
magna
0.930
MRID 416273-04; Bellantoni.
1990
Quantitative
F
Culex
pipiens pallens
73
73.010
28.67
ECOTOX 61915; Lee et al. 1997
Qualitative
F
Culex
quinquefasciatus
5.13
11.26
ECOTOX 63336; Kasai et al.
1998
Qualitative
F
Culex
quinquefasciatus
24.7
ECOTOX 63336; Kasai et al.
1998
Qualitative
E
Gammarus
pseudolimnaeus
0.800
0.800
0.80
ECOTOX 6797; Mayer and
Ellersieck. 1986
Quantitative
F
Chironomus
plumosus
1.000
1.000
1.00
ECOTOX 6797; Mayer and
Ellersieck. 1986
Qualitative, duration
A
Oncorhynchus
mykiss
23.50
23.50
23.50
ECOTOX 6797; Mayer and
Ellersieck. 1986
Quantitative
C
Pimephales
promleas
316.4
316.4
316.4
ECOTOX 68287; Baer et al.
2002
Qualitative, Dechlorinated tap water used;
nominal; control mortality not reported;
possible feeding during test
C
Gambusia
affinis
633.6
633.6
633.6
ECOTOX 100565; Rao et al.
2006
Qualitative, Control mortality unknown;
source water
B
Lepomis
macrochirus
13.50
13.50
13.50
ECOTOX 6797; Mayer and
Ellersieck. 1986
Quantitative
C
Ictalurus
punctatus
18.00
18.00
18.00
ECOTOX 6797; Mayer and
Ellersieck. 1986
Quantitative
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish,
etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
160
-------
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
161
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 0.465 |ig/L, which is V2 of the lowest Daphnia magna
LC50 of 0.930 |ig/L.
The OPP fish acute benchmark is 7.05 |ig/L, which is V2 of the Lepomis macrochirus LC50 of
14.1 |ig/L as it is reported in the OPP document. The value listed (14.1) is based on nominal
concentration and is listed as a measured concentration (13.5) in Table 1.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for profenofos fulfills six of the eight MDRs, corresponding to the
use of a SAF of 5.2. Applying the SAF to the lowest, most sensitive GMAV (i.e., 0.800 |ig/L for
scud (Gammaruspseudolimnaeus), the calculated Secondary Acute Value (SAV) is 0.154 |ig/L.
The SMC, which is calculated as half the SAV, is 0.077 |ig/L. Detailed calculations for the SMC
are shown below:
Lowest GMAV
0.800
SAV = -^-= 0.154 \ig/L
SAV
SMC =
2
0.154
SMC = —— = 0.077 \ig/L
Genus-Level Invertebrate-Only Acute HC05
No genus-level invertebrate acute HC05 could be calculated following the USEPA (1985)
methodology, as there was only two invertebrate genera with quantitative data (Table 2).
Table 2. Profenofos invertebrate SMAVs and G
MAVs (jig/L).
(Ion us
Species
S\1 AY
(IMAY
CMAY kit 11k
Daphnia
magna
1.141
1.141
2
Gammarus
pseudolimnaeus
0.8000
0.8000
1
162
-------
Table 3. Summary and comparison of acute values for profenofos.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(lowest LCso/2) (Year
published, species)
OW GLI Tier II value
(# of IMDRs filled,
magnitude relative to
ALB)
OW Genus-level
Invertebrate-
only HCos/2
Notes
Profenofos
0.465 ng/L
(2008; Daphnia
magna)
0.077 ng/L
(6 MDRs filled, 6X)
NA
(2 genera)
The FIFRA ALB is higher
because the GLI Tier II value
is based on G. pseudolimnaeus
test in the open literature with
a lower LC50.
Figure 1 shows a genus-level sensitivity distribution for the profenofos dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values and GLI Tier II calculated acute value are included.
163
-------
1,000.000 -|
100.000
10.000
CUD
3.
10
o
H—
o
£
£
o
1.000
0.100
0.010
0.001
•
Arthropod
o
Arthropod (Qualitative)
¦
Salmonid Fish
~
Other Fish
~
Other fish (Qualitative)
OPP Invert. Benchmark
OPP Fish Benchmark
GLI Tier II Acute Value
Gammarus •
O Ceriodaphnia
~
Chironomus
O • Daphnia
O Culex
OPP Fish Benchmark = 7.05 pg/L
OPP Invertebrate Benchmark = 0.465 ^ig/L
GLIT Tier II Acute Value =0.077 pg/L
Genus-level Invertebrate cannot be calculated
0.0
0.1
0.2
0.3 0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Profenofos genus-level SD.
Symbols represent GMAVs calculated using all available data from the 2015 EPA literature search, supplemented with the OPP
registration review document for profenofos (U.S. EPA 2015).
164
-------
1.3.2.2 Profenofos Chronic Toxicity Data
Chronic data were gathered by the EPA in 2015 and supplemented with the OPP registration
review document for profenofos (U.S. EPA 2015). The final chronic profenofos dataset consisted
of two NOECs/LOECS for two species across two genera, of which one was an invertebrate and
one was a vertebrate (Table 5).
Table 5. Chronic toxicity data of profenofos to freshwater aquatic organisms
()\\
MDR
C> roil p'
(.onus
Species
Nor.c
I.OIX
(flii/l.)
I'lmlpoini
KiTciyiiit
( (Mil 111011 (
D
Daphnia
magna
0.2
0.33
Survival of
parent and
offspring
MRID 000859-64;
LeBlanc and
Suprenant 1980
Quantitative
B
Pimephales
promelas
2.0
4.4
Not defined
MRID 000859-58;
LeBlanc et al. 1979
-
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 0.2 |ig/L, which is the NOEC for Daphnia magna.
The OPP fish chronic benchmark is 2.0 |ig/L, which is the NOEC for Pimephalespromelas.
GLI Tier II Chronic Value Calculation
Quantitative chronic toxicity data and an analogous acute test for profenofos are available for the
water flea, Daphnia magna, enabling the calculation of one ACR. The default value of 18 was
used to fulfill the second and third ACRs. The acute and chronic tests for water flea (Daphnia
magna) were conducted in different laboratories using water of different physical characteristics;
therefore, OPP's approach was used to calculate the ACR, which involves the use of the NOAEC
in the calculation. The calculated SCV for profenofos is 0.013 |ig/L. Detailed calculations for the
SCV are shown below:
= Geometric Mean of the ACRs
= 3V4.650* 18* 18 = 11.46
SAV
SACR
SACR :
SACR :
SCV =
165
-------
0.154
SCV = U46 = 0'013 Vi9/L
Table 6. Summary and comparison of chronic values for profenofos.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 inc
icates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II value
(# of ACRs filled,
magnitude relative to
ALB)
OW Invertebrate-only
HCos
(# of ACRs filled,
magnitude relative to
ALB)
Notes
Profenofos
0.2 ng/L
(2016, Daphnia
magna)
0.013 ng/L
(GLI Tier II; 1 ACR,
15X)
NA
Two default ACRs of
18 used to derive
GLI Tier II value.
1.3.2.3 Profenofos References
ECOTOX 100565. Rao, J.V., Begum, G., Jakka, N.M., Srikanth, K., and Rao, R.N. 2006.
Sublethal Effects of Profenofos on Locomotor Behavior and Gill Architecture of the Mosquito
Fish, Gambusia affinis. Drug Chem. Toxicol. (N.Y.) 29(3): 255-267.
ECOTOX 158195. Woods, M., Kumar, A., and Correll, R. 2002. Acute Toxicity of Mixtures of
Chlorpyrifos, Profenofos, and Endosulfan to Ceriodaphnia dubia. Bull. Environ. Contam.
Toxicol. 68(6): 801-808.
ECOTOX 61915. Lee, D.K., Shin, E.H., and Shim, J.C. 1997. Insecticide Susceptibility of Culex
pipiens pallens (Culicidae, Diptera) Larvae in Seoul. Korean J. Appl. Entomol. 27(1): 9-13.
ECOTOX 63336. Kasai, S., Weerashinghe, I.S., and Shono, T. 1998. P450 Monooxygenases are
an Important Mechanism of Permethrin Resistance in Culex quinquefasciatus Say Larvae. Arch.
Insect Biochem. Physiol. 37(1): 47-56.
ECOTOX 6797. Mayer, F.L.J, and Ellersieck, M.R. 1986. Manual of Acute Toxicity:
Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals. Resour.
Publ. No. 160, U.S. Department of Interior, Fish and Wildlife Services, Washington, DC 505 p.
ECOTOX 68287. Baer, K.N., Olivier, K, and Pope, C.N. 2002. Influence of Temperature and
Dissolved Oxygen on the Acute Toxicity of Profenofos to Fathead Minnows (Pimephales
promelas). Drug Chem. Toxicol. (N.Y.) 25(3): 231-245.
MRID 000859-58. LeBlanc, G.A., Hoberg, J.R, and Dean, J.W. (1979) The Toxicity of CGA-
15324 to Fathead Minnow (Pimephales promelas) Eggs and Fry: Report #BW-79-6-490.
(Unpublished study received Nov 6, 1981 under 100-598; prepared by EG & G, Bionomics,
submitted by Ciba- Geigy Corp., Greensboro, N.C.; CDL:246216-L).
MRID 000859-64. LeBlanc and Surprenant. 1980. Acute toxicity of priority pollutants to water
flea (Daphnia magna). Bulletin of Environmental Contamination and Toxicology. Volume 24,
Issue 1, pp 684-691.
166
-------
MRID 416273-04. Bellantoni, D.C. 1990. Profenofos Technical: A 48-Hour Static Acute
Toxicity Test with the Cladoceran (Daphnia magna). Laboratory Study No. 108A-106. Prepared
by Wildlife International Ltd., Easton, MD. Submitted by Agricultural Division, Ciba-Geigy
Corporation, Greensboro.
Mayer, F.L.J, and Ellersieck, M.R. 1986. Manual of Acute Toxicity: Interpretation and Data
Base for 410 Chemicals and 66 Species of Freshwater Animals. Resour. Publ. No. 160, U.S.
Department of Interior, Fish and Wildlife Services, Washington, DC 505 p.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2008. Problem formulation for the environmental fate, ecological risk, endangered
species, and drinking water assessments in support of the registration review of profenofos.
Office of Pesticide Programs. Washington, D.C. March 31, 2008.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
167
-------
1.3.3 Comparison of Aquatic Life Toxicity Values for Fenpropathrin: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) for fenpropathrin were gathered by OW in 2015 and combined with
data from the OPP document on which the benchmark values are based (U.S. EPA 2010) and
information in an OPP (Sayer 2016) memo reviewing studies submitted in support of the
fenpropathrin review was also considered below.
1.3.3.1 Fenpropathrin Acute Toxicity Data
Acute fenpropathrin data were gathered by OW in 2015. The OPP document on which the
benchmark values are based (U.S. EPA 2010) and an OPP (Sayer 2016) memo reviewing studies
submitted in support of the fenpropathrin review were also included in the data gathering (See
Table 1). Four LCsos representing four species in four genera were identified and classified as
"quantitative" data. A 96-hour LCso for rainbow trout (Oncorhynchus mykiss) was identified and
classified as qualitative because it was an 89% a.i. solution but considered acceptable in the OPP
document. Two 24-hour LCsos for the Southern house mosquito (Culex quinquefasciatus)
classified as qualitative for multiple reasons (duration, concentrations used not reported, control
not reported, source of organisms unknown, tap water used), but included here to increase the
number of invertebrate genera. Additionally, a review of studies submitted in support of a
registration review was examined (Sayer 2016), and an acceptable 96-hour LCso for the
amphipod species, Hyalella azteca, was added.
The final acute fenpropathrin dataset consisted of eight LCsos for seven species across seven
genera, of which three were invertebrate species representing three invertebrate genera. Ranked
invertebrate GMAVs are listed in Table 2.
168
-------
Table 1. Acute toxicity data of fenpropathrin to freshwater aquatic organisms.
()\\
MDR
(iioup'
(Ion us
Species
I.C50/
I X 50
(MS/I.)
S\1 AY
(MS/'-)
(IMAY
(M8/U
Reference
Comment
D
Daphnia
magna
0.530
0.53
0.53
MRID 249939
Quantitative
E
Hyalella
azteca
0.00305
0.00305
0.00305
MRID 49209502. Bradley. 2013.
F
Culex
quinquefasciatus
0.27000
0.6148
0.6148
ECOTOX 10971
Qualitative: Duration, tap water,
static, concentrations not reported,
control mortality not reported (larvae)
F
Culex
quinquefasciatus
1.40000
ECOTOX 10971
Qualitative: Duration, tap water,
static, concentrations not reported,
control mortality not reported (pupae)
A
Oncorhynchus
mykiss
2.3
2.30
2.30
MRID 249939
Qualitative, 89% a.i.
MRID 41525901. Dionne and
B
Pimephales
promelas
2.370
2.37
2.37
Suprenant. 1990
MRID 42360001. Dionne and
Suprenant. 1992
Quantitative
B
Lepomis
macrochirus
2.200
2.20
2.20
MRID 249939
MRID 00127791
Quantitative
B
Ictalurus
punctatus
5.500
5.50
5.50
MRID 249939
Quantitative
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish,
etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
169
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 0.0015 |ig/L, which is V2 of the Hyalella azteca LC50
of 0.00305 |ig/L.
The OPP fish acute benchmark is 1.1 |ig/L, which is V2 of the Lepomis macrochirus LC50 of 2.2
^g/L-
GLI Tier II Acute Value Calculation
The acceptable acute dataset for fenpropathrin fulfills five of the eight MDRs, corresponding to
the use of a SAF of 6.1. Applying the SAF to the lowest, most sensitive GMAV (i.e.,
0.00305|ig/L for Hyalella azteca), the calculated SAV is 0.0005 |ig/L. The SMC, which is
calculated as half the SAV, is 0.00025 |ig/L.
Detailed calculations for the SMC are shown below:
Lowest GMAV
0.00305
SAV = = 0.0005 ag/L
6.1
SAV
SMC= —
0.0005
SMC = —-— = 0.00025 |xg/L
Genus-Level Invertebrate Acute HC05
No genus-level invertebrate acute HC05 could be calculated using the USEPA (1985)
methodology because there were only three invertebrate genera (Table 2).
Table 2. Fenpropathrin invertebrate SMAVs and GMAVs (^ig/L).
(iOIIIIS
Speck's
SMAY
CMAY
CMAY Kiink
Culex
quinquefasciatus
6.148
6.148
3
Daphnia
magna
0.5300
0.5300
2
Hyalella
azteca
0.00305
0.00305
1
Note: The Culex GMAV is based on data classified as qualitative that was included to increase the number of
invertebrate genera.
170
-------
Table 3. Summary and comparison of acute values for fenpropathrin.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP
Invertebrate
ALB
(lowest
LCso/2) (Year
published,
species)
OW GLI Tier II
value
(# of MDRs
filled,
magnitude
relative to ALB)
OW Genus-
level
Invcrtcbratc-
onlv H Cos/2
Notes
Fenpropathrin
(Synthetic
Pyrethroid)
0.0015 ng/L
(2021;
Hyalella
azteca)
0.00025 ng/L
(5 MDRs filled,
6X)
NA
(2 genera)
The GLI Tier II value is lower than the
FIFRA ALB despite both being based
on the same species. This is because of
the Tier II adjustment factor of 6.1 was
applied to this dataset, which satisfied
5/8 MDRs.
Figure 1 shows a genus-level sensitivity distribution for the fenpropathrin dataset. Major
taxonomic groups are delineated by different symbols, and invertebrate genera are identified by
name. Lines denoting the OPP acute benchmark values and the GLI Tier II calculated value are
included.
171
-------
10.000
1.000
US
3 0-100
.£
JE
4-»
m
a,
o
•
Arthropod
o
Arthropod (Qualitative)
¦
Salmonid Fish
~
Other Fish
OPP Invert. Benchmark
OPP Fish Benchmark
-GLI Tier il Acute Value
Q.
C
V
0.010
0.001
Daphnia
Hyalella
O Culex
OPP Fish Benchmark = 1.1 jig/L
Genus-level Invertebrate HC05/2 could not be calculated
OPP Invertebrate Benchmark = 0,0015 fig/L
GLI Tier II Acute Value = 0.00025 (ig/L
0.000
0.0
0.1
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Fenpropathrin genus-level acute SD.
Symbols represent GMAVs calculated using all available data from the EPA 2015 literature search supplemented with the OPP
registration review document for fenpropathrin (U.S. EPA 2010, Sayer 2016).
172
-------
1.3.3.2 Fenpropathrin Chronic Toxicity Data
Chronic fenpropathrin data were gathered by OW in 2015 and combined with data from the OPP
document on which the benchmark values are based (U.S. EPA 2010) and information in an OPP
(Sayer 2016) memo reviewing studies submitted in support of the fenpropathrin review was also
considered below.
The final chronic fenpropathrin dataset consisted of five NOECs/LOECS for four species across
four genera, of which three were invertebrate genera and one was a vertebrate genus (Table 4).
Table 4. Chronic toxicity data of fenpropathrin to freshwater aquatic organisms
OW
MIJR
(ll'Olip'1
(Ionus
Species
NOEC
(MS/I-)
I.OIX
(MS/'-)
Knilpoinl
Reference
Comment
D
Daphnia
magna
0.064
0.350
100% mortality at 0.350 |ig/L:
prior to mortality, significant
decrease in fecundity (mean
young/adult/reproduction day)
MRID 259678
Quantitative
E
Hyalella
azteca
0.004
0.0101
Survival
MRID 49243301
Acceptable
E
Hyalella
azteca
<0.0015
0.0015
Growth (length)
MRID 49368102
Supplemental
- qualitative
F
Chironomus
dilutus
0.00578
0.01494
Emergence rate
MRID 49316005
Acceptable
B
Pimephales
promelas
0.06
0.091
Not reported
MRID 41525901
Supplemental
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is <0.0015 |ig/L, which is the NOEC for Hyalella
azteca.
The OPP fish chronic benchmark is 0.6 |ig/L, which is the NOEC for Pimephalespromelas.
GLI Tier II Chronic Value Calculation
The acceptable dataset includes paired quantitative chronic and acute toxicity data for water flea
(Daphnia magna), allowing for the calculation of one ACR. The GLI Tier II default value of 18
was used for the second and third ACRs. The acute and chronic water flea (Daphnia magna)
tests were conducted in different laboratories using water of different physical characteristics;
therefore, OPP's approach was used to calculate the ACRs. The Office of Pesticide Program's
approach involves the use of the lowest (i.e., most sensitive) NOAEC for a given species in the
173
-------
ACR calculations. The calculated SCV for fenpropathrin is 0.000036 |ig/L. Detailed calculations
for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = V8.281 * 18 * 18 = 13.90
SCV =
SACR
0.0005
SCV = "l390" = 0-000036
Table 5. Summary and comparison of chronic values for fenpropathrin.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates the OPP value is hig
ier than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II
value
(# of ACRs
filled, magnitude
relative to ALB)
OW Invertebrate-
only HCos
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Fenpropathrin
<0.0015 (ig/L
(2021, Hyalella
azteca)
0.000036 ng/L
(GLI Tier II; 1
ACR, 42X)
NA
Two default ACRs of 18
used to derive GLI Tier
II value.
1.3.3.3 Fenpropathrin References
ECOTOX 10971. Mulla,M.S., H.A. Darwazeh, andL. Ede. 1982. Evaluation of New Pyrethroids
Against Immature Mosquitoes and Their Effects on Nontarget Organisms. Mosq. News, 42, (4),
583-590.
MRID 00127791. Acute Toxicity of S-3206 TGto Bluegill, Report #BW-81-8-988 by EG & GI
Bionomics submitted to Sumitomo Chemical Company, August 1981, Acc #249939.
MRID 249939. Acute Toxicity of S-3206 TG to Bluegill, Report #BW-81-8-988 by EG & GI
Bionomics submitted to Sumitomo Chemical Company, August 1981, Acc #249939.
MRID 259678. Forbis, Alan D., David Burgess, and Brenda Bunch. 1985. Chronic Toxicity of
(cyclopropyl-l-14C) fenpropathrin to Daphnia magna Under Plow-through Test Conditions.
Conducted at Analytical Bio-Chemistry Laboratories, Inc. Report # 32547. September 9, 1985.
Submitted to EPA by Sumitomo Chemical America, Inc. Acc. No. 259678.
174
-------
MRID 41525901. Dionne, E. and D.C. Suprenant. 1990. The chronic toxicity of Fenpropathrin to
the Fathead Minnow (Pimephalespromelas). Conducted by Springborn Laboratories, Inc.,
Wareham, Massachusetts. Laboratory Project No. S-2725. Laboratory Study No.
981.0687.6122.122. Submitted by Chevron Chemical Company, Richmond, California.
MRID 42360001. Dionne, E. and D. Suprenant. 1992. The Chronic Toxicity of Fenpropathrin
Fathead minnow (.Pimephales promelas): Supplement to: Lab Project 89-1-2913. Unpublished
study prepared by Springborn Labs., Inc. 328 p.
MRID 49209502. Bradley, M.J. 2013. Fenpropathrin TG - Acute Toxicity to Freshwater
Amphipods (Hyalella azteca) Under Flow-Through Conditions. Unpublished study performed by
Smithers Viscient, Wareham, MA. Laboratory Study No. 13656.6165. Study sponsored by
Pyrethroid Working Group, FMC Corporation, Ewing, NJ. Study initiated March 27, 2012 and
completed July 30, 2013.
MRID 49243301. Picard, C.R. 2013. Fenpropathrin TG - 42-Day Toxicity Test Exposing
Freshwater Amphipods (.Hyalella azteca) to a Test Substance Applied to Sediment Under Static-
Renewal Conditions Following EPA Test Methods. Unpublished study conducted by Smithers
Visient, Wareham, MA. Report No 12709.6335. Study sponsored by Valent USA Corporation,
Walnut Creek, CA Study completed October 15, 2013.
MRID 49316005. Picard, C.R. Life-Cycle Toxicity Test Exposing Midges (Chironomus dilutus)
to Fenpropathrin TG Applied to Sediment under Static-Renewal Conditions Following EPA Test
Methods. Unpublished study conducted by Smithers Visient, Wareham, MA. Report No
12709.6334. Study sponsored by Valent USA Corporation, Walnut Creek, CA Study completed
December 17, 2013.
MRID 49368102. Picard, C.R. 2014. 10-Day Toxicity Test Exposing Freshwater Amphipods
(.Hyalella azteca) to Fenpropathrin Applied to Sediment Under Static-Renewal Conditions
Unpublished study conducted by Smithers Visient, Wareham, MA. Report No 13656.6157.
Study sponsored by Pyrethroid Working Group, Ewing, NJ. Study completed April 3, 2014.
Sayer, A. 2016. Fenpropathrin: Review of ecological studies submitted in support of registration
review. Memorandum to OPP Pesticide Re-evaluation Division. April 9, 2016.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2010. Environmental fate and ecological risk assessment problem formulation in
support of registration review for fenpropathrin. Office of Pesticide Programs. Washington, D.C.
June 16, 2010.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
175
-------
1.3.4 Comparison of Aquatic Life Toxicity Values for Fenbutatin Oxide: Data Sources
and Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) for fenbutatin oxide were gathered by OW in 2015 and combined with
data obtained from the OPP registration review document for fenbutatin oxide (U.S. EPA 2009).
1.3.4.1 Fenbutatin Oxide Acute Toxicity Data
Acute fenbutatin oxide data were gathered by the EPA in 2015 and were also obtained from the
OPP registration review document for fenbutatin oxide (U.S. EPA 2009; See Table 1). Six LCsos
representing three species in three genera were identified and classified as "quantitative" data.
One 24-hour LCso for an unidentified insect species in the family Chironomidae was classified as
qualitative but included here to increase the number of invertebrate genera. The Chironomidae
test was classified as qualitative because of a non-standard exposure duration, the unidentified
species, and the non-definitive (>4,400 ng/L) LCso test result.
The final acute fenbutatin oxide dataset consisted of seven LCsos for four species across four
genera, of which two were invertebrate species representing two invertebrate genera. Ranked
invertebrate GMAVs are listed in Table 2.
176
-------
Table 1. Acute toxicity data of fenbutai
in oxide to freshwater aquatic organisms.
()\\
MDR
(iioup'
liimilv
(Ionus
Species
IX 50/
I X 50
(uii/l.)
S\1 AY
(MS/'-)
(IMAY
(MS/'-)
Reference
D
Daplmiidae
Daplmia
magna
31.UU
31.00
31.00
MRU) 4u4~3509. lluUon. 198"
F
Chironomidae
-
-
>4,400
>4,400
>4,400
MRID 47910407. Picard. 2005
A
Salmonidae
Oncorhynchus
mykiss
1.700
2.773
2.773
MRID 40098001. ECOTOX 6797. Mayer and Ellersieck. 1986.
A
Salmonidae
Oncorhynchus
mykiss
1.900
MRID 00113075. Johnson. 1973
A
Salmonidae
Oncorhynchus
mykiss
6.600
MRID 40473506. Hutton. 1987
B
Centrarchidae
Lepomis
macrochirus
4.800
4.800
4.800
MRID 40098001. ECOTOX 6797. Mayer and Ellersieck. 1986
B
Centrarchidae
Lepomis
macrochirus
4.800
MRID 00113076. Johnson and Jones. 1971
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish,
etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
177
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 15.5 |ig/L, which is V2 of the Daphnia magna LC50 of
31.00 |ig/L.
The OPP fish acute benchmark is 0.85 |ig/L, which is V2 of the Oncorhynchus mykiss LC50S of
1.7|ig/L.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for fenbutatin oxide fulfills three of the eight MDRs, corresponding
to the use of a SAF of 8. Applying the SAF to the lowest, most sensitive GMAV (i.e., 2.773 |ig/L
for rainbow trout (Oncorhynchus mykiss), the calculated SAV is 0.347 |ig/L. The SMC, which is
calculated as half the SAV, is 0.173 |ig/L.
Detailed calculations for the SMC are shown below:
Lowest GMAV
2.773
SAV = —— = 0.347 |xg/L
O
SAV
SMC= —
0.347
SMC = —= 0.173 |xg/L
Genus-Level Invertebrate-only Acute HC05
No genus-level invertebrate acute HC05 could be calculated following the USEPA (1985)
methodology because there were only two invertebrate genera (Table 2).
Table 2. Fenbutatin oxide invertebrate SMAVs and GMAVs (iig/L).
(Ion us
Species
S\1 AY
(IMAY
linerlehnile
CMAY kit 11k
I uiuiIn Cliii'oiioniidae
4,4UU
4,400
Daphnia
magna
31.00
31.00
1
Note: The Family Chironomidae GMAVs is based on data classified as qualitative that was included to increase the
number of invertebrate genera.
178
-------
Table 3. Summary and comparison of acute values for fenbutatin oxide.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP Most Sensitive
ALB
(lowest LCso/2) (Year
published, species)
OW GLI Tier II
value
(# of IMDRs filled,
magnitude relative to
ALB)
OW Genus-level
Invcrtcb rate-only
HCos/2
Fenbutatin Oxide
(Organotin Acaricide)
0.85 ng/L
(2009; Oncorhynchus
mykiss)
0.173 ng/L
(3 MDRs filled, 4.9X)
NA
(1 genus)
Figure 1 shows a genus-level sensitivity distribution for the fenbutatin oxide dataset. Major
taxonomic groups are delineated by different symbols, and invertebrate genera are identified by
name. Lines denoting the OPP acute benchmark values and GLI Tier II calculated acute value
are included.
179
-------
10,000.00
1,000.00
cuo
0)
¦O
X.
O
c
IT!
¦M
3
-Q
C
-------
1.3.4.2 Fenbutatin Oxide Chronic Toxicity Data
Data were gathered by the EPA in 2015, supplemented with the OPP registration review
document for fenbutatin oxide (U.S. EPA 2015). The final chronic fenbutatin oxide dataset
consisted of two NOECs/LOECS for two species across two genera, of which one was an
invertebrate and one was a vertebrate (Table 4).
o\\
MDR
Croup'1
(Ion us
Species
NOIX
(MS/I-)
Loi:c
(MS/I-)
Knilpoinl
Reference
Comment
D
Daphnia
magna
16.00
39.00
Reduced growth and
percent survival in
adults and total
number of young
MRID
40525901;
Hutton 1988
Quantitative
A
Oncorhynchus
mykiss
0.310
0.610
Reduced larval
survival and growth
MRID
40473512;
Hutton 1987
Quantitative
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 16 |ig/L, which is the NOEC for Daphnia magna.
The OPP fish chronic benchmark is 0.31 |ig/L, which is the NOEC for Oncorhynchus mykiss.
GLI Tier II Chronic Value Calculation
The dataset of quantitative chronic toxicity data for fenbutatin oxide includes data for rainbow
trout (Oncorhynchus mykiss) and water flea (Daphnia magna). Analogous quantitative acute
tests are available for both species; therefore, two ACRs were calculated. The default value of 18
was used for the third ACR. The acute and chronic tests were conducted in different laboratories
using water of different physical characteristics; therefore OPP's approach was used to calculate
the ACRs. OPP's approach involves the use of the lowest (i.e., most sensitive) NOAEC for a
given species in the ACR calculations. The calculated SCV for fenbutatin oxide is 0.060 |ig/L.
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = V 1.938# 5.484* 18 = 5.761
181
-------
SCV =
SACR
0.347
SCV = 5761 = °-060 ^/L
Table 5. Summary and comparison of chronic values for fenbutatin oxide.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates the OPP value is hig
ier than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II
value
(#of ACRs
filled, magnitude
relative to ALB)
OW Invertebrate-
only HCos
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Fenbutatin Oxide
0.31 ng/L
(2009,
Oncorhynchus
mykiss). Note the
vertebrate ALB is
lower than the
invertebrate ALB (16
Ug/L)
0.06 ng/L
(GLI Tier II; 2
ACRs, 5.IX)
NA
One default ACR of 18
used to derive GLI Tier
II value.
1.3.4.3 Fenbutatin Oxide References
MRID 00113075. Johnson, W. 1973. Acute toxicity of Technical SD14114 to Rainbow Trout
{Oncorhynchus mykiss formerly Scilmo gairdneri). U.S. Fish and Wildlife Service, Fish
Pesticide Research Laboratory; unpublished study. Raw data relayed from W. W.
Johnson (USFWS) to Shell Chemical Com, San Ramon, CA.
MRID 00113076. Johnson, W.; Jones, T. 1971. Static Acute Toxicity of SD 14114 toBluegill.
U.S. Fish and Wildlife Service, Fish-pesticide Research Laboratory; unpublished study;
CDL:098036-I.
MRID 40098001. ECOTOX 6797. Mayer, F. L. J. and Ellersieck, M. R. 1986. Manual of Acute
Toxicity: Interpretation and Data Base for 410 Chemicals and 66 Species of Freshwater Animals.
Resour. Publ. No. 160, U.S. Department of Interior, Fish and Wildlife Services, Washington, DC
505 p.
MRID 40473506. Hutton, D. 1987. Static Acute 96-hour LC50 of Technical Vendex to Rainbow
Trout (Salmo gairdneri): Haskell Laboratory Report No. 327-87: MR 4581-472. Unpublished
study prepared by Haskell Laboratory for Toxicology and Industrial Medicine. 10 p.
MRID 40473509. Hutton, D. 1987. Daphnia magna Static Acute 48-hour EC50 of Technical
Vendex: Haskell Laboratory Report No. 316-87: MR 4581501. Unpublished study prepared by
Dupont Haskell Laboratory for Toxicology and Industrial Medicine. 10 p.
182
-------
MRID 40473512. Hutton, D. 1987. Early Life Stage Toxicity of Technical Vendex to Rainbow
Trout (Salmo gairdneri): Haskell Laboratory Report No. 460-87: MR 4581-472. Unpublished
study prepared by Dupont Haskell Laboratory for Toxicology and Industrial Medicine. 19 p.
MRID 40525901. Hutton, D. 1988. Chronic Toxicity of Technical Vendex to Daphnia magna:
Rept. No. 94-88. Unpublished study prepared by E.I. du Pont de Nemours and Co., Inc. 20 p.
MRID 47910407. Picard, C. R. 2009. Fenbutatin-oxide - 10-Day Toxicity Test Exposing Midge
(Chironomus dilutus) to a Test Substance Applied to Sediment Under Static-Renewal
[Intermittent Flow] Conditions Following OCSPP Draft Guideline 850.1735. Unpublished study
conducted by Springborn Smithers Laboratory, Wareham, MA. Report No.
13845.6122. Sponsored by United Phosphorus, King of Prussia, PA.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2009. Problem formulation for the environmental fate, ecological risk, endangered
species, and drinking water assessments in support of the registration review of fenbutatin-oxide.
Office of Pesticide Programs. Washington, D.C. September 28, 2009.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
183
-------
1.3.5 Comparison of Aquatic Life Toxicity Values for Methoxyfenozide: Data Sources
and Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) for methoxyfenozide were gathered by OW in 2015 and supplemented
with additional values described in the OPP document on which the benchmark values are based
(U.S. EPA 2013).
1.3.5.1 Methoxyfenozide Acute Toxicity Data
Data were gathered by the OW in 2015 and supplemented with additional values described in the
OPP document on which the benchmark values are based (U.S. EPA 2013). One LCso for
Daphnia magna determined to be "quantitative" data. Two 96-hour LCsos for Oncorhynchus
mykiss and Lepomis macrochirus were classified as qualitative because they were greater than
toxicity values used to fulfill MDR groups, but otherwise considered acceptable. A 120-hour
LCso for the mosquito Anophales gambiae was classified as qualitative because of duration,
uncharacterized source water, feeding during the test, and lack of replicates, but was included in
order to increase the number of invertebrate genera.
The final acute methoxyfenozide dataset consisted of four LCsos for four species representing
four genera, of which two were invertebrate species representing two invertebrate genera (Table
1). The invertebrate GMAVs are listed in Table 2.
184
-------
Table 1. Acute toxicity data of methoxyfenozide to freshwater aquatic organisms.
()\\
MDR
(iroup'1
(Ion us
Species
IX 50/
I X 50
(MS/'-)
S\1 AY
(MS/I-)
(IMAY
(Jili/I)
Reference
Comment
D
Daphnia
magna
3,700
3,700
3,700
MRID 44144411; Holmes and
Swigert. 1993
Quantitative
F
Anaphales
gambiae
248
247.70
247.70
ECOTOX 165535; Morou et al.
2013
Qualitative: Duration; fed during experiment;
tests conducted with unknown water type in
plastic cups; no replicates.
A
Oncorhynchus
mykiss
>4,200
>4,200
>4,200
MRID 44144410; Graves and
Swigert. 1995
Qualitative, greater than endpoint
B
Lepomis
macrochirus
>4,300
>4,300
>4,300
MRID 44144409; Graves and
Swigert. 1995
Qualitative, greater than endpoint
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species (e.g., bluegill, channel catfish,
etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
185
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 28.5 |ig/L, which is V2 of the calculated (estimated)
Chironomus riparius acute test value of 57 |ig/L. This acute value for C. riparius was calculated
by multiplying the acute to chronic ratio from studies with Daphnia magna by the NOAEC for
Chironomus riparius (Described in a footnote to Table 4.1 of U.S. EPA 2013). Briefly, The ACR
for D. magna is 18.5. The C. riparius NOAEC (3.1 |ig/L) served as the basis for the OPP
invertebrate chronic benchmark and is used in the acute value calculation. The
estimated/calculated acute value for C. riparius is 57 |ig/L (i.e., 3.1 x 18.5). The OPP fish acute
benchmark is >2,100 |ig/L, which is V2 of the Oncorhynchus mykiss LC50 of >4,200 |ig/L.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for methoxyfenozide fulfills three of the eight MDRs,
corresponding to the use of a Secondary Acute Factor (SAF) of 8. Applying the SAF to the
lowest, most sensitive GMAV (i.e., the only GMAV available, 3,700 |ig/L for water flea
(Daphnia magna)), the calculated Secondary Acute Value (SAV) is 462.5 |ig/L. The Secondary
Maximum Criterion (SMC), which is calculated as half the SAV, is 231.3 |ig/L. Detailed
calculations for the SMC are shown below:
Lowest GMAV
3,700
SAV = —— = 462.5 |xg/L
SAV
SMC =
2
462.5
SMC = —= 231.3 |xg/L
Genus-Level Invertebrate Acute HC05
No genus-level invertebrate Acute HC05 could be calculated following USEPA (1985)
methodology because there were only two invertebrate genera (Table 2).
Table 2. Methoxyfenozide invertebrate SMAVs and GMAVs (ng/L).
(iOIIIIS
Species
SMAY
(;\1AY
CMAY Kiink
Daphnia
magna
3,700
3,700
2
Anaphales
gambiae
247.7
247.7
1
Note: The A. gambiae GMAV is based on data classified as qualitative that was included to increase the number of
invertebrate genera.
186
-------
Table 3. Summary and comparison of acute values for methoxyfenozide.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP
Invertebrate
ALB
(lowest
LCso/2) (Year
published,
species)
OW GLI Tier II
value
(# of MDRs
filled,
magnitude
relative to ALB)
OW Genus
Level
Invertebrate-
only HCos/2
Notes
Methoxyfenozide
(Insect Growth
Regulator;
Diacylhydrazine)
28.5 ng/L
(2013;
Chironomus
riparius)
231.3 ng/L
(3 MDRs filled,
0.0043X)
NA
(2 genera)
FIFRA ALB value was calculated
by multiplying the acute-to-chronic
ratio from studies with I), magna by
the NOAEC for C. riparius. The C.
riparius NOAEC (3.1 |ig/L) serves
as the basis for the FIFRA ALB
chronic benchmark.
The Tier II value is approximately
10 times larger than the FIFRA
ALB because it is based on the
GMAV for Daphnia, which is 74
times larger than the calculated test
value for C. riparius (57 ug/L).
Figure 1 shows a genus-level sensitivity distribution for the methoxyfenozide dataset. Major
taxonomic groups are delineated by different symbols, and invertebrate genera are identified by
name. Lines denoting the OPP acute benchmark values and the GLI Tier II calculated value are
included.
187
-------
10,000.0
1,000.0
w>
3.
01
N
o
c
£
>
X
o
c
0
-C
+-»
01
100.0
10.0
1.0
•
Arthropod
o
Arthropod (Qualitative)
¦
Salmonid Fish
~
Other Fish
OPP Invert. Benchmark
OPP Fish Benchmark
GLI Tier II Acute Value
0.0
0.1
0.2
• Daphnia
Anaphales
~
OPP Fish Benchmark = 2,100 pg/L
GLI Tier II Acute Value = 231.3 pg/L
OPP Invertebrate Benchmark = 28.5 pg/L
Genus-level Invertebrate HC05/2 could not be calculated
0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
Sensitivity Centile
Figure 1. Methoxyfenozide genus-level acute SD.
Symbols represent GMAVs calculated using all available data from the 2015 EPA literature search, supplemented with the OPP
registration review for methoxyfenozide (U.S. EPA 2013).
188
-------
1.3.5.2 Methoxyfenozide Chronic Toxicity Data
Chronic methoxyfenozide data were gathered by the OW in 2015 and supplemented with
additional values described in the OPP document on which the benchmark values are based (U.S.
EPA 2013). The final chronic methoxyfenozide dataset consisted of three NOECs/LOECS for
three species across three genera, of which two were invertebrate genera and one was a
vertebrate genus (Table 4).
Table 4. Chronic toxicity data of methoxyfenozide to freshwater aquatic organisms
OW
MIJR
(Irniip'1
(ion lis
Spocios
NOEC
(Mii/U
LOIX
(MS/'-)
Knilpoinl
Rol'oronco
Common!
D
Daphnia
magna
200.0
390.0
Survival
MRID 446177-14;
Zelinkaetal. 1993
Quantitative
F
Chironomus
riparius
3.1
6.3
Delayed emergence
and development
MRID 450328-01;
Kolk 2000
Supplemental
(non-guideline)
B
Pimephales
promelas
530
1,000
Survival
MRID 446177-16;
Rhodes and
Hurshman 1998
Acceptable
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 3.1 |ig/L, which is the NOEC for Chironomus
riparius.
The OPP fish chronic benchmark is 530 |ig/L, which is the NOEC for Pimephalespromelas.
GLI Tier II Chronic Value Calculation
Paired quantitative chronic and acute toxicity data for methoxyfenozide were available for water
flea (Daphnia magna), allowing for the calculation of one ACR. The remaining two ACRs were
fulfilled by the default value of 18. The acute and chronic tests were conducted in different
laboratories using water of different physical characteristics; therefore, OPP's approach was used
to calculate the ACR. OPP's approach involves the use of the NOAEC) in the calculations. The
calculated SCV for methoxyfenozide is 25.46 |ig/L.
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = V18.50* 18* 18 = 18.17
189
-------
SCV =
SACR
462.5
SCV = ——=25 A6\ig/L
18.17
Table 5. Summary and comparison of chronic values for methoxyfenozide
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP va
ue is lower than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II
value
(#of ACRs
filled, magnitude
relative to ALB)
OW Invertebrate-
only ALC (FCV)
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Methoxyfenozide
3.1 ng/L
(2019, Chironomus
riparius)
25.5 ng/L
(GLI Tier II; 1
ACR, 0.25X)
NA
Two default ACRs of 18
used to derive GLI Tier
II value.
1.3.5.3 Methoxyfenozide References
ECOTOX 165535. Morou, E., M. Lirakis, N. Pavlidi, M. Zotti, Y. Nakagawa, G. Smagghe, J.
Vontas, and L. Swevers. 2013. A New Dibenzoylhydrazine with Insecticidal Activity Against
Anopheles Mosquito Larvae. PestManag. Sci.69(7): 827-833.
MRID 44144409. Graves, W., and Swigert, J. 1995. RH-112,485 Technical: A 96-Hour Flow-
Through Acute Toxicity Test with the Bluegill (Lepomis macrochirus): Final Report: Lab Project
Number: 129A-125: 95RC-0026: 129/013195/BLU-96H2/CHP83. Unpublished study prepared
byWildlife International Ltd. 90 p.
MRID 44144410. Graves, W., and Swigert, J. 1995. RH-112,485 Technical: A 96-Hour Flow-
Through Acute Toxicity Test with the Rainbow Trout (Oncorhynchus mykiss): Final Report: Lab
Project Number: 129A-124: 95RC-0025: 129/013195/RBT-96H2/CHP84. Unpublished study
prepared by Wildlife International Ltd. 90 p.
MRID 44144411. Holmes, C., and Swigert, J. 1993. RH-112,485 Technical: A 48-Hour Flow-
Through Acute Toxicity Test with the Cladoceran (Daphnia magna): Final Report: Lab Project
Number: 129A- 112B: 92RC-0028: 129/032692/DAP-48H2/CHP38. Unpublished study
prepared by Wildlife International Ltd. 93 p.
MRID 446177-14. Zelinka, E. Holmes, C., Martin, K. et al. 1993. RH-112,485 Technical: A
Flow-Through Life-Cycle Toxicity Test With the Cladoceran (Daphnia magna): Amended Final
Report: Lab Project Number: 129A-113B: 92RC-0029: 129/032692/DAP-LC2/CHP38.
Unpublished study prepared by Wildlife International Ltd. 108 p.
MRID 446177-16. Rhodes, J., andHurshman, B. 1998. Full Life-Cycle Toxicity of RH-112,485
Technical to the Fathead Minnow (Pimephales promelas) Under Flow-Through Conditions: Lab
Project Number: 43701: 96RC-0184: 96P-184. Unpublished study prepared by ABC
Laboratories. 1246 p.
190
-------
MRID 450328-01. Kolk, J. 2000 RH-2485 Technical: Chronic Effects on Midge Larvae
(Chironomus riparius)in Water/Sediment System: Final Report: Lab Project Number: 99P-001:
1007.051.173: 99RC-0001. Unpublished study prepared by Springborn Labs. (Europe) AG. 119
P-
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2013. Registration review. Preliminary problem formulation for environmental fate,
ecological risk, endangered species, and human health drinking water exposure assessments for
methoxyfenozide. Office of Pesticide Programs. Washington, D.C. April 25, 2013.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
191
-------
1.3.6 Comparison of Aquatic Life Toxicity Values for Norflurazon: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) for norflurazon were gathered by OW in 2015. Additionally, three OPP
documents (U.S. EPA 2008, 2012, 2017) on which the benchmark values are based also provided
data. The OPP invertebrate and fish benchmark values were the same in all three documents.
1.3.6.1 Norflurazon Acute Toxicity Data
Acute norflurazon data were gathered by OW in 2015. Additionally, three OPP documents (U.S.
EPA 2008, 2012, 2017) on which the benchmark values are based also provided data. (See Table
1.) The OPP invertebrate and fish benchmark values were the same in all three documents
examined. Two LCsos were classified as "quantitative" data and one 96-hour LCso for Daphnia
magna was classified as qualitative because of its duration and because it was a greater than
value. This test was included to fulfill a MDR group, and because it serves as the basis for the
OPP invertebrate benchmark value.
The final acute norflurazon dataset consisted of three LCsos for three species representing three
genera, of which one was an invertebrate species. The invertebrate GMAV for Daphnia is listed
in Table 2.
Table 1. Acute toxicity data of norflurazon to freshwater aquatic organisms.
OW
M l)K
(iroiip'1
(ionus
Species
IX 50/
I X 50
(MS/'-)
S\1 AY
(M8/U
(IMAY
(MS/'-)
Reference
Comment
D
Daphnia
magna
>15,000
>15,000
>15,000
MRID
00035709;
Vilkas and
Browne. 1980
Qualitative,
greater than
value,
duration
A
Oncorhynchus
mykiss
8,100
8,100
8,100
MRID
00087863; Stall
etal. 1981
Quantitative
B
Lepomis
macrochirus
16,300
16,300
16,300
MRID 0087862;
Stall etal. 1981
Quantitative
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is >7,500 |ig/L, which is '/2 of the Daphnia magna test
value of >15,000 |ig/L.
192
-------
The OPP fish acute benchmark is 4,050 |ig/L, which is V2 of the Oncorhynchus mykiss LC50 of
8,100 |ig/L.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for norflurazon fulfills three MDRs, corresponding to the use of a
SAF of 8. Applying the SAF to the lowest, most sensitive GMAV (i.e., 8,100 |ig/L for rainbow
trout (Oncorhynchus mykiss), the calculated SAV is 1,012.5 |ig/L. The SMC, which is calculated
as half the SAV, is 506.3 |ig/L. Detailed calculations for the SMC are shown below:
Lowest GMAV
8,100
SAV = —— = 1,012.5 |xg/L
SAV
SMC =
2
1,012.5
SMC = —-— = 506.3 |xg/L
Genus-Level Invertebrate-only Acute HC05
No genus-level invertebrate acute HC05 could be calculated using the USEPA (1985)
methodology because there was only one invertebrate genus (Table 2).
Table 2. Norflurazon invertebrate SMAV and GMAV (^g/L).
Genus
Species
SMAV
GMAV
GMAV Rank
Daphnia
magna
>15,000
>15,000
1
Table 3. Summary and comparison of acute values for norflurazon. Magnitude relative to
ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for each value
comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Most
Sensitive ALB
(lowest LCso/2)
(Year published,
species)
OW GLI Tier II
value
(# of MDRs filled,
magnitude
relative to ALB)
OW Genus-
level
Invertebrate-
only HCos/2
Notes
Norflurazon
(Pyridazine
Herbicide)
4,050 (ig/L
(2023;
Oncorhynchus
mykiss)
506.3 ng/L 3
MDRs filled, 8X)
NA
(1 genus)
The lowest OPP ALB is for
nonvascular plants (6.03 |ig/L).
but the GLI Tier II value is based
on O. mykiss so the vertebrate
ALB is used in this comparison.
Figure 1 shows a genus-level sensitivity distribution for the norflurazon dataset. Major
taxonomic groups are delineated by different symbols, and invertebrate genera are identified by
193
-------
name. Lines denoting the OPP acute benchmark values and GLI Tier II calculated values are
included.
194
-------
100,000
10,000
GO
3-
c
o
N
ro
1,000
•
Arthropod (Qualitative)
¦
Salmonid Fish
~
Other Fish
OPP Invert. Benchmark
OPP Fish Benchmark
GLI Tier II Acute Value
• Daphnia
~
OPP Invertebrate Benchmark = >7,500 pg/L
OPP Fish Bench ma rk = 4,050 pg/L
GLI Tier II Acute Value = 506.3 ng/L
100
Genus-level Invertebrate HC05/2 could not be calculated
0.0
0.1
0.2
0.3
0.4 0.5 0.6 0.7 0.8 0.9 1.0
Sensitivity Centile
Figure 1. Norflurazon genus-level SD.
Symbols represent GMAVs calculated using all available data from the 2015 EPA literature search, supplemented the OPP registration
review document for norflurazon (U.S. EPA 2017).
195
-------
1.3.6.2 Norflurazon Chronic Toxicity Data
Chronic norflurazon data were gathered by OW in 2015. Additionally, three OPP documents
(U.S. EPA 2008, 2012, 2017) on which the benchmark values are based also provided data.
The final chronic norflurazon dataset consisted of three NOECs/LOECS for three species across
three genera, of which one was an invertebrate genus and two were vertebrate genera (Table 4).
Table 4.
Chronic toxicit
y data of norflurazon to freshwater aquatic organisms
OW
M l)K
(Iroup1
(ion lis
Species
NOEC
(MB/'-)
I.OIX
Knilpoinl
Reference
D
1 );iphni;i
mauiia
1 .(ion
2.<><><)
Reduced iiuiiihei'of
oil's pi'niK
Nlkll) uu| IX()4<>.
LeBlanc 1982
A
Oncorhynchus
mykiss
770
1,500
Growth
MRID 0018048;
LeBlanc 1982
B
Pimephales
promelas
1,100
2,100
Growth
MRID 00118047;
LeBlanc 1982
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 1,000 |ig/L, which is the NOEC for Daphnia magna.
The OPP fish chronic benchmark is 770 |ig/L, which is the NOEC for Oncorhynchus mykiss.
GLI Tier II Chronic Value Calculation
Paired quantitative chronic and acute toxicity data for norflurazon were not available for
freshwater aquatic organisms; therefore, each of the three ACRs were fulfilled by the default
value of 18. The calculated SCV for norflurazon is 56.25 |ig/L.
Detailed calculations for the SCV are shown below:
= Geometric Mean of the ACRs
= Vl8 * 18 * 18 = 18
SACR
1,012.5
—- = 56.25 [ig/L
SACR :
SACR :
SCV =
SCV =
196
-------
Table 5. Summary and comparison of chronic values for norflurazon. Magnitude relative to
ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for each value
comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
Most Sensitive
OPP ALB
(NOAEC) (Year
published, species)
OW Tier II
value
(#of ACRs
filled, magnitude
relative to ALB)
OW
Invertebrate-only
HCos
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Norflurazon
770 ng/L
(2023,
Oncorhynchus
mykiss).
56.3 ng/L
(GLI Tier II; 0
measured-data
based ACRs,
14X)
NA
Three default ACRs of
18 used to derive GLI
Tier II value.
Note the lowest ALB is
for nonvascular plants
(5.33 |ig/L). but the GLI
Tier II value is based on
O. mykiss so the
vertebrate ALB is used
in this comparison.
1.3.6.3 Norflurazon References
MRID 00035709. Vilkas, A.G.; Browne, A.M. 1980. The Acute Toxicity ofNorflurazon (99.4
Percent Active Ingredient) to the Water Flea, Daphnia magna Straus: UCCES Project No. 11506-
16-04. (Unpublished study including letter dated May 20, 1980 from R.J. McCormack to R.E.
Stoll, received Jun 5, 1980 under 11273- 19; prepared by Union Carbide Corp., submitted by
Sandoz, Inc.—Crop Protection, San Diego, Calif.; CDL:242619-A).
MRID 00087863. Stoll, R.E.; LeBlanc, G.A.; Sousa, J.V. 1981. Acute LCI5W' Toxic-ity Study
in the Rainbow Trout on Nortlurazon: EG&G Bionomics No. BW 31-7-899; Sandoz Project T -
163 7. (Unpublished study received Dec 18, 1981 under 11273-10; prepared in cooperation with
EG & G, Bionomics, submitted by Sandoz, Inc.—Crop Protec-tion, San Diego, Calif.;
CDL:246433-A).
MRID 00118047. LeBlanc, G. (1982) Early Life Stage Toxicity Study in the Fathead Minnow on
Norflurazon: Report #BW-82-5-l 166; Sandoz Project T- 1767. (Unpublished study received Nov
15, 1982 under 11273-13; prepared by EG & G, Bionomics, submitted by Sandoz, Inc., Crop
Protection, San Diego, CA; CDL:248828-A).
MRID 00118048. LeBlanc, G. (1982) Early-life Stage Toxicity Study in the Rainbow Trout on
Norflurazon: Report #BW-82-5-l 165; Sandoz Project T- 1733. (Unpublished study received Nov
15, 1982 under 11273-13; prepared by EG& G, Bionomics, submitted by Sandoz, Inc., Crop
Protection, San Diego, CA; CDL:248829-A).
MRID 00118049. LeBlanc, G. (1982) 21-day Chronic Toxicity Test in the Daphnia magna:
Bionomics Report #BW-82-5-l 169; Sandoz Project T-1768. (Unpublished study received Nov
15, 1982 under 11273-13; pre- pared by EG & G, Bionomics, submitted by Sandoz, Inc., Crop
Pro- tection, San Diego, CA; CDL:248830-A).
197
-------
MRID 0087862. Stoll, R.E.; LeBlanc, G.A.; Sousa, J.V. 1981. Acute LCI5QI' Toxici-ty Study in
the Bluegill Sunfish on Nortlurazon: EG&G Bionomics No. BW 81-7 -897; Sandoz Project T -
163 8. (Unpublished study received Dec 18, 1981 under 11273-10; prepared in cooperation with
EG & G, Bionomics, submitted by Sandoz, Inc.—Crop Protec-tion, San Diego, Calif.;
CDL:246434-A).
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2008. Risks of norflurazon use to federally threatened California red-legged frog
(Rana aurora draytonii). Pesticides effects determination. Office of Pesticide Programs.
Washington, D.C. February 18, 2008.
U.S. EPA. 2012. Registration review. Preliminary problem formulation for environmental fate
and ecological risk, endangered species, and drinking water assessments for norflurazon. Office
of Pesticide Programs. Washington, D.C. August 9, 2012.
U.S. EPA. 2017. Registration review: Preliminary risk assessment for environmental fate and
ecological risk for norflurazon. Office of Pesticide Programs. Washington, D.C. September 28,
2017.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
198
-------
1.3.7 Comparison of Aquatic Life Toxicity Values for Propargite: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) for propargite were gathered by OW in 2015 and supplemented with
data from the OPP propargite document on which the benchmark values are based (U.S. EPA
2014).
1.3.7.1 Propargite Acute Toxicity Data
Acute propargite data were gathered by OW in 2015 and supplemented with data from the OPP
document on which the benchmark values are based (U.S. EPA 2014; See Table 1). Five LCsos
across three species representing three genera were classified as "quantitative" data; Three LCsos
(one each for Daphnia magna, Lepomis macrochirus, and Oncorhynchus mykiss; the three
species represented with quantitative test data) were classified as acceptable in U.S. EPA (2014).
One 24-hour LCsos for the yellow fever mosquito Aedes aegypti was classified as qualitative
because of duration, feeding during the test, unknown control mortality, and lack of information
in source or control water, but included here to increase the number of invertebrate genera.
The final acute propargite dataset consisted of nine LCsos for four species representing four
genera, of which two were invertebrate species representing two invertebrate genera. The
invertebrate GMAVs are listed in Table 2.
Table 1. Acute toxicity data of propargite to freshwater aquatic organisms.
OW
I X 50/
S\1 AY
(M8/U
(IMAY
(MS/'-)
MIJR
(iroup'1
(ion us
Species
l-X 50
(MB/1-)
Reference
D
Daphnia
magna
91
ECOTOX 344; U.S. Environmental
Protection Agency, and Office of
Pesticide Programs. 2013
D
Daphnia
magna
14
45.64
45.64
MRID 46015901; Knight and Allan.
2002
D
Daphnia
magna
74.6
MRID 43759002; Davis. 1995
F
Aedes
aegypti
780.0
780.0
780.0
ECOTOX 116328; Pridgeon et al.
2009
A
Oncorhynchus
mykiss
118
89.86
89.86
ECOTOX 344; U.S. Environmental
Protection Agency, and Office of
Pesticide Programs. 2013
A
Oncorhynchus
mykiss
43
MRID 41458301; Sousa. 1990
A
Oncorhynchus
mykiss
143
MRID 43759001; Davis. 1995
B
Lepomis
macrochirus
167
116.3
116.3
ECOTOX 344; U.S. Environmental
Protection Agency, and Office of
Pesticide Programs. 2013
B
Lepomis
macrochirus
81
MRID 46073301; Knight and Allan.
2002
a MDR Groups - Freshwater:
199
-------
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian,
etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 7 |ig/L, which is V2 of the Daphnia magna LC50 of 14
Hg/L.
The OPP fish acute benchmark is 40.5 |ig/L, which is V2 of the Lepomis macrochirus LC50 of 81
Hg/L.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for propargite fulfills three of the eight MDRs, corresponding to the
use of a SAF of 8. Applying the SAF to the lowest, most sensitive GMAV (i.e., 35.69 |ig/L for
water flea (Daphnia magna), the calculated SAV is 4.462 |ig/L. The SMC, which is calculated as
half the SAV, is 2.231 |ig/L.
Detailed calculations for the SMC are shown below:
Lowest GMAV
35.69
SAV = —— = 4.462 |xg/L
SAV
SMC= —
4.462
SMC = —— = 2.2311xg/L
Genus-Level Invertebrate Acute HC05
No genus-level invertebrate acute HC05 could be calculated using the USEPA (1985)
methodology because there were only two invertebrate genera (Table 2).
Table 2. Propargite invertebrate SMAVs and GMAVs (iig/L).
(ion us
Species
S\1 AY
(IMAY
CMAY kiink
Aedes
aezypd
"SU.U
"SU.U
:
Daphnia
magna
45.64
45.64
1
200
-------
Table 3. Summary and comparison of chronic values for propargite.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates t
le OPP value is higher than the OW value.
Pesticide
OPP Invertebrate ALB
(lowest LCso/2) (Year
published, species)
OW GLI Tier II value
(# of MDRs filled,
magnitude relative to
ALB)
OW Genus-level
Invertebrate-only
HCos/2
Propargite
(OS Miticide)
7 (ig/L
(2021; Daphnia magna)
2.231 jig/L (3 MDRs
filled, 3.IX)
NA
(1 genus)
Figure 1 shows a genus-level sensitivity distribution for the propargite dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values and GLI Tier II calculated value are included.
201
-------
1,000.00
100.00 -
ClD
3.
QJ
¦M
bfl
i_
TO
CL
O
10.00 -
• Arthropod
O Arthropod (Qualitative)
¦ Salmonid Fish
~ Other Fish
OPP Invert. Benchmark
•- OPP Fish Benchmark
GLI Tier II Acute Value
• Daphnia
O Aedes
OPP Fish Benchmark = 40.5 ng/L
OPP Invertebrate Benchmark = 7 |ig/L
GLI Tier II Acute Value = 2.231 (ig/L
1.00
Genus-level Invertebrate FIC05/2 could not be calculated
0.0
0.1
0.2
0.3
0.4
0.5
0.6
0.7
0.8
0.9
1.0
Sensitivity Centile
Figure 1. Propargite genus-level acute SD.
Symbols represent GMAVs calculated using all available data from obtained from the EPA's 2015 literature search, supplemented the
OPP registration review document for propargite (U.S. EPA 2014).
202
-------
1.3.7.2 Propargite Chronic Toxicity Data
Chronic data for propargite were gathered by OW in 2015 and supplemented with data from the
OPP propargite document on which the benchmark values are based (U.S. EPA 2014).
The final chronic propargite dataset consisted of three NOECs/LOECS for three species across
three genera, of which one was an invertebrate genus and two were vertebrate genera (Table 4).
Table 4. Chronic toxicity data of propargite to freshwater aquatic organisms
OW
MIJR
(iioup'
(Ion us
Species
\oi:c
(MS/'-)
I.OIX
(MB/I-)
Kiulpoinl
Reference
Comment
D
Daphnia
magna
9.000
14.00
Growth
(length)
MRID 0126738;
Forbis et al. 1983 /
MRID 00142594;
Forbis and
Franklin. 1984
Quantitative
A
Oncorhynchus
mykiss
14
21
Survival and
growth
(weight)
MRID 41458301;
Sousa 1990
Supplemental
B
Pimephales
promelas
16
28
Survival and
growth
(weight)
MRID 00126739/
00132605; Forbis
et al. 1983
Acceptable
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 9 |ig/L, which is the NOEC for Daphnia magna. The
OPP fish chronic benchmark is 16 |ig/L, which is the NOEC for Pimephalespromelas.
GLI Tier II Chronic Value Calculation
Paired quantitative chronic and acute toxicity data for propargite were available for water flea
(Daphnia magna), allowing for the calculation of one ACR. The remaining two ACRs were
fulfilled by the default value of 18. The acute and chronic tests were conducted in different
laboratories using water of different physical characteristics; therefore, OPP's approach was used
to calculate the ACR. OPP's approach involves the use of the NOAEC in the calculations. The
calculated SCV for propargite is 0.561 |ig/L.
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = Vl.556 * 18 * 18 = 7.958
203
-------
SCV =
SACR
4.462
5CK = JI^q = °"561 M/L
Table 5. Summary and comparison of chronic values for propargite.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II
value
(#of ACRs
filled, magnitude
relative to ALB)
OW Invertebrate-
only HCos
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Propargite
9 (ig/L
(2021, Daphnia
magna)
0.56 ng/L
(GLI Tier II; 1
ACR, 16X)
NA
Two default ACRs of 18
used to derive GLI Tier
II value.
Note the lowest ALB is
for nonvascular plants
(1.27 |ig/L). but the GLI
Tier II value is based on
D. magna so the
invertebrate ALB is used
in this comparison.
1.3.7.3 Propargite References
ECOTOX 116328. Pridgeon, J.W., J.J. Becnel, G.G. Clark, and K.J. Linthicum. 2009. A High-
Throughput Screening Method to Identify Potential Pesticides for Mosquito Control. J. Med.
Entomol.46(2): 335-341.
ECOTOX 344. U.S. Environmental Protection Agency, and Office of Pesticide Programs. 2013.
Pesticide Ecotoxicity Database (Formerly: Environmental Effects Database (EEDB))
Environmental Fate and Effects Division, U.S.EPA, Washington, D.C.
MRJD 00126739 / 00123605. Forbis, A.; Franklin, L.; Boudreau, P.; et al. 1983. Early Life Stage
Toxicity of Omite to Fathead Minnows in a Flow-through System: Early Life Stage Final Report
#29634. (Unpublished study received Apr 8, 1983 under 400-104; prepared by Analytical Bio-
Chemistry Laboratories, Inc., submitted by Uniroyal Chemi- cal, Bethany, CT; CDL:249886-A)
MRID 00142594. Forbis, A.; Franklin, L. 1984. Chronic Toxicity of Omite to Daphnia magna
under Flow-through Test Conditions: ABC Final Re- port #31133. Unpublished study prepared
by Analytical Bio-Chemistry Laboratories, Inc. 172 p.U.S. EPA. 2015. Tier II aquatic life
community benchmarks for propargite. Office of Water and Office of Pesticide Programs.
Washington, D.C. March 2015.
204
-------
MRID 0126738. Forbis, A.; Franklin, L.; Boudreau, P.; et al. 1983. Early Life Stage Toxicity of
Omite to Fathead Minnows in a Flow-through System: Early Life Stage Final Report #29634.
(Unpublished study received Apr 8, 1983 under 400-104; prepared by Analytical Bio-Chemistry
Laboratories, Inc., submitted by Uniroyal Chemical, Bethany, CT; CDL:249886-A).
MRID 41458301. Sousa, J. 1990. Omite Technical: Acute Toxicity to Rainbow Trout
(Oncorhynchus mykiss): Lab Project Number: 89-6-3010: 41.0289. 6117.108. Unpublished
study prepared by Springborn Labs., Inc. 41 p.
MRID 43759001. Davis, J. 1995. Comite: Acute Toxicity to Rainbow Trout (Oncorhynchus
mykiss) Under Flow-Through Test Conditions: Lab Project Number: J9501010B. Unpublished
study prepared by Toxikon Environmental Sciences. 64 p.
MRID 43759002. Davis, J. 1995. Comite: Acute Toxicity to Water Flea (Daphnia magna) Under
Flow-Through Test Conditions: Lab Project Number: J9501010C. Unpublished study prepared
by Toxikon Environmental Sciences. 64 p.
MRID 46015901. Knight, B.; Allan, J. 2002. Determination of Acute Toxicity (EC50) of
Propargite to Daphnia magna (48 h, Continous-Flow). Project Number: 20632, 800052.
Unpublished study prepared by Inveresk Research International. 54 p.
MRID 46073301. Knight, B.; Allan, J. 2002. Determination of Acute Toxicity (LC50) of
Propargite to Bluegill Sunfish (96 h, Continuous-Flow). Project Number: 20480, 800031.
Unpublished study prepared by Inveresk Research International. 52 p.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2014. Registration review. Problem formulation (for) propargite. Office of Pesticide
Programs. Washington, D.C. May 5, 2014.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
205
-------
1.3.8 Comparison of Aquatic Life Toxicity Values for Pyridaben: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) for pyridaben were gathered by the OW in 2015, supplemented with
additional values from the OPP document on which the benchmark values are based (U.S. EPA
2010).
1.3.8.1 Pyridaben Acute Toxicity Data
Acute pyridaben toxicity data were gathered by the OW in 2015 and supplemented with
additional values from the OPP document on which the benchmark values are based (U.S. EPA
2010; See Table 1). Four LCsos across three species and three genera were identified and
classified as "quantitative" data. Four LCsos (two for Oncorhynchus mykiss, one for Daphnia
magna, and one for Pimephales) were classified as acceptable in Appendix C of U.S. EPA
(2010).
The final acute pyridaben dataset consisted of eight LCsos for four species representing four
genera, of which one was an invertebrate species. The invertebrate GMAV is listed in Table 2.
Table 1. Acute toxicity data of pyridaben to freshwater aquatic organisms.
OW
l .( 50/
S\1 AY
(MB/'-)
(IMAY
(^g/L)
M l)K
(iroup'
(ionus
Species
IX 50
(Mli/U
Reference
D
Daphnia
magna
0.530
0.7353
0.7353
MRID 42680111; Willis and Wilson.
1987
D
Daphnia
magna
1.02
MRID 43680404; Graves and
Swigert. 1993
A
Oncorhynchus
mykiss
0.720
MRID 43680402; Ward. 1994
A
Oncorhynchus
mykiss
2.3
1.743
1.743
MRID 42680109; Willis and Wilson.
1987
A
Oncorhynchus
mykiss
3.2
MRID 43680403; Bootman et al.
1989
B
Lepomis
macrochirus
3.430
2.940
2.940
MRID 43680401; Ward. 1994
B
Lepomis
macrochirus
2.520
MRID 42680110; Willis. 1988
C
Pimephales
promelas
2.30
2.3
2.3
MRID 43792106; Rhodes et al. 1995
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
206
-------
OPP Acute Benchmark Values
The OPP invertebrate acute benchmark is 0.265 |ig/L, which is V2 of the Daphnia magna LC50 of
0.530 |ig/L.
The OPP fish acute benchmark is 0.36 |ig/L, which is V2 of the Oncorhynchus mykiss LC50 of
0.72 |ig/L.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for pyridaben fulfills three OW MDRs, corresponding to the use of
a SAF of 8. Applying the SAF to the lowest, most sensitive GMAV (i.e., 0.530 |ig/L for water
flea (Daphnia magna), the calculated SAV is 0.066 |ig/L. The SMC, which is calculated as half
the SAV, is 0.033 |ig/L.
Detailed calculations for the SMC are shown below:
Lowest GMAV
0.530
SAV = —— = 0.066 |xg/L
SAV
SMC= —
0.066
SMC = —— = 0.033 |xg/L
Genus-Level Invertebrate-only Acute HC05
No genus-level invertebrate acute HC05 could be calculated using the USEPA (1985)
methodology because there was only one invertebrate genus (Table 2).
Table 2. Pyridaben invertebrate SMAV and GMAV (iig/L).
Genus
Species
SMAV
GMAV
GMAV Rank
Daphnia
magna
0.7353
0.7353
1
Table 3. Summary and comparison of acute values for pyridaben.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
OPP Invertebrate
ALB
(lowest LCso/2) (Year
published, species)
OW GLI Tier II value
(# of MDRs filled,
magnitude relative to ALB)
OW Genus-level
Invertebrate-only ALC
(FAV/2) "
Pyridaben
(Nicotinamide Inhibitor)
0.265 ng/L
(2023; Daphnia
magna)
0.033 (ig/L (3 MDRs filled,
8X)
NA
(1 genus)
207
-------
Figure 1 shows a genus-level sensitivity distribution for the pyridaben dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values and GLI Tier II calculated acute value are included.
208
-------
100.00
10.00
ho
3
c
01
-Q
ro
;u
"C
>•
Q.
1.00
0.10
•
Arthropod
¦
Salmonid Fish
~
Other Fish
OPP Invert. Benchmark
OPP Fish Benchmark
GLI Tier II Acute Value
~
~
• Daphnia
OPP Fish Benchmark = 0.36 pg/L
OPP Invertebrate Benchmark = 0.265 ^ig/L
GLI Tier II Acute Value = 0.033 pg/L
Genus-level Invertebrate HC05/2 could not be calculated
0.01
0.0
0.1
0.2
0.3
0.4 0.5 0.6
Sensitivity Centile
0.7
0.9
1.0
Figure 1. Pyridaben genus-level acute SD.
Symbols represent GMAVs calculated using all available data from EPA's 2015 literature search supplemented the OPP registration
review document for pyridaben (U.S. EPA 2010).
209
-------
1.3.8.2 Pyridaben Chronic Toxicity Data
Chronic pyridaben toxicity data were gathered by the OW in 2015 and supplemented with
additional values from the OPP document on which the benchmark values are based (U.S. EPA
2010). The final chronic pyridaben dataset consisted of two NOECs/LOECS for two species
across two genera, of which one was an invertebrate and one was a vertebrate (Table 4).
Table
. Chronic toxicity data of pyridaben to freshwater aqual
tic organisms.
OW
MDR
(iioup'
(Ion us
Species
\oi:c
(fiii/i)
I.OIX
(MU/I-)
Knilpoint
Reference
Comment
D
Daphnia
magna
0.044
0.086
Delayed time to
reproduction
MRID 43680408;
Drottar and Swigert
1994
Quantitative
B
Pimephales
promelas
0.277
0.555
Growth of F0 and
F1 generation and
F1 survival
MRID 43792106;
Rhodes etal. 1995
Acceptable
a MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important warmwater species
(e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP invertebrate chronic benchmark is 0.044 |ig/L, which is the NOEC for Daphnia magna.
The OPP fish chronic benchmark is 0.087 |ig/L, which is the estimated NOEC for Oncorhynchus
mykiss. The 0. mykiss NOEC was estimated using P. promelas data. Acute and chronic toxicity
data are available fori5, promelas exposed to pyridaben (96-h LC50 = 2.3 (J,g/L; NOAEC =
0.277 (J,g/L; ACR = 8.3; MRID 43792106). Because the rainbow trout is more sensitive on an
acute exposure basis, the ACR is used to derive a NOAEC for the rainbow trout (0.72 8.3 =
0.0867 |ig/L)
GLI Tier II Chronic Value Calculation
Paired quantitative chronic and acute toxicity data for pyridaben were available for water flea
(Daphnia magna), allowing for the calculation of one ACR. The remaining two ACRs were
fulfilled by the default value of 18. The acute and chronic tests were conducted in different
laboratories using water of different physical characteristics; therefore, OPP's approach was used
to calculate the ACR. OPP's approach involves the use of the NOAEC in the calculations. The
calculated SCV for pyridaben is 0.004 |ig/L.
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
210
-------
SACR = V12.05# 18* 18 =15.74
SCV =
SACR
0.066
5CK = l574 = 0-°04W7/L
Table 5. Summary and comparison of chronic values for pyridaben.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP Invertebrate
ALB
(NOAEC) (Year
published, species)
OW Tier II
value
(#of ACRs
filled, magnitude
relative to ALB)
OW Invertebrate-
only ALC (FCV)
(# of ACRs filled,
magnitude
relative to ALB)
Notes
Pyridaben
0.044 (ig/L
(2023, Daphnia
magna)
0.004 (ig/L
(GLI Tier II; 1
ACR, 11X)
NA
Two default ACRs of 18
used to derive GLI Tier
II value.
1.3.8.3 Pyridaben References
MRID 42680109. Willis, C.; Wilson, I. (1987) The Acute Toxicity of NC-129 to Rainbow Trout:
Final Report: Lab Project Number: AFT/86/022B: 88/0596. Unpublished study prepared by
Aquatox, Ltd. 40 p.
MRID 42680110. Willis, C. 1988. The Acute Toxicity of NC-129 toBluegill Sunfish: Final
Report: Lab Project Number: LSR/87/NAS021/600: 87/NAS021/600: 88/0595. Unpublished
study prepared by Life Science Research, Ltd. 51 p.
MRID 42680111. Willis, C.; Wilson, I. 1987. The Acute Toxicity of NC-129 to Daphnia Magna:
Final Report: Lab Project Number: AFT/86/024: 88/0594. Unpublished study prepared by
Aquatox, Ltd. 35 p.
MRID 43680401. Ward, G. 1994. Pyridaben Technical: Acute Toxicity to Bluegill, Lepomis
macrochirus, Under Flow- Through Conditions: Lab Project Number: 94/5002: 93062: ER93046.
Unpublished study prepared by Toxikon Environmental Sciences. 33 p.
MRID 43680402. Ward, G. 1994. Pyridaben Technical: Acute Toxicity to Rainbow Trout,
Oncorhynchus mykiss, Under Flow- Through Conditions: Lab Project Number: 94/5001: 93142:
ER93047. Unpublished study prepared by Toxikon Environmental Sciences. 33 p.
MRID 43680403. Bootman, J.; Jenkins, W.; O'Connor, J. (1989) NC-129: 21-Day Rainbow
Trout Toxicity Study Under Flow-Through Conditions: Lab Project Number: 89/0258:
88/NAS041/0824: 88/0824. Unpublished study prepared by Life Sciences Research Ltd. 41 p.
MRID 43680404. Graves, W.; Swigert, J. (1993) Pyridaben Technical A.I.: A 48-Hour Flow-
Through Acute Toxicity Test with the Cladoceran (Daphnia magna): Lab Project Number:
93/5169: ER 93057: 92076. Unpublished study prepared by Wildlife International Ltd. 45 p.
211
-------
MRID 43680408. Drottar, K.; Swigert, J. 1994. (Carbon 14)-Pyridaben: A Flow-Through Life
Cycle Toxicity Test with the Cladoceran, Daphnia magna: Lab Project Number: 94/5074: 93063:
ER 94001. Unpublished study prepared by Wildlife International Ltd. 61 p. U.S. EPA. 2015. Tier
II aquatic life community benchmarks for pyridaben. Office of Water and Office of Pesticide
Programs. Washington, D.C. March 2015.
MRID 43792106. Rhodes, J.; Leak, T.; Holmes, C. 1995. Full Life-Cycle Toxicity of BAS 300 I
(Pyridaben) to the Fathead Minnow (Pimephales promelas) Under Flow-Through Conditions:
Lab Project Number: 40571: 92160: ER94070. Unpublished study prepared by ABC Labs, Inc.
and BASF Corp. 1310 p.
U.S. EPA. 1985. Guidelines for derving numerical national water critera for the protection of
aquatic organisms and their uses. United States Environmental Protection Agency. Stephan,
C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. PB85-227049.
National Technical Information Service, Springfield, VA. U.S.
U.S. EPA. 2010. Registration review: Preliminary problem formulation for environmental fate,
ecological risk, endangered species, and drinking water exposure assessments for pyridaben.
Office of Pesticide Programs. Washington, D.C. August 26, 2010.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
212
-------
2 Herbicides
2.1 Data-Rich Herbicides
2.1.1 Comparison of Aquatic Life Toxicity Values for Atrazine: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
(CWA) (U.S. EPA 2024) were obtained from the Office of Pesticide Programs (OPP) registration
review document for atrazine (U.S. EPA 2016) and an EPA ECOTOX Knowledgebase search
conducted in 2021. No chronic comparative analysis was conducted for atrazine.
2.1.1.1 Atrazine Acute Toxicity Data
Acute data for atrazine are shown in Table 1. Ranked invertebrate GMAVs from all data sources
are listed in Table 2.
Table 1. Acute toxicity data of atrazine to freshwater aquatic organisms.
ATDR specifics OW minimum data icc|Liiicnienls under Ihc Guidelines )
OW
MI)R'
Species
I X 50
S\1 AY
(IMAY
Source
M KID/
ECOTOX
r i: i
F
Acroneuria sp.
6700
6700
6700
ECOTOX
17138
B
Ameiurus melas
35000
35000
35000
ECOTOX
7199
Plant
Anabaena cylindrica
3600
1200
2078
585.0
ECOTOX
11659
ECOTOX
11659
Plant
Anabaena flos-aquae
230
230
OPP/
ECOTOX
41065203a/
344/ 103781
Plant
Anabaena inaequalis
100
30
54.77
ECOTOX
11659
ECOTOX
11659
Plant
Anabaena variabilis
4000
5000
4472
ECOTOX
11659
ECOTOX
11659
Plant
Ankistrodesmus braunii
60
60
60
ECOTOX
11424
H
Arrenurus sp.
<20
<20
<20
ECOTOX
153867
Plant
Azolla caroliniana
>100000
>100000
>100000
ECOTOX
176903
C
Bufo americanus
>48,000
>48000
>48000
ECOTOX
19124
B
Carassius auratus
60000
56000
58181
>58181
OPP/
ECOTOX
230303/
80976
ECOTOX
80976
B
Carassius carassius
58615
>100000
>100000
ECOTOX
80976
ECOTOX
7199
Plant
Ceratophyllum sp.
22
ECOTOX
152770
Plant
Ceratophyllum demersum
22
22
ECOTOX
19461
ECOTOX
112909
D
Ceriodaphnia dubia
>30000
>30000
>30000
ECOTOX
3590
F
Chironomus tentans
720
>4900
>25
OPP
24377
213
-------
()\\
MI)R'
M KID/
Species
LC 50
SM AN
(;ma\
Source
IX ()T()\
r i: i
>28000
ECOTOX
156062
F
Chironomus tepperi
25
25
ECOTOX
153818
Plant
Chlorella pyrenoidosa
300
547.7
547.7
ECOTOX
11659
1000
ECOTOX
11659
B
Coregonus fera
11200
17163
17163
ECOTOX
7792
26300
ECOTOX
7792
B
Cyprinus carpio
2142
6346
6346
ECOTOX
170959
18800
ECOTOX
6681
B
Danio rerio
6090
22048
22048
ECOTOX
174503
15630
ECOTOX
174503
34190
ECOTOX
174503
29060
ECOTOX
170833
39510
ECOTOX
170833
30740
ECOTOX
170833
D
Daphnia carinata
22400
28367
25262
ECOTOX
74233
23100
ECOTOX
74233
24600
ECOTOX
74233
25300
ECOTOX
74233
26700
ECOTOX
74233
60600
ECOTOX
160885
D
Daphnia magna
9400
22497
ECOTOX
50679
72000
ECOTOX
89626
16823
ECOTOX
170827
E
Diporeia sp.
>3000
>3000
>3000
ECOTOX
118745
E
Echinogammarus tibaldii
3300
3300
3300
ECOTOX
18621
Plant
Elodea canadensis
4.6
75.88
75.88
OPP
McGregor et
al 2008
79
ECOTOX
160884
116
ECOTOX
160884
305
ECOTOX
160884
80
ECOTOX
9159
75
ECOTOX
4634
187.8
ECOTOX
154073
G
Elliptic) complanata
>30000
>30000
>30000
ECOTOX
100597
E
Gammarus italicus
10100
10100
14168
ECOTOX
18621
E
Gammarus kischineffensis
18900
18900
ECOTOX
183521
E
Gammarus pulex
14900
14900
ECOTOX
5023
E
Hyalella azteca
1500
6594
6594
ECOTOX
118745
13000
ECOTOX
89626
14700
ECOTOX
17138
B
Ictalurus punctatus
220
220
220
ECOTOX
19124
214
-------
()\\
MI)R'
Species
LC 50
SM AN
(;ma\
Source
M KID/
IX ()T()\
r i: i
G
Lampsilis fasciola
>30000
>30000
>30000
>30000
ECOTOX
100597
ECOTOX
100597
G
Lampsilis siliquoidea
>30000
>30000
>30000
>30000
>30000
ECOTOX
99469
ECOTOX
99469
ECOTOX
100597
ECOTOX
100597
Plant
Lemna gibba
43
57
49.51
74.63
OPP
43074803
OPP
46150901
Plant
Lemna minor
5270
60
149.8
188.8
93.2
114
112.5
ECOTOX
176903
ECOTOX
13695
ECOTOX
174524
ECOTOX
160947
ECOTOX
174501
ECOTOX
170972
B
Lepomis macrochirus
24000
54510
36170
36170
OPP/
ECOTOX
24717/
80976
ECOTOX
344
C
Lithobates boylii
5517
5517
5517
ECOTOX
118706
C
Lithobates catesbeiana
410
>16000
>2561
ECOTOX
19124
ECOTOX
89626
G
Lumbriculus variegatus
>37100
>37100
>37100
ECOTOX
17138
D
Mesocyclops longisetus
1085
1503
1277
1277
ECOTOX
164050
ECOTOX
164050
Plant
Myriophyllum aquaticum
142.2
154.5
458.8
93.5
294
194.3
768.9
ECOTOX
164771
ECOTOX
164771
ECOTOX
164771
ECOTOX
160947
ECOTOX
170972
Plant
Myriophyllum sibiricum
2119
2119
ECOTOX
74985
Plant
Myriophyllum spicatum
1104
1104
ECOTOX
9159
Plant
Najas sp.
24
24
24
ECOTOX
19461
Plant
Navicula pelliculosa
60
60
60
OPP/
ECOTOX
41065203b/
344/ 103781
A
Oncorhynchus mykiss
5300
4500
870
13000
6031
5350
17000
5478
10769
OPP/
ECOTOX
24716/344
OPP/
ECOTOX
24716 pr 23-
3-3 / 80976
ECOTOX
19124
ECOTOX
89626
ECOTOX
80976
ECOTOX
80976
ECOTOX
7199
215
-------
()\\
MI)R'
M KID/
Species
LC 50
SM AN
(;ma\
Source
IX ()T()\
r i: i
A
Oncorhynchus kisutch
12000
12000
ECOTOX
89626
A
Oncorhynchus tshawytscha
19000
19000
ECOTOX
89626
Plant
Oscillatoria lutea
<1
< 1
< i
OPP
23544
E
Pacifastacus leniusculus
77900
77900
77900
ECOTOX
167249
B
Perca sp.
50000
50000
50000
ECOTOX
7199
G
Physella virgata
>34100
>34100
>34100
ECOTOX
17138
C
Physalaemus cuvieri
19690
19690
19690
ECOTOX
179653
OPP/
42547103 /
B
Pimephales promelas
20000
20000
20000
ECOTOX
78794
Plant
Potamogeton perfoliatus
53
53
53
ECOTOX
4634
Plant
Pseudanabaena galeata
14
14
14
ECOTOX
6712
C
Pseudacris regilla
1686
1686
1686
ECOTOX
118706
D
Pseudosida ramosa
13500
17565
17565
ECOTOX
153837
16900
ECOTOX
153837
17400
ECOTOX
153837
16400
ECOTOX
153837
16900
ECOTOX
153837
20900
ECOTOX
153837
16400
ECOTOX
153837
16400
ECOTOX
153837
21600
ECOTOX
153837
26000
ECOTOX
153837
19900
ECOTOX
153837
18700
ECOTOX
153837
13400
ECOTOX
153837
12300
ECOTOX
153837
15200
ECOTOX
153837
23500
ECOTOX
153837
16900
ECOTOX
153837
19700
ECOTOX
153837
Plant
Raphidocelis subcapitata
49
126.3
126.3
OPP
43074802
120
ECOTOX
344
53
ECOTOX
344
58.7
ECOTOX
11780
410
ECOTOX
11780
200
ECOTOX
16010
50
ECOTOX
17639
235
ECOTOX
18093
128.2
ECOTOX
18933
159
ECOTOX
19285
300
ECOTOX
19285
216
-------
OW
MDR-'
Species
LC 50
SM AN
(;ma\
Source
MRU)/
IX ()T()\
r i: i
110
ECOTOX
56747
118
ECOTOX
62246
220
ECOTOX
69584
200
ECOTOX
69584
200
ECOTOX
69584
55
ECOTOX
69630
115
ECOTOX
72626
76.4
ECOTOX
82748
89.9
ECOTOX
82748
86.1
ECOTOX
82748
63.4
ECOTOX
82748
94.9
ECOTOX
82748
81.4
ECOTOX
102060
1,600
ECOTOX
118745
277
ECOTOX
152770
138
ECOTOX
152770
103
ECOTOX
152770
107
ECOTOX
152770
65
ECOTOX
152770
126
ECOTOX
152770
196
ECOTOX
165277
87.6
ECOTOX
174384
130
ECOTOX
69631
B
Rhamdia quelen
10200
10200
10200
ECOTOX
111938
C
Rhinella arenarum
27160
27160
27160
ECOTOX
112588
B
Rutilus kutum
24950
26880
26880
ECOTOX
171062
28960
ECOTOX
171062
Plant
Scenedesmus abundans
110
110
210.3
ECOTOX
11677
Plant
Scenedesmus acutus var.
acutus
597.5
597.5
ECOTOX
164777
Plant
Scenedesmus quadricauda
100
141.4
ECOTOX
11659
200
ECOTOX
11659
Plant
Vallisneria americana
163
163.0
163
ECOTOX
4634
G
Villosa constricta
>30000
>30000
>30000
ECOTOX
100597
G
Villosa delumbis
>30000
30000
ECOTOX
100597
C
Xenopus tropicalis
9620
9620
9620
ECOTOX
178499
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
217
-------
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP non-vascular plant benchmark value for atrazine is <1 |ig/L, which is the LC50 for 0.
lutea. The OPP vascular plant benchmark is 4.6 |ig/L, which is the LC50 for E. canadensis.
The OPP invertebrate acute benchmark value for atrazine is 360 |ig/L, which is V2 the LC50 for C.
tentans.
The OPP fish acute benchmark value is 2,650 |ig/L, which is V2 the LC50 for 0. mykiss.
OW Acute Criterion
There is no acute criterion, criterion maximum concentration (CMC), for atrazine. An illustrative
example was developed for this analysis, using all available data (Table 2). The FAV calculated
following the U.S. EPA (1985) methodology for the 51 genera in the atrazine dataset was 11.47
|ig/L (Table 3).
Table 2. Atrazine SMAVs and GMAVs (^ig/L).
(ionus
Species
S\1 AY
(IMAY
Riink
Percentile
()\Y
MIJR
C ¦ roup
Azolla*
caroliniana
>100,000
100,000
51
0.981
Plant
Pacifastacus
leniusculus
77,900
77,900
50
0.962
E
Carassius*
auratus
58,181
76,277
49
0.942
B
Perca
sp.
50,000
50,000
48
0.923
B
Bufo*
americanus
>48,000
48,000
47
0.904
C
Lumbriculus*
variegatus
>37,100
37,100
46
0.885
G
Lepomis
macrochirus
36,170
36,170
45
0.865
B
Ameiurus
melas
35,000
35,000
44
0.846
B
Physella*
virgata
>34,100
34,100
43
0.827
G
Elliptio*
complanata
>30,000
30,000
42
0.808
G
Lampsilis*
fasciola
>30,000
30,000
41
0.788
G
Villosa*
constricta
>30,000
30,000
40
0.769
G
Ceriodaphnia *
dubia
>30,000
30,000
39
0.750
D
Rhinella
arenarum
27,160
27,160
38
0.731
C
Rutilus
kutum
26,880
26,880
37
0.712
B
Daphnia
carinata
28,367
25,262
36
0.692
D
Danio
rerio
22,048
22,048
35
0.673
B
Pimephales
promelas
20,000
20,000
34
0.654
B
Physalaemus
cuvieri
19,690
19,690
33
0.635
C
218
-------
(ionus
Species
SM AN
(IMAV
kiink
Percentile
OW
MIJR
(J roup
Pscudosida
ramosa
l~,5o5
r.xo
32
O.ol5
D
Coregonus
fera
17,163
17,163
31
0.596
B
Gammarus
italicus
10,100
14,168
30
0.577
E
Oncorhynchus
kisutch
12,000
10,769
29
0.558
A
Rhamdia
quelen
10,200
10,200
28
0.538
B
Xenopus
tropicalis
9,620
9,620
27
0.519
C
Acroneuria
sp.
6,700
6,700
26
0.500
F
Hyalella
azteca
6,594
6,594
25
0.481
E
Cyprinus
carpio
6,346
6,346
24
0.462
B
Lithobates*
boylii
5,517
3,759
23
0.442
C
Echinogammarus
tibaldii
3,300
3,300
22
0.423
E
Diporeia*
sp.
>3,000
3,000
21
0.404
E
Pseudacris
regilla
1,686
1,686
20
0.385
C
Mesocyclops
longisetus
1,277
1,277
19
0.365
D
Myriophyllum
aquaticum
194.3
768.9
18
0.346
Plant
Anabaena
cylindrica
2,078
585.0
17
0.327
Plant
Chlorella
pyrenoidosa
547.7
547.7
16
0.308
Plant
Chironomus*
tentans
>4,490
335
15
0.288
F
Ictalurus
punctatus
220
220
14
0.269
B
Scenedesmus
abundans
110
210.3
13
0.250
Plant
Vallisneria
americana
163.0
163.0
12
0.231
Plant
Raphidocelis
subcapitata
126.3
126.3
11
0.212
Plant
Elodea
canadensis
75.88
75.88
10
0.192
Plant
Lemna
gibba
49.51
74.63
9
0.173
Plant
Navicula
pelliculosa
60
60
8
0.154
Plant
Ankistrodesmus
braunii
60
60
7
0.135
Plant
Potamogeton
perfoliatus
53
53
6
0.115
Plant
Najas
sp.
24
24
5
0.096
Plant
Ceratophyllum
demersum
22
22
4
0.077
Plant
Arrenurus*
sp.
<20
20
3
0.058
H
Pseudanabaena
galeata
14
14
2
0.038
Plant
Oscillatoria *
lutea
<1
1
1
0.019
Plant
* (non-definitive value, less than value)
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
219
-------
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
Table 3. Genus-level acute HCos for atrazine calculated following the U.S. EPA (1985)
methodology.
.V
Kiink
(;m.w
InKiMAY)
Iikc;mw i:
l*=K/( N+l)
mii-iiP)
51
4
22
3.091
9.55
0.0769
0.2774
3
20
2.996
8.97
0.0577
0.2402
2
14
2.639
6.96
0.0385
0.1961
1
1
0.000
0.00
0.0192
0.1387
Sum:
8.73
25.5
0.192
0.852
S2 =
604.19
L =
-3.056
A =
2.440
FAV =
11.47
CMC =
5.7
220
-------
Table 4. Summary and comparison of acute values for atrazine.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
Most Sensitive OPP ALB
(Year published, species)
OW Illustrative ALC example
(# of MDRs filled, magnitude
relative to ALB)
OW Modified HCos
(# of MDRs filled,
# of genera available,
magnitude relative to ALB)
Atrazine1
< 1 ^g/L
(2016; Oscillatoria lute a;
nonvascular plant)
5.7 (ig/L
(illustrative ALC example
calculated for this analysis; 8
MDRs filled, 0.18X)
NA
'No 304(a) ALC recommendation available but has sufficient data to develop an illustrative ALC example for the purposes of
these analyses only.
Figure 1 shows a genus-level sensitivity distribution for the atrazine dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values and the illustrative OW ALC example.
221
-------
1007000
10,000
1,000
UO
3 100
-------
2.1.1.2 Atrazine References
MRID 23544. Ramirea Torrest, A.M, and L.M. O'Flaherty. 1976. Influence of pesticides on
Chlorella, Chlorococcum, Stigeoclonium (Chlorophyceae), Tribonema, Vaucheria
(Xanthophyceae) and Oscillatoria (Cyanophyceae). Phycoleia 15(1): 376-387.
MRID 24377. U.S. Environmental Protection Agency. 1976. Chronic toxicity of atrazine to
selected aquatic invertebrates and fishes. Environmental Research Laboratory, Office of
Research and Development, USEPA, Duluth, MN. EPA -600/3-76-047
MRID 24716. Atrazine Acute toxicity in Rainbow Trout —SR. 00625-023-1; 230303-0-P.
MRID 41065203. Hughes, J. S. 1986. The toxicity of atrazine, Lot No. FL-850612 to four
species of aquatic plants. Unpublished study conducted by Malcolm Pirnie, Inc, White Plains,
NY. Laboratory Study No. 267-28-1100. Sponsored by Agricultural Division Ciba-Geigy,
Greensboro, NC. Study completed March 17, 1986.
MRID 42547103. Dionne, E. 1992. Chronic Toxicity to the Fathead Minnow (Pimephales
promelas) during a full life-cycle exposure. Unpublished study conducted by Springborn
Laboratories, Inc., Wareham, MA. Laboratory report No. 92-7-4324. Sponsored by Agricultural
Division, Ciba-Geigy Corporation, Greensbore, NC.
MRID 43074802. Hobert, J.R. 1993. Toxicity to the Freshwater Green Alga, Selenastrum
carpricornutum. Unpublished study conducted by Springborn Laboratories, Inc., Wareham, MA.
Study No. 93-4-4751. Sponsored by Ciba Plant Protection, Ciba-Geigy Corporation,
Greensboro, NC. Study completed November 15, 1993.
MRID 43074803. Hoberg, J.R. 1983. Atrazine Technical - Toxicity to Duckweed (Lemna
gibba). Unpublished study conducted by Springborn Laboratories, Inc, Wareham, MA. Study
No. 93-11-5053. Sponsored by Ciba Plant Protection, Ciba-Geigy Corp, Greensboro, NC. Study
completed December 21, 1983.
MRID 80976 associated with MRID 230303. Beliles, R.P., and W.J., Jr. Scott. 1965. Atrazine
Safety Evaluations on Fish and Wildlife (Bobwhite Quail, Mallard Ducks, Rainbow Trout,
Sunfish, and Goldfish). Prepared by Woodard Res. Corp., Submitted by Geigy Chem. Co.,
Ardsley, NY (MRID No.00059214), 9 p. ECOREF #80976
Abdel-Hamid, M.I.. 1996. Development and Application of a Simple Procedure for Toxicity
Testing Using Immobilized Algae. Water Sci. Technol. 33(6): 129-138. ECOREF #69584
Bathe, R., K. Sachsse, L. Ullmann, W.D. Hormann, F. Zak, and R. Hess. 1975. The Evaluation
of Fish Toxicity in the Laboratory. Proc. Eur. Soc. Toxicol. 16:113-124. ECOREF #7199
Baxter, L., R.A. Brain, L. Lissemore, K.R. Solomon, M.L. Hanson, and R.S. Prosser. 2016.
Influence of Light, Nutrients, and Temperature on the Toxicity of Atrazine to the Algal Species
Raphidocelis subcapitata: Implications for the Risk Assessment of Herbicides. Ecotoxicol.
Environ. Saf. 132:250-259. ECOREF #174384
Beliles, R.P., and W.J.,Jr. Scott. 1965. Atrazine Safety Evaluations on Fish and Wildlife
(Bobwhite Quail, Mallard Ducks, Rainbow Trout, Sunfish, and Goldfish). Prepared by Woodard
Res. Corp., Submitted by Geigy Chem. Co., Ardsley, NY (MRID No.00059214): 9 p. ECOREF
#80976.
223
-------
Berard, A., U. Dorigo, I. Mercier, K. Becker-Van Slooten, D. Grandjean, and C. Leboulanger.
2003. Comparison of the Ecotoxicological Impact of the Triazines Irgarol 1051 and Atrazine on
Microalgal Cultures and Natural Microalgal Communities in Lake Geneva. Chemosphere 53(8):
935-944. ECOREF #72626.
Birge, W.J., J.A. Black, A.G. Westerman, and B.A. Ramey. 1983. Fish and Amphibian Embryos
- a Model System for Evaluating Teratogenicity. Fundam. Appl. Toxicol. 3:237-242. ECOREF
#19124.
Brain, R.A., J. Hoberg, A.J. Hosmer, and S.B. Wall. 2012. Influence of Light Intensity on the
Toxicity of Atrazine to the Submerged Freshwater Aquatic Macrophyte Elodea canadensis.
Ecotoxicol. Environ. Saf. 79:55-61. ECOREF #160884.
Bringolf, R.B., W.G. Cope, C.B. Eads, P.R. Lazaro, M.C. Barnhart, and D. Shea. 2007. Acute
and Chronic Toxicity of Technical-Grade Pesticides to Glochidia and Juveniles of Freshwater
Mussels (Unionidae). Environ. Toxicol. Chem. 26(10): 2086-2093. ECOREF #100597.
Bringolf, R.B., W.G. Cope, M.C. Barnhart, S. Mosher, P.R. Lazaro, and D. Shea. 2007. Acute
and Chronic Toxicity of Pesticide Formulations (Atrazine, Chlorpyrifos, and Permethrin) to
Glochidia and Juveniles of Lampsilis siliquoidea. Environ. Toxicol. Chem. 26(10): 2101-2107.
ECOREF #99469.
Brodeur, J.C., G. Svartz, C.S. Perez-Coll, D.J.G. Marino, and J. Herkovits. 2009. Comparative
Susceptibility to Atrazine of Three Developmental Stages of Rhinella arenarum and Influence on
Metamorphosis: Non-Monotonous Acceleration of the Time to Climax and Delayed Tail
Resorption. Aquat. Toxicol. 91(2): 161-170. ECOREF #112588.
Brooke, L.T. 1991. Results of Freshwater Exposures with the Chemicals Atrazine, Biphenyl,
Butachlor, Carbaryl, Carbazole, Dibenzofuran, 3,3'-Dichlorobenzidine, Dichlorvos, 1,2-
Epoxyethylbenzene (Styrene Oxide), Isophorone, Isopropalin, Ox. Center for Lake Superior
Environmental Studies, University of Wisconsin, Superior, WI:110. ECOREF #17138.
Burrell, R.E., W.E. Inniss, and C.I. Mayfield. 1985. Detection and Analysis of Interactions
Between Atrazine and Sodium Pentachlorophenate with Single and Multiple Algal-Bacterial
Populations. Arch. Environ. Contam. Toxicol. 14:167-177. ECOREF #11424.
Choung, C.B., R.V. Hyne, M.M. Stevens, and G.C. Hose. 2010. A Low Concentration of
Atrazine does not Influence the Acute Toxicity of the Insecticide Terbufos or Its Breakdown
Products to Chironomus tepperi. Ecotoxicology 19(8): 1536-1544. ECOREF #153818.
Davis, D.E. 1980. Effects of Herbicides on Submerged Seed Plants. Completion Rep.Project A-
067-ALA, Office of Water Res.and Technol., Washington, DC: 19 p. ECOREF #9159.
Delia Vechia, J.F., C. Cruz, A.F. Silva, W.R., Jr. Cerveira, and N. Garlich. 2016. Macrophyte
Bioassay Applications for Monitoring Pesticides in the Aquatic Environment. Planta Daninha
34(3): 597-603. ECOREF #176903.
Demirci, K. Guven, D. Asma, S. Oqut, and P. Ugurlu. 2018. Effects of Endosulfan,
Thiamethoxam, and Indoxacarb in Combination with Atrazine on Multi-Biomarkers in
Gammarus kischineffensis. Ecotoxicol. Environ. Saf. 147:749-758. ECOREF #183521.
224
-------
Dionne, E. 1992. Chronic Toxicity to the Fathead Minnow (Pimephales promelas) During a Full
Life-Cycle Exposure. Lab. Study #92-7-4324, CIBA-GEIGY Corp., Greensboro, NC:439 p.
ECOREF #78794.
Ebke, K.P., C. Felten, and L. Doren. 2013. Impact of Heterophylly on the Sensitivity of
Myriophyllum aquaticum Biotests. Environ. Sci. Eur. 25(6): 9 p. ECOREF #164771.
Fai, P.B., A. Grant, and B. Reid. 2007. Chlorophyll a Fluorescence as a Biomarker for Rapid
Toxicity Assessment. Environ. Toxicol. Chem. 26(7): 1520-1531. ECOREF #102060.
Fairchild, J., S. Ruessler, M. Nelson, and P. Haverland. 1994. Bioavailability and Toxicity of
Agricultural Chemicals in Runoff from MSEA Sites: Potential Impacts on Non-Target Aquatic
Organisms: An Aquatic Hazard Assessment of Four Herbicides Using Six Species of Algae and
Five S. Final report for IAG DW14935600-01-2. Environmental Research Laboratory, U.S.
Environmental Protection Agency, Duluth, MN:123 p. ECOREF #152770.
Fairchild, J.F., D.S. Ruessler, and A.R. Carlson. 1998. Comparative Sensitivity of Five Species
of Macrophytes and Six Species of Algae to Atrazine, Metribuzin, Alachlor, and Metolachlor.
Environ. Toxicol. Chem. 17(9): 1830-1834. ECOREF #19461.
Fairchild, J.F., D.S. Ruessler, P.S. Haverland, and A.R. Carlson. 1997. Comparative Sensitivity
of Selenastrum capricornutum and Lemna minor to Sixteen Herbicides. Arch. Environ. Contam.
Toxicol. 32(4): 353-357. ECOREF #18093.
Forney, D.R., and D.E. Davis. 1981. Effects of Low Concentrations of Herbicides on Submersed
Aquatic Plants. Weed Sci. 29:677-685. ECOREF #4634.
Freitas, E.C., and O. Rocha. 2011. Acute Toxicity Tests with the Tropical Cladoceran
Pseudosida ramosa: The Importance of Using Native Species as Test Organisms. Arch. Environ.
Contam. Toxicol. 60(2): 241-249. ECOREF #153837.
Gala, W.R., and J.P. Giesy. 1990. Flow Cytometric Techniques to Assess Toxicity to Algae.
ASTM Spec. Tech. Publ. 13:237-246. ECOREF #18933.
Garrett, D.C. 2004. Effects of Methanol, Atrazine, and Copper on the Ultrastructure of
Pseudokirchneriella subcapitata (Selenastrum capricornutum). Ph.D. Thesis, University of North
Texas, Denton, TX:192 p. ECOREF #82748.
Geyer, H., I. Scheunert, and F. Korte. 1985. The Effects of Organic Environmental Chemicals on
the Growth of the Alga Scenedesmus subspicatus: A Contribution to Environmental Biology.
Chemosphere 14(9): 1355-1369. ECOREF #11677.
Gunkel, G., and H. Kausch.1976. Acute Toxicity of Atrazine (S-Triazine) on Coregonus fera
Under Starvation Conditions. Arch. Hydrobiol. Suppl. 48(2): 207-234. ECOREF #7792.
Gutierrez, M.F., A.M. Gagneten, and J.C. Paggi. 2013. Acute and Behavioral Sensitivity of
Mesocyclops longisetus to Atrazine and Endosulfan Formulations Under Predation Pressure.
Water Air Soil Pollut. 224(1): 9 p. ECOREF #164050.
He, H., J. Yu, G. Chen, W. Li, J. He, and H. Li. 2012. Acute Toxicity of Butachlor and Atrazine
to Freshwater Green Alga Scenedesmus obliquus and Cladoceran Daphnia carinata. Ecotoxicol.
Environ. Saf. 80:91-96. ECOREF #160885.
225
-------
Hoberg, J.R. 1991. Atrazine Technical - Toxicity to the Freshwater Green Alga Selenastrum
capricornutum. Final SLI Rep.No.91-1-3600, Springborn Lab. Inc., Environ. Sci. Div.,
Wareham, MA: 50 p. ECOREF #69631.
Hoberg, J.R. 1993. Atrazine Technical - Toxicity to the Freshwater Green Alga, (Selenastrum
capri cornutum). Final SLI Rep.No.93-4-4751, Springborn Lab. Inc., Environ. Sci. Div.,
Wareham, MA: 63 p. ECOREF #69630.
Hughes, J.S., J.S. Reed, and S.K. Krishnaswami. 1986. The Toxicity of Atrazine, Lot No. FL-
850612, to Four Species of Aquatic Plants. Final Rep. from Malcom Pirnie, Inc.to Giba-Geigy
Corp., Greensboro, NC: MRID No.410652-03, U.S.EPA, Duluth, MN, 71 p. ECOREF# 103781.
James-Yi, S.A. 2008. Systematics, Ecology, and Distribution of Water Mites (Acari:
Parasitengonina). Ph.D. Thesis, University of Illinois at Urbana-Champaign, Champaign, IL:181
p. ECOREF #153867.
Johnson, I.C., A.E. Keller, and S.G. Zam. 1993. A Method for Conducting Acute Toxicity Tests
with the Early Life Stages of Freshwater Mussels. ASTM Spec. Tech. Publ.: 381-396 ECOREF
#50679.
Kallqvist, T., and R. Romstad. 1994. Effects of Agricultural Pesticides on Planktonic Algae and
Cyanobacteria — Examples of Interspecies Sensitivity Variations. Norw. J. Agric. Sci. Suppl.
13:117-131. ECOREF #16010.
Kerby, J.L. 2006. Pesticide Effects on Amphibians: A Community Ecology Perspective. Ph.D.
Thesis, University of California, Davis: 146 p. ECOREF #118706.
Khoshnood, Z., S. Jamili, S. Khodabandeh, A. Mashinchian Moradi, and A.A. Motallebi
Moghanjoghi. 2014. Histopathological Effects and Toxicity of Atrazine Herbicide in Caspian
Kutum, Rutilus frisii kutum, Fry. Iran. J. Fish. Sci. 13(3): 702-718. ECOREF #171062.
Kirby, M.F., and D.A. Sheahan. 1994. Effects of Atrazine, Isoproturon, and Mecoprop on the
Macrophyte Lemna minor and the Alga Scenedesmus subspicatus. Bull. Environ. Contam.
Toxicol. 53(1): 120-126. ECOREF #13695.
Knezevic, V., T. Tunic, P. Gajic, P. Marjan, D. Savic, D. Tenji, and I. Teodorovic. 2016. Getting
More Ecologically Relevant Information from Laboratory Tests: Recovery of Lemna minor
After Exposure to Herbicides and Their Mixtures. Arch. Environ. Contam. Toxicol. 71(4): 572-
588. ECOREF #174524.
Kreutz, L.C., L.J.G. Barcellos, T.O. Silva, D. Anziliero, D. Martins, M. Lorenson, A.
Marteninghe, and L.B. Da Silva. 2008. Acute Toxicity Test of Agricultural Pesticides on Silver
Catfish (Rhamdia quelen) Fingerlings. Ciencia Rural 38(4): 1050-1055. ECOREF #111938.
Mayer, P., J. Frickmann, E.R. Christensen, andN. Nyholm. 1998. Influence of Growth
Conditions on the Results Obtained in Algal Toxicity Tests. Environ. Toxicol. Chem. 17(6):
1091-1098. ECOREF #19285.
McGregor, E.B., K.R. Solomon, and M.L Hanson. 2008. Effects of planting system design on the
toxicological sensitivity of Myriophyllum spicatum and Elodea canadensis to atrazine.
Chemosphere 73(3): 249-260. https://doi.Org/10.1016/j.chemosphere.2008.06.045.
226
-------
McNamara, P.C. 1991. Atrazine Technical - Acute Toxicity to Midge (Chironomus tentans)
Under Flow-Through Conditions. SLI Report No.91-2-3649, Springborn Laboratories Inc.,
Wareham, MA: 61 p. ECOREF #156062.
Mofeed, J., and Y.Y. Mosleh. 2013. Toxic Responses and Antioxidative Enzymes Activity of
Scenedesmus obliquus Exposed to Fenhexamid and Atrazine, Alone and in Mixture. Ecotoxicol.
Environ. Saf. 95: 234-240. ECOREF #164777.
Neskovic, N.K., I. Elezovic, V. Karan, V. Poleksic, and M. Budimir.1993. Acute and Subacute
Toxicity of Atrazine to Carp (Cyprinus carpio L.). Ecotoxicol. Environ. Saf. 25: 173-182.
ECOREF #6681.
Okamura, H., I. Aoyama, D. Liu, R.J. Maguire, G.J. Pacepavicius, and Y.L. Lau. 2000. Fate and
Ecotoxicity of the New Antifouling Compound Irgarol 1051 in the Aquatic Environment. Water
Res. 34(14): 3523-3530. ECOREF #56747.
Oris, J.T., R.W. Winner, and M.V. Moore. 1991. A Four-Day Survival and Reproduction
Toxicity Test for Ceriodaphnia dubia. Environ. Toxicol. Chem. 10(2): 217-224. ECOREF #3590.
Pan, H., X. Li, X. Xu, and S. Gao. 2009. Phytotoxicity of Four Herbicides on Ceratophyllum
demersum, Vallisneria natans and Elodea nuttallii. J. Environ. Sci. 21:307-312. ECOREF
#112909.
Pantani, C., G. Pannunzio, M. De Cristofaro, A.A. Novelli, and M. Salvatori. 1997. Comparative
Acute Toxicity of Some Pesticides, Metals, and Surfactants to Gammarus italicus Goedm. and
Echinogammarus tibaldii Pink, and Stock (Crustacea: Amphipoda). Bull. Environ. Contam.
Toxicol. 59(6): 963-967. ECOREF #18621.
Perez, J., I. Domingues, A.M.V.M. Soares, and S. Loureiro. 2011. Growth Rate of
Pseudokirchneriella subcapitata Exposed to Herbicides Found in Surface Waters in the Alqueva
Reservoir (Portugal): A Bottom-up Approach Using Binary Mixtures. Ecotoxicology 20(6):
1167-1175. ECOREF #165277.
Phyu, Y.L., M.St. J. Warne, and R.P. Lim. 2004. Toxicity of Atrazine and Molinate to the
Cladoceran Daphnia carinata and the Effect of River Water and Bottom Sediment on Their
Bioavailability. Arch. Environ. Contam. Toxicol. 46(3): 308-315. ECOREF #74233.
Ralston-Hooper, K., J. Hardy, L. Hahn, H. Ochoa-Acuna, L.S. Lee, R. Mollenhauer, and M.S.
Sepulveda. 2009. Acute and Chronic Toxicity of Atrazine and Its Metabolites Deethylatrazine
and Deisopropylatrazine on Aquatic Organisms. Ecotoxicology 18(7): 899-905. ECOREF
#118745.
Rentz, N.C. 2009. Evaluating the Field and Laboratory Efficacy of a Toxicity Test for the
Aquatic Macrophyte Elodea canadensis. M.S. Thesis, University of Manitoba, Canada: 219 p.,
ECOREF #154073.
Roshon, R.D. 1997. A Toxicity Test for the Effects of Chemicals on the Non-Target Submersed
Aquatic Macrophyte, Myriophyllum sibiricum Komarov. Ph.D. Thesis, University of Guelph,
Ontario, Canada:464 p. ECOREF #74985.
227
-------
Saka, M., N. Tada, and Y. Kamata. 2018. Chronic Toxicity of 1,3,5-Triazine Herbicides in the
Postembryonic Development of the Western Clawed Frog Silurana tropicalis. Ecotoxicol.
Environ. Saf. 147: 373-381. ECOREF #178499.
Seguin, F., C. Leboulanger, F. Rimet, J.C. Druart, and A. Berard. 2001. Effects of Atrazine and
Nicosulfuron on Phytoplankton in Systems of Increasing Complexity. Arch. Environ. Contam.
Toxicol. 40(2): 198-208. ECOREF #62246.
Sengupta, N., E.J. Litoff, and W.S. Baldwin. 2015. The HR96 Activator, Atrazine, Reduces
Sensitivity of D. magna to Triclosan and DHA. Chemosphere 128: 299-306. ECOREF #170827.
Stratton, G.W. 1984. Effects of the Herbicide Atrazine and Its Degradation Products, Alone and
in Combination, on Phototrophic Microorganisms. Arch. Environ. Contam. Toxicol. 13(1): 35-
42. ECOREF #11659.
Taylor, E.J., S.J. Maund, and D. Pascoe. 1991. Toxicity of Four Common Pollutants to the
Freshwater Macroinvertebrates Chironomus riparius Meigen (Insecta: Diptera) and Gammarus
pulex (L.). Arch. Environ. Contam. Toxicol. 21: 371-376. ECOREF #5023.
Teodorovic, I., V. Knezevic, T. Tunic, M. Cucak, J.N. Lecic, A. Leovac, and I.I. Tumbas. 2012.
Myriophyllum aquaticum Versus Lemna minor: Sensitivity and Recovery Potential After
Exposure to Atrazine. Environ. Toxicol. Chem. 31(2): 417-426. ECOREF #160947.
Tunic, T., V. Knezevic, U. Kerkez, A. Tubic, D. Sunjka, S. Lazic, D. Brkic, and I. Teodorovic.
2015. Some Arguments in Favor of a Myriophyllum aquaticum Growth Inhibition Test in a
Water-Sediment System as an Additional Test in Risk Assessment of Herbicides. Environ.
Toxicol. Chem. 34: 2104-2115. ECOREF #170972.
Turbak, S.C., S.B. Olson, and G.A. McFeters. 1986. Comparison of Algal Assay Systems for
Detecting Waterborne Herbicides and Metals. Water Res. 20(1): 91-96. ECOREF #11780.
U.S. Environmental Protection Agency. 1992. Pesticide Ecotoxicity Database (Formerly:
Environmental Effects Database (EEDB)). Environmental Fate and Effects Division, U.S.EPA,
Washington, D.C. ECOREF #344.
U.S. Environmental Protection Agency. 2024. Draft Comparison of Aquatic Life Protective
Values Developed for Pesticides under the Federal Insecticide, Fungicide, and Rodenticide Act
(FIFRA) and the Clean Water Act (CWA). EPA-820-D-24-002.
Velisek, J., A. Kouba, and A. Stara. 2013. Acute Toxicity of Triazine Pesticides to Juvenile
Signal Crayfish (Pacifastacus leniusculus). Neuroendocrinol. Lett. 34(2): 31-36. ECOREF
#167249.
Versteeg, D.J. 1990. Comparison of Short- and Long-Term Toxicity Test Results for the Green
Alga, Selenastrum capricornutum. ASTM Spec. Tech. Publ.: 40-48. ECOREF #17639.
Wan, M.T., C. Buday, G. Schroeder, J. Kuo, and J. Pasternak. 2006. Toxicity to Daphnia magna,
Hyalella azteca, Oncorhynchus kisutch, Oncorhynchus mykiss, Oncorhynchus tshawytscha, and
Rana catesbeiana of Atrazine, Metolachlor, Simazine, and Their Formulated Products. Bull.
Environ. Contam. Toxicol. 76(1): 52-58. ECOREF #89626.
228
-------
Wang, Y., L. Lv, Y. Yu, G. Yang, Z. Xu, Q. Wang, and L. Cai. 2017. Single and Joint Toxic
Effects of Five Selected Pesticides on the Early Life Stages of Zebrafish (Denio rerio).
Chemosphere 170: 61-67. ECOREF #174503.
Wrubleswski, J., F.W., Jr. Reichert, L. Galon, P.A. Hartmann, and M.T. Hartmann. 2018. Acute
and Chronic Toxicity of Pesticides on Tadpoles of Physalaemus cuvieri (Anura,
Leptodactylidae). Ecotoxicology 27(3): 360-368. ECOREF #179653.
Xing, H., T. Liu, Z. Zhang, X. Wang, and S. Xu. 2015. Acute and Subchronic Toxic Effects of
Atrazine and Chlorpyrifos on Common Carp (Cyprinus carpio L.): Immunotoxicity Assessments.
Fish Shellfish Immunol. 45: 327-333. ECOREF #170959.
Yan, H., S. Huang, and M. Scholz. 2015. Kinetic Processes of Acute Atrazine Toxicity to
Brachydanio rerio in the Presence and Absence of Suspended Sediments. Water Air Soil Pollut.
226(3): 13 p. ECOREF #170833.
229
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2.1.2 Comparison of Aquatic Life Toxicity Values for Propazine: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) were obtained from the Office of Pesticide Programs (OPP) registration
review document for propazine (U.S. EPA 2016) and an EPA ECOTOX Knowledgebase search
conducted in 2021.
2.1.2.1 Propazine Acute Toxicity Data
Acute data for propazine are shown in Table 1. Ranked invertebrate GMAVs from all data
sources are listed in Table 2.
Table 1. Acute toxicity data of propazine to freshwater aquatic organisms.
MDR specifies OW minimum data requirements under the Guidelines.)
OW
Ml)k'
Species
IX 50
S\1 AY
(;ma\
Source
MRID/IX OTO\
ri:i
Plant
Blue Green Algae (Anabaena
flos-aquae)
160
160
160
OPP/
ECOTOX
44287312/344
Plant
Duckweed (Lemna gibba)
100
100
100
OPP/ ECOTOX
44287309 / 344
B
Bluegill Sunfish
(Lepomis macrochirus)
>4380
>4500
>4440
>4440
OPP
48036203
OPP/
ECOTOX
178499
Plant
Freshwater Diatom (Navicula
pelliculosa)
24.8
24.8
24.8
OPP/ ECOTOX
44287310/344
A
Rainbow Trout (Oncorhynchus
mykiss)
5000
16500
9083
9083
OPP
47452301
OPP
34123
Plant
Green Algae
(Raphidocelis subcapitata)
29
29
29
OPP/
ECOTOX
44287308 / 344
C
Western Clawed Frog
(Xenopus tropicalis)
>5200
>5200
>5200
ECOTOX
178499
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP non-vascular plant benchmark value for propazine is 24.8 |ig/L, which is the LCso for
N. pelliculosa. The OPP vascular plant benchmark value is 100 |ig/L, which is the LCso for L.
gibba.
The OPP invertebrate acute benchmark value is >2,660 |ig/L, which is '/2 the LC50 for D. magna.
230
-------
The OPP fish acute benchmark value is >2,190 |ig/L, which is V2 the LC50 for L. macrochirus.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for propazine fulfills three of the eight MDRs, corresponding to the
use of a Secondary Acute Factor (SAF) of 8. Applying the SAF to the lowest, most sensitive
GMAV regardless of taxa (i.e., 28.4 |ig/L for the freshwater diatom (Naviculapelliculosa)), the
calculated Secondary Acute Value (SAV) is 3.1 |ig/L. The Secondary Maximum Criterion
(SMC), which is calculated as half the SAV, is 1.55 |ig/L. Detailed calculations for the SMC are
shown below:
Lowest GMAV
28.4
SAV = — = 3.1 \ig/L
SAV
SMC= —
3.55
SMC = —= 1.55 |xg/L
Modified Acute HC05
The genus-level modified acute HC05 calculated following the U.S. EPA (1985) methodology for
the four most sensitive genera regardless of taxa (Table 2) in the propazine dataset was 8.468
|ig/L (Table 3).
Table 2. Propazine SMAVs and G
MAVs (pg/L).
(ioniis
Species
S\1 AY
(;ma\
(IMAY
kiink
MI)R
(iroup
Oncorhynchus
mykiss
9,083
9,083
3
A
Xenopus
tropicalis
>5,200
>5,200
2
C
Lepomis
macrochirus
>4,440
>4,440
1
B
Anabaena
flos-aquae
160
160
4
Plant
Lemna
gibba
100
100
3
Plant
Raphidocelis
subcapitata
29
29
2
Plant
Navicula
pelliculosa
24.8
24.8
1
Plant
231
-------
Table 3. Modified acute HCos for propazine calculated following the U.S. EPA (1985)
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
7
4
160
5.075
25.76
0.5000
0.7071
3
100
4.605
21.21
0.3750
0.6124
2
29
3.367
11.34
0.2500
0.5000
1
24.8
3.211
10.31
0.1250
0.3536
Sum:
16.26
68.6
1.250
2.173
S2 =
36.39
L =
0.787
A =
2.136
FAV =
8.468
CMC =
4.2
Table 4. Summary and comparison of acute values for propazine.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the OPP value is higher than the OW value.
Pesticide
Most Sensitive OPP ALB
(Year published, species)
OW GLI Tier II value
(# of MDRs filled, magnitude
relative to ALB)
OW Modified HCos
(# of MDRs filled,
# of genera available,
magnitude relative to ALB)
Propazine
24.8 ng/L
(2022; Naviculapelliculosa;
nonvascular plant)
1.55 ng/L
(GLI Tier II; 4 MDRs filled*, 16X)
4.2 (ig/L
(3 MDRs, 7 genera, 5.9X)
Figure 1 shows a genus-level sensitivity distribution for the propazine dataset. Major taxonomic
groups are delineated by different symbols. Lines denoting the OPP acute benchmark values,
GLI Tier II calculated acute value, and modified HCos value are included.
232
-------
10,000
1,000
&Q
3 100
-------
2.1.2.2 Propazine Chronic Toxicity Data
Data Sources and Considerations
Chronic toxicity data for propazine were consolidated by OW and combined with data from
OPP's registration review document for acephate (U.S. EPA 2016). The final chronic propazine
dataset consisted of NOECs/LOEC for seven species (Table 5).
Table 5. Chronic toxicity data of propazine to freshwater aquatic organisms.
(MDR specifies OW minimum data requirements under the Guidelines
OW
M l)K
Species
\oi:c
I.OIX
SMC V
(IMC V
Source
MRID/IX ()T()\
ri:i
Plant
Blue Green Algae
(Anabaena flos-aquae)
68
68
68
OPP/
ECOTOX
44287312/344
D
Water Flea
(Daphnia magna)
47
91
65.40
65.40
OPP/
ECOTOX
44327602 / 344
370
ECOTOX
344
Plant
Duckweed
(Lemna gibba)
22
22
22
OPP/
ECOTOX
44287309 / 344
Plant
Freshwater Diatom
(Navicula pelliculosa)
6.5
6.5
6.5
OPP/
ECOTOX
44287310/344
B
Fathead minnow
(Pimephales promelas)
560
1230
829.9
829.9
OPP
48036205
Plant
Green Algae
(Raphidocelis
subcapitata)
12
12
12
OPP/
ECOTOX
44287308 / 344
C
Western Clawed Frog
(Xenopus tropicalis)
101.7
1036.5
324.7
324.7
ECOTOX
178499
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP nonvascular plant benchmark value for propazine is 6.5 |ig/L, which is the NOEC for
N. pelliculosa. The OPP vascular plant benchmark value is 22 |ig/L, which is the NOEC for L.
gibba.
234
-------
The OPP invertebrate chronic benchmark value is 47 |ig/L, which is the NOEC for Daphnia
magna.
The OPP fish chronic benchmark value is 560 |ig/L, which is the NOEC for Pimephales
promelas.
GLI Tier II Chronic Value Calculation
Paired quantitative acute and chronic toxicity data were available for the frog Xenopus tropicalis
allowing for the calculation of one ACR. Per the GLI Tier II methodology, the default value of
18 was used to fulfill the remaining two ACRs. The resulting X. tropicalis ACR is 16.01, and the
final SACR is 17.31. Dividing the SAV of 3.100 |ig/L by the SACR of 17.31 results in a
Secondary Continuous Value ofO.1791 |ig/L, and a Secondary Continuous Concentration of 0.18
Hg/L-
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = V16.01 * 18 * 18 = 17.13
SCV =
SACR
3.100
5CK = JfJ3 = °-18 w/L
Modified Chronic HCos
The genus-level modified chronic HC05 calculated following the U.S. EPA (1985) methodology
for the four most sensitive genera regardless of taxa (Table 6) in the propazine dataset was 2.3
|ig/L (Table 7).
Table 6. Propazine SMCVs and G
MCVs (jug/L).
(ion us
Species
SMC V
(IMC V
(;m( y
kit nk
OW
MIJR
(iroup
Pimephales
promelas
x:<>
x:<>
"
i:
Xenopus
tropicalis
324.7
324.7
6
c
Anabaena
flos-aquae
68
68
5
Plant
Daphnia
magna
65.40
65.40
4
D
Lemna
gibba
22
22
3
Plant
Raphidocelis
subcapitata
12
12
2
Plant
Navicula
pelliculosa
6.5
6.5
1
Plant
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
235
-------
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
Table 7. Modified chronic HCos for propazine calculated following the U.S. EPA (1985)
N
Rank
GMCV
ln(GMCV)
ln(GMCV)2
P=R/(N+1)
sqrt(P)
1
4
65.40
4.181
17.48
0.5000
0.7071
3
22
3.091
9.55
0.3750
0.6124
2
12
2.485
6.17
0.2500
0.5000
1
6.5
1.872
3.50
0.1250
0.3536
Sum:
11.63
36.7
1.250
2.173
S2 =
41.82
L =
-0.606
A =
0.840
FCV =
2.316
ccc=
2.3
Table 8. Summary and comparison of chronic values for propazine.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison.
Pesticide
Most Sensitive OPP ALB
(Year published and species)
OW GLI Tier II value
(# of ACRs filled,
magnitude relative to ALB)
OW Modified HCos
(# of MDRs filled, # of genera
available, magnitude relative to ALB)
Propazine
6.5 ng/L
(2022; Naviculapelliculosa;
nonvascular plant)
0.18 ng/L
(GLI Tier II; 1 ACR filled,
36X)
2.3 ng/L
(3 MDRs, 7 genera, 2.8X)
Figure 2 shows a chronic genus-level sensitivity distribution for the propazine dataset. Major
taxonomic groups are delineated by different symbols. Lines denoting the OPP chronic
benchmark values, GLI Tier II calculated chronic value, and modified HCos value are included.
236
-------
10,000
1,000
01
C
•
N
ro
Q.
O
100
10
Amphibian
Fish
Invertebrate
Nonvascular plant
Vascular plant
-Modified HC05
GLI Tier II
Nonvascular Plant ALB
Vascular Plant ALB
Navicula
Lemna
"KapHicfocefis"
+ Daphnia
t
Anabaena
Pimephales A
~ Xenopus
Vascular Plant ALB = 22 pg/L
^ i\avicuia *
Nonvascular Plant ALB = 6.5 pg/L
Modified HC05 =2.3 pg/L
1 -
GLI Tier II = 0.18 pg/L
1 1
0.8 0.9
0.0
0.1
0.2
0.3 0.4 0.5 0.6
Chronic Sensitivity Centile
0.7
1.0
Figure 2. Propazine genus-level chronic SD.
Symbols represent Genus Mean Chronic Values (GMCVs) calculated using all available data from an Office of Water ECOTOX
search in 2021 and the Office of Pesticide Programs (OPP) registration review document for propazine (U.S. EPA 2016).
237
-------
2.1.2.3 Propazine References
MRID 34123. Woodard Research Corporation. 1980. Propazine Acute Toxicity in Rainbow
Trout 2402-094-03/0003 33-5-C.
MRID 44287308. Hicks, S.L., J.B. Bussard, and D.W. Gledhill. 1995. Acute toxicity to
propazine to Selenastrum capricornutum Printz. Unpublished study conducted by ABC
Laboratories, Columbina, Missouri. Final Report No 41962. Study sponsored by Griffin
Corporation, Valdosta, GA. Study completed April 19, 1995.
MRID 44287309. Hicks, S.L., D.W. Gledhill, and J. Veltri. 1995. 14-day Statis Toxicity of
Propazine to Lemna gibba G3. Unpublished study conducted by ABC Laboratories, Inc.
Columbia, Missouri. Final report No 41963. Sponsored by Griffin Corporation, Valdosta, GA.
Study completed May 24, 1995.
MRID 44287310. Hicks, S.L. and D.W. Gledhill. 1995. Acute toxicity of propazine toNavicula
pelliculosa. Unpublished study conducted by ABC Laboratories, Inc., Columbia, Missouri. Final
Report No. 41966. Study sponsored by Griffin Corporation, Valdosta, GA. Study completed
August 30, 1995.
MRID 44287312. Gledhill, D.W., and J.M. Bussard, 1995. Acute toxicity of propazine to
Anabaena flos-aquae. Unpublished study conducted by ABC Laboratories, Inc. Columbia,
Missouri. Report No. 41968. Sponsored by Griffin Corporation, Valdosta, GA. Study completed
May 22, 1995.
MRID 44327602. Murrell, H.R. and J.L. Veltri. 1997. Chronic toxicity of propazine to Daphnia
magna under flow-through test conditions. Unpublished study conducted by ABC Laboratories,
Inc, Columbia, Missouri. Amended final report No. 41958. Study sponsored by Griffin
Corporation, Valdosta, GA. Study completed July 3, 1997.
MRID 47452301. Bergfield, A. 2008. Propazine: Acute Toxicity to the Rainbow Trout,
Oncorhynchus mykiss, Determined Under Static Test Conditions. Unpublished study performed
by ABC Laboratories, Inc., Missouri, USA. Laboratory report number 63222. Study sponsored
by Albaugh,Inc. Study completed on June 13, 2008.
MRID 48036203. Bergfield, A. 2009. Propazine: Acute toxicity to the Bluegill Sunfish, Lepomis
macrochirus, determined under flow-through test conditions. Unpublished study performed by
ABC Laboratories, Inc., Columbia, Missouri. Laboratory Study No. 64353. Study sponsored by
Albaugh, Inc., Valdosta, Georgia. Study completed April 30, 2009.
MRID 48036205. Lehman, C. 2009. Propazine: Early life-stage toxicity test with the Fathead
Minnow, Pimephales promelas, under flow-through conditions. Unpublished study conducted by
ABC Laboratories, Columbia, Missouri. ABC Study No. 64354. Study sponsored by Albaugh,
Inc., Valdosta, GA. Study completed June 29, 2009.
Saka, M., N. Tada, and Y. Kamata. Chronic Toxicity of 1,3,5-Triazine Herbicides in the
Postembryonic Development of the Western Clawed Frog Silurana tropicalis. Ecotoxicol.
Environ. Saf 147:373-381, 2018. ECOREF #178499.
238
-------
U.S. Environmental Protection Agency. Pesticide Ecotoxicity Database (Formerly:
Environmental Effects Database (EEDB)). Environmental Fate and Effects Division, U.S.EPA,
Washington, D.C., 1992. ECOREF #344.
U.S. EPA. 2024. Draft Comparison of Aquatic Life Protective Values Developed for Pesticides
under the Federal Insecticide, Fungicide, and Rodenticide Act (FIFRA) and
the Clean Water Act (CWA). EPA-820-D-24-002.
239
-------
2.1.3 Comparison of Aquatic Life Toxicity Values for Simazine: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) were obtained from the Office of Pesticide Programs (OPP) registration
review document for simazine (U.S. EPA 2016) and an EPA ECOTOX Knowledgebase search
conducted in 2021.
2.1.3.1 Simazine Acute Toxicity Data
Acute data for simazine are shown in Table 1. Ranked invertebrate GMAVs from all data
sources are listed in Table 2.
Table 1. Acute toxicity data of simazine to freshwater aquatic organisms.
MDR specifies OW minimum data requirements under the Guidelines.)
OW
MI)Ra
Species
IX 50
S\1 AY
<;may
Source
MRU) / l-X'OTOX
ri:i
Plant
Anabaena flos-aquae
36
36
36
ECOTOX
344
Plant
Arthrospira platensis
6
6
6
OPP
E17259
G
Branchiura sowerbyi
1,090,000
1,588,201
1,588,201
ECOTOX
70292
1,700,000
ECOTOX
70292
1,897,000
ECOTOX
70292
1,810,000
ECOTOX
70292
B
Carassius auratus
>32,000
>32000
>32000
OPP/
ECOTOX
344
B
Cirrhinus mrigala
765,000
820,378
820,378
ECOTOX
70292
1,050,000
ECOTOX
70292
1,100,000
ECOTOX
70292
895,000
ECOTOX
70292
840,000
ECOTOX
70292
608,000
ECOTOX
70292
635,000
ECOTOX
70292
800,000
ECOTOX
70292
E
Cypridopsis vidua
3700
3,700
3,700
OPP
4009801
D
Daphnia magna
1,000
>10192
>153213
OPP
45088221
1,100
OPP
4009801
>10,000
ECOTOX
6797
>10,000
ECOTOX
6797
>1,000,000
ECOTOX
89626
D
Daphnia pulex
424,000
153,213
ECOTOX
2897
92,100
ECOTOX
2897
92,100
ECOTOX
11881
E
Gammarus fasciatus
130,000
130,000
130,000
OPP/
ECOTOX
4009801/6797
E
Hyalella azteca
270,000
270,000
270,000
ECOTOX
89626
240
-------
()\\
MDR-
Species
IX 50
S\1 AY
<;may
Source
MRU) / l-X'OTOX
ri:i
Plant
Lemna gibba
140
140
152.4
OPP/
ECOTOX
42503704 / 344
Plant
Lemna minor
166
166
ECOTOX
18093
16,000
40,000
40,000
OPP/
25438 or 229607/
B
Lepomis macrochirus
ECOTOX
344
100,000
OPP/
ECOTOX
4009801/6797
C
Lithobates catesbeiana
1,780,000
1,780,000
1,780,000
ECOTOX
89626
B
Morone saxatilis
250
>20,083
>20,083
ECOTOX
909
>180,000
ECOTOX
5324
>180,000
ECOTOX
5324
Plant
Navicula pelliculosa
90
90
90
OPP/
ECOTOX
42503707 / 344
A
Oncorhynchus kisutch
330,000
330,000
>264441
ECOTOX
89626
A
Oncorhynchus mykiss
60,000
>61579
ECOTOX
344
40,500
ECOTOX
344
>10,000
ECOTOX
344
>82,000
ECOTOX
344
70,500
ECOTOX
344
44,600
ECOTOX
344
>100,000
ECOTOX
6797
330,000
ECOTOX
89626
A
Oncorhynchus
tshawytscha
910,000
910,000
ECOTOX
89626
E
Pacifastacus leniusculus
30,600
30,600
30,600
ECOTOX
167249
E
Palaemonetes
kadiakensis
>5,600
>5600
>5600
OPP
4009801
B
Pimephales promelas
6,400
>31958
>31958
OPP/
ECOTOX
33309/344
>10,000
ECOTOX
6797
510,000
ECOTOX
6797
F
Pteronarcys californica
1,900
1,900
1,900
OPP/
ECOTOX
4009801/6797
Plant
Raphidocelis subcapitata
100
232.1
232.1
OPP/
ECOTOX
42503706 / 344
200
ECOTOX
16010
100
ECOTOX
17639
1,240
ECOTOX
18093
100
ECOTOX
56747
200
ECOTOX
69584
220
ECOTOX
69584
220
ECOTOX
69584
748.5
ECOTOX
83543
252
ECOTOX
165277
Plant
Selenastrum sp.
73.6
58.96
58.96
ECOTOX
84045
241
-------
OW
MDR'
Species
IX 50
S\1 AY
<;may
Source
MRU) / l-X'OTOX
ri:i
57.3
ECOTOX
84045
48.6
ECOTOX
84045
Plant
Vallisneria americana
67
67
67
OPP/
ECOTOX
E164763 / 164763
G
Viviparus bengalensis
2,280,000
1,671,145
1,671,145
ECOTOX
70292
1,676,000
ECOTOX
70292
986,000
ECOTOX
70292
2,070,000
ECOTOX
70292
C
Xenopus tropicalis
7,550
7,550
7,550
ECOTOX
178499
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Acute Benchmark Values
The OPP nonvascular plant benchmark value for simazine is 6 |ig/L, which is the LC50 for A.
platensis. The OPP vascular plant benchmark value is 67 |ig/L, which is the LC50 for V.
americana.
The OPP invertebrate acute benchmark value is 500 |ig/L, which is V2 the LC50 for D. magna.
The OPP fish acute benchmark value is 3,200 |ig/L, which is V2 the LC50 fori5, promelas.
OW Acute Criterion
There is no criterion maximum concentration (CMC) for simazine. An illustrative example
calculated was developed for this analysis, using all available data (Table 2). The Final Acute
Value (FAV) calculated following the U.S. EPA (1985) methodology for the 22 genera in the
simazine dataset was 10.36 |ig/L (Table 3).
Table 2. Simazine SMAVs and <
jMAVs (jug/L).
(ienus
Species
SMAV
(IMAY
(;may
R;ink
ONY
MDR
(J roup
liana
catesbeiana
1,780,000
1,780,000
22
C
Viviparus
bengalensis
1,671,145
1,671,145
21
G/H
Branchiura
sowerbyi
1,588,201
1,588,201
20
G
Cirrhinus
mrigala
820,378
820,378
19
B
Hyalella
azteca
270,000
270,000
17
E
242
-------
(ion us
Species
S\1 AY
(IMAY
(IMAY
kiink
OW
M l)K
(J roup
Oncorhynchus
kisutch
330,000
>264,441
17
A
Oncorhynchus
mykiss
>61,597
A
Oncorhynchus
tshawytscha
910,000
A
Gammarus
fasciatus
130,000
130,000
16
E
Lepomis
macrochirus
40,000
40,000
15
B
Daphnia
magna
>10,192
>39,517
14
D
Daphnia
pulex
153,213
D
Carassius
auratus
>32,000
>32,000
13
B
Pimephales
promelas
>31,958
>31,958
12
B
Pacifastacus
leniusculus
30,600
30,600
11
E
Morone
saxatilis
20,083
20,083
10
B
Xenopus
tropicalis
7,550
7,550
9
C
Palaemonetes
kadiakensis
>5,600
>5,600
8
E
Cypridopsis
vidua
3,700
3,700
7
E
Pteronarcys
spp
1,900
1,900
6
F
Lemna
gibba
140
140
5
Plant
Raphidocelis
subcapitata
100
100
4
Plant
Navicula
pelliculosa
90
90
3
Plant
Vallisneria
americana
67
67
2
Plant
Arthrospira
platensis
6
6
1
Plant
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
243
-------
Table 3. Genus-level acute HCos for simazine calculated following the U.S. EPA (1985)
methodology.
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
22
4
100
4.605
21.21
0.1739
0.4170
3
90
4.500
20.25
0.1304
0.3612
2
67
4.205
17.68
0.0870
0.2949
1
6
1.792
3.21
0.0435
0.2085
Sum:
15.10
62.3
0.435
1.282
S2 =
220.64
L =
-0.984
A =
2.338
FAV =
10.36
CMC =
5.18
Table 4. Summary and comparison of acute values for simazine.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
Most Sensitive OPP ALB
(Year published, species)
OW Illustrative ALC
example
(# of MDRs filled,
magnitude relative to
ALB)
OW Modified HCos
(# of MDRs filled,
# of genera available,
magnitude relative to
ALB)
Simazine1
6 (ig/L
(2023; Arthrospira
platensis; nonvascular plant)
5.2 (ig/L
(illustrative example
calculated for this analysis; 8
MDRs filled, 1.2X)
NA
'No 304(a) ALC recommendation available but has sufficient data to develop an illustrative ALC example for the purposes of
these analyses only.
Figure 1 shows a genus-level sensitivity distribution for the simazine dataset. Major taxonomic
groups are delineated by different symbols, and invertebrate genera are identified by name. Lines
denoting the OPP acute benchmark values and the illustrative OW ALC example.
244
-------
10,000,000
1,000,000
100,000
~ Amphibian
O Fish
A Insect
A Invertebrate
+ Mollusk
• Nonvascular plant
¦ Vascular plant
• (FAV/2) - ALC (illustrative example calculated for this analysis)
Nonvascular Plant ALB
....... vascular Plant ALB
A + ~
O
O A
A O O
A O
<. 10,000
cm
m
c 1,000
re
,1
^ 100
A
- Raphidocelis
r Selenastrum B Lemna
Navicula
10
¦L
- Anabaena
Arthrospira
Vallisneria
Vascular Plant ALB = 67 pg/L
Nonvascular Plant ALB = 6 pg/L
(FAV/2) - ALC {illustrative example calculated for this analysis) = 5.1...
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7
Acute Sensitivity Centile
0.8
0.9
1.0
Figure 1. Simazine genus-level acute SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from an Office of Water ECOTOX search
in 2021 and the Office of Pesticide Programs (OPP) registration review document for simazine (U.S. EPA 2016).
245
-------
2.1.3.2 Simazine Chronic Toxicity Data
Data Sources and Considerations
Chronic toxicity data for simazine were consolidated by OW and combined with data from
OPP's registration review document for acephate (U.S. EPA 2016). The final chronic simazine
dataset consisted of NOECs/LOEC for 15 species (Table 5).
Table 5. Chronic toxicity data of simazine to freshwater aquatic organisms.
(MDR s
necifies OW minimum data requirements under the Guidelines
OW
MIJR
Scientific
\oi:c
LOIX
SMC V
(IMC V
Source
Mkii)
Plain
_ 1rthrospira plalensis
l( ()5 | o
1
1
OH'
i:r:5<>
B
Cyprinus carpio
60
600
189.7
189.7
OPP/
ECOTOX
Velisek et al 2012
/197125
B
Danio rerio
60
60
60
ECOTOX
167124
D
Daphnia magna
40
40
OPP
43676
40
OPP
based on ACR
Plant
Lemna gibba
50
110
50
61.24
OPP/
ECOTOX
42503704 / 344
Plant
Lemna minor
75
150
75
ECOTOX
18093
Plant
Myriophyllum
aquaticum
50
1,500
50
50
ECOTOX
68622
Plant
Navicula pelliculosa
30
70
30
30
OPP/
ECOTOX
42503707 / 344
B
Pimephales promelas
960
2000
1,386
1,386
OPP
43675
Plant
Pontederia cordata
300
1,000
300
300
ECOTOX
59738
Plant
Raphidocelis
subcapitata
93.2
>93.2
85.60
85.60
OPP
49389101
30
70
OPP/
ECOTOX
42503706 / 344
600
1,200
ECOTOX
18093
32
100
ECOTOX
165277
Plant
Typha latifolia
300
1000
300
300
ECOTOX
57010
Plant
Vallisneria americana
<58
<58
<58
<58
OPP/
ECOTOX
E164763 / 164763
C
Xenopus laevis
1.2
11
3.633
30.87
ECOTOX
178652
C
Xenopus tropicalis
83
828.5
262.2
ECOTOX
178499
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
246
-------
OPP Chronic Benchmark Values
The OPP nonvascular plant benchmark value for simazine is 1 |ig/L, which is the NOEC for
Arthrospiraplatensis. The OPP vascular plant benchmark value is 67 |ig/L, which is the NOEC
for L. gibba.
The OPP invertebrate chronic benchmark value is 40 |ig/L, which is the estimated NOEC for
Daphnia magna (LC50 (rounded to 1,000 ug/L) divided by D. magna atrazine ACR of 25).
The OPP fish chronic benchmark value is 60 |ig/L, which is the NOEC for C. carpio.
GLI Tier II Chronic Value Calculation
Paired quantitative acute and chronic toxicity data were available for Pimephalespromelas and
Xenopus tropicalis allowing for the calculation of two ACRs. Per the GLI Tier II methodology,
the default value of 18 was used to fulfill the remaining one ACR. The resulting ACRs for X
tropicalis is 28.79 and I\ promelas is 4.618, and the final SACR is 13.38. Dividing the SAV of
10.36 |ig/L by the SACR of 13.38 results in a Secondary Continuous Value of 0.7742 |ig/L, and
a Secondary Continuous Concentration of 0.77 |ig/L.
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = V28.79 * 4.618 * 18 = 13.38
10.36
5CK = = °-7742 M/L
Modified Chronic HCos
The genus-level modified chronic HCos calculated following the U.S. EPA (1985) methodology
for the four most sensitive genera regardless of taxa (Table 6) in the simazine dataset was 0.8
|ig/L (Table 7).
Table 6. Simazine SMCVs and GMCVs
(Hg/L).
(Ionus
Species
SMC V
(IMC V
(;m( y
kiink
()\\
MIJR
(iroup
Pimephales
promelas
1,386
1,386
13
B
Typha
latifolia
300.0
300.0
12
Plant
Pontederia
cordata
300.0
300.0
11
Plant
Cyprinus
carpio
189.7
189.7
10
B
Danio
rerio
60
60
9
B
Daphnia
magna
40
40
8
D
Raphidocelis
subcapitata
85.60
85.60
7
Plant
Lemna
gibba
50
61.24
6
Plant
247
-------
(ionus
Species
S\l( V
(IMC A
(;m( y
k:in k
OW
M l)K
(iroup
Lemna
minor
75
Plant
Vallisneria
americana
<58
<58
5
Plant
Myriophyllum
aquaticum
50
50
4
Plant
Xenopus
laevis
3.633
30.87
3
C
Xenopus
tropicalis
262.2
C
Navicula
pelliculosa
30
30
2
Plant
Arthrospira
platensis
1
1
1
Plant
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
Table 7. Modified chronic HCos for propazine calculated following the U.S. EPA (1985)
methodology.
.V
Kiink
(;\K \
Iim(;\i( \ t
|ik(;mcy):
l*=K/( N+l)
MII-IlP)
13
4
40
3.689
13.61
0.2857
0.5345
3
30.87
3.430
11.76
0.2143
0.4629
2
30
3.401
11.57
0.1429
0.3780
1
1
0.000
0.00
0.0714
0.2673
Sum:
10.52
36.9
0.714
1.643
S2 =
233.54
L =
-3.646
A =
-0.229
FCV =
0.7956
ccc=
0.80
248
-------
Table 8. Comparison and summary of chronic values for simazine.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio >1 indicates the 0
3P value is higher than the OW value.
Pesticide
Most Sensitive OPP ALB
(Year published and
species)
OW GLI Tier II value
(# of ACRs filled,
magnitude relative to
ALB)
OW Modified HCos
(# of MDRs filled, # of
genera available,
magnitude relative to
ALB)
Simazine
1 (ig/L
(Arthrospira platensis;
nonvascular plant)
0.77 jig/L
(GLI Tier II; 2 ACRs
filled, 1.3X)
0.8 (ig/L
(3 MDRs, 13 genera,
1.3X)
Figure 2 shows a chronic genus-level sensitivity distribution for the simazine dataset. Major
taxonomic groups are delineated by different symbols. Lines denoting the OPP chronic
benchmark values, GLI Tier II calculated chronic value, and modified HCos value are included.
249
-------
10,000
1,000
^ 100
00
3
01
c
*N 10
(B
£
In
1 .
Amphibian
Fish
Invertebrate
Nonvascular plant
Vascular plant
¦ Modified HC05
GLI Tier II
Vascular Plant ALB
V
~
Navicula
Arthrospira
+
^-Typha |
~
Pontederia
r Lemna
ir w
Myriophyllum
Vallisneria (non-definitive, less than value)
Raphidocelis
Vascular Plant ALB = 58 pg/L
Modified HC05 =0.80 pg/L
~i r
0.8 0.9
0.0
0.1
0.2
0.3 0.4 0.5 0.6 0.7
Chronic Sensitivity Centile
1.0
Figure 2. Simazine genus-level chronic SD.
Symbols represent Genus Mean Chronic Values (GMCVs) calculated using all available data from an Office of Water ECOTOX
search in 2021 and the Office of Pesticide Programs (OPP) registration review document for propazine (U.S. EPA 2016).
250
-------
2.1.3.3 Simazine References
MRID 42503704. Thompson, S.G. 1992. A 14-day toxicity test with duckweed (Lemna gibba
G3). Unpublished study conducted by Wildlife International, Ltd, Easton, MD. Laboratory
Report No. 108A-137. Study sponsored by Agricultural Division, Ciba-Geigy Corporation,
Greensboro, NC.
MRID 42503706. Thompson, S.G. 1992. A 5-day toxicity test with the freshwater alga
(Selenastrum capricornutum). Unpublished study conducted by Wildlife Internationa, Ltd.,
Easton, MD. Laboratory study number 108A-141. Study sponsored by Agricultural Division
Ciba-Geigy Corporation, Greensboro, NC. Study completed September 10, 1992.
MRID 42503707. Thompson, S.G. 1992. A 5-day toxicity test with the freshwater diatom
(Navicular pelliculosa). Unpublished study conducted by Wildlife International, Easton, MD.
Laboratory study number 108A-138. Study sponsored by Agricultural Division, Ciba-Geigy
Corporation, Greensboro, NC. Study completed September 11, 1992.
MRID 43676. Mayer, F.L. and M.D. Sander. 1981. Effects of Atrazine Fathead Minnow under...
Unpublished study conducted by Fish-Pesticide Research Laboratory, Fish and Wildlife Service,
Columbia, Missouri.
MRID 49389101. Grade, R. 1999. Growth Inhibition Test of G 30414 to Green Algae
(Selenastrum capricornutum) under Static Conditions. Final Report. Unpublished study
conducted by Novartis Crop Protection AG, Basel, Switzerland. Report Number 991589. Study
sponsored by Syngenta Crop Protection LLC, Greensboro, NC. Study completed on November
16, 1999.
Abdel-Hamid, M.I. 1996. Development and Application of a Simple Procedure for Toxicity
Testing Using Immobilized Algae. Water Sci. Technol. 33(6): 129-138.
doi: 10.2166/wst. 1996.0089. ECOREF #69584.
Bednarz, T. (1981). The Effect of Pesticides on the Growth of Green and Blue-Green Algae
Cultures. Acta Hydrobiol., 23, (2), 155-172. ECOREF#:17259
Carter, J.G. 1981. Effects of the Herbicide Simazine upon Production in a Two Member Aquatic
Food Chain. Ph.D. Thesis, Utah State University, Logan, UT:213 p. ECOREF #70902.
Fairchild, J.F., D.S. Ruessler, P.S. Haverland, and A.R. Carlson. 1997. Comparative Sensitivity
of Selenastrum capricornutum and Lemna minor to Sixteen Herbicides. Arch. Environ. Contam.
Toxicol., 32, (4), 353-357. doi:10.1007/s002449900196. ECOREF #18093.
Fairchild, J.F., D.S. Ruessler, P.S. Haverland, and A.R. Carlson. 1997. Comparative Sensitivity
of Selenastrum capricornutum and Lemna minor to Sixteen Herbicides. Arch. Environ. Contam.
Toxicol. 32(4): 353-357. doi:10.1007/s002449900196. ECOREF #18093.
Fairchild, J.F., D.S. Ruessler, P.S. Haverland, and A.R. Carlson. 1997. Comparative Sensitivity
of Selenastrum capricornutum and Lemna minor to Sixteen Herbicides. Arch. Environ. Contam.
Toxicol. 32(4): 353-357. doi:10.1007/s002449900196. ECOREF #18093.
Fitzmayer, K.M., J.G. Geiger, and M.J. Van den Avyle. 1982. Acute Toxicity Effects of
Simazine on Daphniapulex and Larval Striped Bass. Proc. Annu. Conf. Southeast. Assoc. Fish
Wildl. Agencies36:146-156. ECOREF #2897.
251
-------
Fitzmayer, K.M., J.G. Geiger, and M.J. Van den Avyle. 1982. Effects of Chronic Exposure to
Simazine on the Cladoceran, Daphniapulex. Arch. Environ. Contam. Toxicol. 11(5): 603-609.
ECOREF #11881.
Kallqvist, T., and R. Romstad. 1994. Effects of Agricultural Pesticides on Planktonic Algae and
Cyanobacteria — Examples of Interspecies Sensitivity Variations. Norw. J. Agric. Sci. Suppl. 13:
117-131. ECOREF #16010.
Kamaya, Y., T. Takada, and K. Suzuki. 2004. Effect of Medium Phosphate Levels on the
Sensitivity of Selenastrum capricornutum to Chemicals. Bull. Environ. Contam. Toxicol. 73(6):
995-1000. doi: 10.1007/sOO 128-004-0524-8. ECOREF #84045.
Knuteson, S.L., T. Whitwell, and S.J. Klaine. 2002. Influence of Plant Age and Size on Simazine
Toxicity and Uptake. J. Environ. Qual. 31(6): 2096-2103. ECOREF #68622.
Ma, J., S. Wang, P. Wang, L. Ma, X. Chen, and R. Xu. 2006. Toxicity Assessment of 40
Herbicides to the Green Alga Raphidocelis subcapitata. Ecotoxicol. Environ. Saf. 63(3): 456-
462. doi: 10.1016/j.ecoenv.2004.12.001. ECOREF #83543.
Mayer, F.L., Jr., and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data
Base for 410 Chemicals and 66 Species of Freshwater Animals. USDI Fish and Wildlife Service,
Publication No.160, Washington, DC:505 p. ECOREF #6797.
McCann, J.A., and R.K. Hitch. 1980. Simazine Toxicty to Fingerling Striped Bass. Prog. Fish-
Cult. 42(3): 180-181. ECOREF #5324.
Okamura, H., I. Aoyama, D. Liu, R.J. Maguire, G.J. Pacepavicius, and Y.L. Lau. 2000. Fate and
Ecotoxicity of the New Antifouling Compound Irgarol 1051 in the Aquatic Environment. Water
Res. 34(14): 3523-3530. doi:10.1016/S0043-1354(00)00095-6. ECOREF #56747.
Perez, J., I. Domingues, A.M.V.M. Soares, and S. Loureiro. 2011. Growth Rate of
Pseudokirchneriella subcapitata Exposed to Herbicides Found in Surface Waters in the Alqueva
Reservoir (Portugal): A Bottom-up Approach Using Binary Mixtures. Ecotoxicology 20(6):
1167-1175. doi: 10.1007/s 10646-011-0661-x. ECOREF #165277.
Perez, J., I. Domingues, A.M.V.M. Soares, and S. Loureiro. 2011. Growth Rate of
Pseudokirchneriella subcapitata Exposed to Herbicides Found in Surface Waters in the Alqueva
Reservoir (Portugal): A Bottom-up Approach Using Binary Mixtures. Ecotoxicology 20(6):
1167-1175. doi:10.1007/s 10646-011-0661-x. ECOREF #165277.
Plhalova, L., I. Haluzova, S. Macova, P. Dolezelova, E. Praskova, P. Marsalek, M. Skoric, Z.
Svobodova, V. Pistekova, an. 2011. Effects of Subchronic Exposure to Simazine on Zebrafish
(Danio rerio). Neuroendocrinol. Lett. 32(Suppl. 1): 89-94. ECOREF #167124.
Sai,L., Y. Liu, B. Qu, G. Yu, Q. Guo, C. Bo, L. Xie, Q. Jia, Y. Li, X. Li, J.C. Ng, and C. Peng.
2015. The Effects of Simazine, a Chlorotriazine Herbicide, on the Expression of Genes in
Developing Male Xenopus laevis. Bull. Environ. Contam. Toxicol. 95(2): 157-163. ECOREF
#178652.
Saka, M., N. Tada, and Y. Kamata. 2018. Chronic Toxicity of 1,3,5-Triazine Herbicides in the
Postembryonic Development of the Western Clawed Frog Silurana tropicalis. Ecotoxicol.
Environ. Saf. 147: 373-381. ECOREF #178499.
252
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U.S. Environmental Protection Agency. 1992. Pesticide Ecotoxicity Database (Formerly:
Environmental Effects Database (EEDB)). Environmental Fate and Effects Division, U.S.EPA,
Washington, D.C., 1992. ECOREF #344.
U.S. Environmental Protection Agency. 2024. Draft Comparison of Aquatic Life Protective
Values Developed for Pesticides under the Federal Insecticide, Fungicide, and Rodenticide Act
(FIFRA) and the Clean Water Act (CWA). EPA-820-D-24-002.
Velisek, J., A. Kouba, and A. Stara. 2013. Acute Toxicity of Triazine Pesticides to Juvenile
Signal Crayfish (Pacifastacus leniusculus). Neuroendocrinol. Lett.34(2): 31-36. ECOREF
#167249.
Velisek, J., A. Stara, J. Machova, and Z. Svobodova. 2012. Effects of long-term exposure to
simazine in real concentrations on common carp (Cyprinus carpio L). Ecotoxicol. Environ. Saf.
76: 79-86.
Versteeg, D.J. 1990. Comparison of Short- and Long-Term Toxicity Test Results for the Green
Alga, Selenastrum capricornutum. ASTM Spec. Tech. Publ., 40-48. ECOREF #17639.
Wan, M.T., C. Buday, G. Schroeder, J. Kuo, and J. Pasternak. 2006. Toxicity to Daphnia magna,
Hyalella azteca, Oncorhynchus kisutch, Oncorhynchus mykiss, Oncorhynchus tshawytscha, and
Rana catesbeiana of Atrazine, Metolachlor, Simazine, and Their Formulated Products. Bull.
Environ. Contam. Toxicol. 76(1): 52-58. doi:10.1007/s00128-005-0888-4. ECOREF #89626.
Wilson, P.C., and S.B. Wilson. 2010. Toxicity of the Herbicides Bromacil and Simazine to the
Aquatic Macrophyte, Vallisneria americana Michx. Environ. Toxicol. Chem. 29(1): 201-211.
doi:10.1002/etc.22. ECOREF #164763.
Wilson, P.C., and S.B. Wilson. 2010. Toxicity of the Herbicides Bromacil and Simazine to the
Aquatic Macrophyte, Vallisneria americana Michx. Environ. Toxicol. Chem. 29(1): 201-211.
ECOREF #164763.
Wilson, P.C., T. Whitwell, and S.J. Klaine. 2000. Metalaxyl and Simazine Toxicity to and
Uptake by Typha latifolia. Arch. Environ. Contam. Toxicol. 39(3): 282-288. ECOREF #57010.
Wilson, P.C., T. Whitwell, and S.J. Klaine. 2000. Phytotoxicity, Uptake, and Distribution of
14C-Simazine in Acorus gramenius and Pontederia cordata. Weed Sci. 48: 701-709. ECOREF
#59738.
253
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2.1.4 Comparison of Aquatic Life Toxicity Values for Bensulide: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) were obtained from the Office of Pesticide Programs (OPP) registration
review document for bensulide (U.S. EPA 2016) and an EPA ECOTOX Knowledgebases search
conducted in 2021.
2.1.4.1 Bensulide Acute Toxicity Data
Acute data for bensulide are shown in Table 1. Ranked invertebrate GMAVs from all data
sources are listed in Table 2.
Table 1. Acute toxicity data of bensulide to freshwater aquatic organisms.
MDR specifies OW minimum data requirements under the Guidelines.)
OW
Ml)k'
Scientific
I X 50
SM AY
(;ma\
Source
MRID/I-X ()T()\
r i: i
Plant
Blue green algae
(Anabaena flos-aquae)
>3,580
>3580
>3580
OPP/
ECOTOX
44720403 / 344
D
Water Flea (Daphnia
magna)
580
580
580
OPP
159322
E
Scud (Gammarus
fasciatus)
1,400
1,400
1,400
OPP/
ECOTOX
40098001/6797
Plant
Duckweed (Lemna gibba)
160
149.7
149.7
OPP/
ECOTOX
45334101 /344
140
OPP/
ECOTOX
44720406 / 344
B
Bluegill (Lepomis
macrochirus)
1,400
1065
1065
OPP/
ECOTOX
157316/344
810
OPP/
ECOTOX
40098001/6797
Plant
Diatom (Navicula
pelliculosa)
<690
<690
<690
ECOTOX
344
A
Rainbow trout
(Oncorhynchus mykiss)
1,100
889.9
889.9
OPP/
ECOTOX
157315/344
720
OPP/
ECOTOX
40098001/6797
Plant
Green algae
(Raphidocelis
subcapitata)
1800
1800
1800
OPP/
ECOTOX
44720402 / 344
Plant
Diatom (Skeletonema
costatum)
780
780
780
OPP
44720405
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
254
-------
OPP Acute Benchmark Values
The OPP vascular plant benchmark value for bensulide is 140 |ig/L, which is the LC50 for L.
gibba. The OPP nonvascular plant benchmark value is 780 |ig/L, which is the LC50 for S.
costatum.
The OPP invertebrate acute benchmark value is 290 |ig/L, which is V2 the LC50 of 580 |ig/L for
D. magna.
The fish acute benchmark value is 550 |ig/L, which is V2 the LC50 of 1,100 |ig/L for 0. mykiss.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for bensulide fulfills four of the eight MDRs, corresponding to the
use of a Secondary Acute Factor (SAF) of 7. Applying the SAF to the lowest, most sensitive
GMAV regardless of taxa (i.e., 149.7 |ig/L for duckweed (Lemna gibba)), the calculated
Secondary Acute Value (SAV) is 21.39 |ig/L. The Secondary Maximum Criterion (SMC), which
is calculated as half the SAV, is 10.7 |ig/L. Detailed calculations for the SMC are shown below:
Lowest GMAV
149.7
SAV = —— = 21.39 |xg/L
SAV
SMC =
2
21.39
SMC =—— = 10.7 [ig/L
Modified Acute HC05
The genus-level modified acute HC05 calculated following the U.S. EPA (1985) methodology for
the four most sensitive genera regardless of taxa (Table 2) in the bensulide dataset was 106.4
|ig/L (Table 3).
Table 2. Bensulide S
MAVs and GMAVs (ng/L).
(Ion us
Species
S\1 AY
(IMAY
(IMAY
k:iiik
(>\Y MDR
(iroup
Anabaena
Jlos-aquae
>3,580
>3,580
9
Plant
Raphidocelis
subcapitata
1,800
1,800
8
Plant
Gammarus
fasciatus
1,400
1,400
7
E
Oncorhynchus
mykiss
1,100
1,100
6
A
Lepomis
macrochirus
1,065
1,065
5
B
Skeletonema
costatum
780
780
4
Plant
255
-------
Genus
Species
SMAV
GMAV
GMAV
Rank
OW MDR
Group
Navicula
pelliculosa
<690
<690
3
Plant
Daphnia
magna
580
580
2
D
Lemna
gibba
149.7
149.7
1
Plant
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
wannwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
Table 3. Modified acute HCos for bensulide calculated following the U.S. EPA (1985)
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
9
4
780
6.659
44.35
0.4000
0.6325
3
690
6.537
42.73
0.3000
0.5477
2
580
6.363
40.49
0.2000
0.4472
1
149.7
5.009
25.09
0.1000
0.3162
Sum:
24.57
152.6
1.000
1.944
S2 =
31.60
L =
3.410
A =
4.667
FAV =
106.4
CMC =
53.21
Table 4. Comparison and summary of acute values for bensulide.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
OPP Most Sensitive ALB
(Year published, species)
OWGLI Tier II value
(# of MDRs filled, magnitude
relative to ALB)
OW Modified HCW2
(# of MDRs filled,
# of genera available,
magnitude relative to ALB)
Bensulide
140 (ig/L
(2016; Lemna gibba;
vascular plant)
10.7 ng/L
(GLI Tier II; 4 MDRs filled, 13X)
53.21 (ig/L
(4 MDRs, 9 genera, 2.6X)
256
-------
Figure 1 shows a genus-level sensitivity distribution for the bensulide dataset. Major taxonomic
groups are delineated by different symbols. Lines denoting the OPP acute benchmark values,
GLI Tier II calculated acute value, and modified HCos/2 value are included.
257
-------
10,000
1,000
1
~
Fish
H
~
Invertebrate
H
•
Nonvascular plant
J
¦
Vascular plant
j
Modified HC05/2
j
GLI Tier II
j
, ,
Vascular Plant ALB
Invertebrate ALB
¦ Lemna
M
3 100
01
-Q
—
w
Anabaena (non-definitive, greater than value)
V
I
Skeletonema
~
1
^ - Raphidoceiis
Navicula (non-definitive, less than value)
I
Invertebrate ALB = 290 pg/L
.L
Vascular Plant ALB = 140 pg/L
Modified HC05/2 = 53.2 pg/L
m
m
10 T
GLI Tier II = 10,7 pg/L
0.0
0,1
0.2
0.3 0.4 0.5 0.6
Acute Sensitivity Centile
0.7
0.8
0.9
1.0
Figure 1. Bensulide genus-level acute SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from an Office of Water ECOTOX search
in 2021 and the Office of Pesticide Programs (OPP) registration review document for bensulide (U.S. EPA 2016).
258
-------
2.1.4.2 Bensulide Chronic Toxicity Data
Data Sources and Considerations
Chronic toxicity data for bensulide were consolidated by OW and combined with data from
OPP's registration review document for acephate (U.S. EPA 2016). The final chronic bensulide
dataset consisted of NOECs/LOEC for seven species (Table 5).
Table 5. Chronic toxicity data of bensulide to freshwater aquatic organisms.
MDR specifies OW minimum data requirements under the Guidelines.)
OW
MDR'
Species
\()IX
LOIX
SMC V
(IMC V
Source
MRID/IX ()T()\
ri:i
Plant
Blue green algae
(Anabaena flos-aquae)
3,580
3,580
3,580
OPP/
ECOTOX
44720403 / 344
Water Flea
D
(Daphnia magna)
10.9
16
<7.057
<7.057
OPP
49110401
OPP/
4.2
10
ECOTOX
45303101/344
OPP/
<4.2
4.2
ECOTOX
45063401/344
OPP/
<6.9
6.9
ECOTOX
44720407 / 344
OPP/
Plant
Duckweed (Lemna gibba)
42.8
<42.4
<42.4
ECOTOX
45334101/344
OPP/
<42.1
ECOTOX
44720406 / 344
Diatom (Navicula
Plant
pelliculosa)
<410
<410
<410
ECOTOX
344
Fathead minnow
49378102 and
B
(Pimephales promelas)
200
369
384.2
384.2
OPP
49001601
374
789
OPP
44720408
Plant
Green algae (Raphidocelis
subcapitata)
ECo5=930
930
930
OPP/
ECOTOX
44720402 / 344
Diatom (Skeletonema
Plant
costatum)
635
635
635
OPP
44720405
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP vascular plant benchmark value is 42 |ig/L, which is the NOEC for Lemna gibba. The
OPP non-vascular plant benchmark value for bensulide is 635 |ig/L, which is the NOEC for the
diatom (Skeletonema costatum).
259
-------
The OPP invertebrate chronic benchmark for bensulide value is 11 |ig/L, which is the NOEC for
Daphnia magna.
The OPP fish chronic benchmark value is 169 |ig/L, which is the NOEC for Pimephales
promelas.
GLI Tier II Chronic Value Calculation
Paired quantitative acute and chronic toxicity data were available for Daphnia magna allowing
for the calculation of one D. magna ACR of 43.92. Per the GLI Tier II methodology, the default
value of 18 was used to fulfill the remaining two ACRs. The resulting final SACR is 24.23.
Dividing the SAV of 21.39 |ig/L by the SACR of 17.31 results in a Secondary Continuous Value
of 0.8828 |ig/L, and a Secondary Continuous Concentration of 0.88 |ig/L. Detailed calculations
for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = a/43.92 * 18 * 18 = 24.23
SCV =
SACR
21.39
SCV = = 0.8828 uq/L
24.23
Modified Chronic HCos
The genus-level modified chronic HC05 calculated following the U.S. EPA (1985) methodology
for the four most sensitive genera regardless of taxa (Table 6) in the bensulide dataset was 2.3
|ig/L (Table 7).
Table 6. Bensulide S1V
[CVs and GMCVs (ng/L).
Clonus
Species
SMC V
(IMC V
(IMC V
kiink
MI)R
CI roup
_ 1nabaena
flos-aquae
3,5 SO
3,5 So
"
Plain
Raphidocelis
subcapitata
930a
930a
6
Plant
Skeletonema
costatum
635
635
5
Plant
Navicula
pelliculosa
<410
<410
4
Plant
Pimephales
promelas
368.3
368.3
3
B
Lemna
gibba
<42.4
<42.4
2
Plant
Daphnia
magna
<7.057
<7.057
1
D
a - EC05 (NOAEC not reported)
260
-------
Table 7. Modified chronic HCos for bensulide calculated following the U.S. EPA (1985)
N
Rank
GMCV
ln(GMCV)
ln(GMCV)2
P=R/(N+1)
sqrt(P)
7
4
410
6.016
36.19
0.5000
0.7071
3
368.3
5.909
34.92
0.3750
0.6124
2
42.4
3.747
14.04
0.2500
0.5000
1
7.057
1.954
3.82
0.1250
0.3536
Sum:
17.63
89.0
1.250
2.173
S2 =
162.60
L =
-2.521
A =
0.331
FCV =
1.392
ccc=
1.4
Table 8. Summary and comparison of chronic values for bensulide.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
Most Sensitive OPP ALB
(Year published and species)
OW GLI Tier II value
(# of ACRs filled,
magnitude relative to ALB)
OW Modified HCos
(# of MDRs filled, # of genera
available, magnitude relative
to ALB)
Bensulide
11 (ig/L
(2016; Daphnia magna;
invertebrate)
0.88 ng/L
(GLI Tier II; 1 ACR filled,
12.5X)
1.4 (ig/L
(2 MDRs, 7 genera, 7.9X)
Figure 2 shows a chronic genus-level sensitivity distribution for the propazine dataset. Major
taxonomic groups are delineated by different symbols. Lines denoting the OPP chronic
benchmark values, GLI Tier II calculated chronic value, and modified HCos value are included.
261
-------
10,000
1,000
01
"O
"3
w
c
01
CO
~
Fish
A
Invertebrate
•
Nonvascular plant
¦
Vascular plant
-Modified HC05
GLI Tier II
— . .
Vascular Plant ALB
Invertebrate ALB
100
10
Anabaena
Skeletonema r RaPhidocelis
Skeletonema
V
Navicula (non-definitive, less than value)
Lemna (non-definitive, less than value)
1
1
A Daphnia (non-definitive, less than value)
Vascular Plant ALB = 42 |ig/L
Invertebrate ALB = 11 |ig/L
Modified HC05 = 1.4 |ig/L
1
GLI Tier II = 0.88 ng/L
0.0
0.1
0.2
0.3 0.4 0.5 0.6 0.7
Chronic Sensitivity Centile
0.8
0.9
1.0
Figure 2. Bensulide genus-level chronic SD.
Symbols represent Genus Mean Chronic Values (GMCVs) calculated using all available data from an Office of Water ECOTOX
search in 2021 and the Office of Pesticide Programs (OPP) registration review document for bensulide (U.S. EPA 2016).
262
-------
2.1.4.3 Bensulide References
MRID 44720402. Kransfelder, J.A. and L. Stuerman. 1998. Static Toxicity Test for Determining
the Effects of Test Substances to the Green Alga, Selenastrum capricornutum. Unpublished study
conducted by ABC Laboratories, Inc., Columbia, Missouri. ABC Study No. 44601. Study
sponsored by Gowan Company, Yuma, AZ. Study completed December 11, 1998.
MRID 44720403. Kranzfelder, J.A. and L. Stuerman. 1998. Static Toxicity Test for Determining
the Effects of Test Substances to the Blue-green Alga, Anabaena flos-aquae. Unpublished study
conducted by ABC Laboratories, Ins., Columbia, Missouri, ABC Study No 44602. Study
sponsored by Gowan Company, Yuma, AZ. Study completed December 11, 1998.
MRID 44720405. Kransfelder, J.A. and L. Stuerman. 1998. Static Toxicity Test for Determining
the Effects of Test Substances to the Saltwater Diatom, Skeletonema costatum. Unpublished
study conducted by ABC Laboratories, Inc., Columbia, Missouri. ABC Study No. 44604. Study
sponsored by Gowan Company, Yuma, AZ. Study completed December 11, 1998.
MRID 44720406. Kranzfelder, J.A. and L. Stuerman. 1998. Static Toxicity test for Determining
the Effects of the test Substance to Duckweed, Lemna gibba G3. Unpublished study conducted
by ABC Laboratories, Inc. Columbia, Missouri. ABC Study No. 44605. Study sponsored by
Gowan Company, Yuma, AZ. Study completed December 11, 1998.
MRID 44720407. Kranzfelder, J.A., L. Stuerman, and D. Malorin. 1998. Life-cycle toxicity test
of Daphnia magna under flow-through conditions. Unpublished study conducted by ABC
Laboratories, Inc., Columbia, Missouri. ABC Study No. 44606. Study sponsored by Gowan
Company, Yuma, AZ. Study completed December 14, 1998.
MRID 44720408. Kranzfelder, J.A., L. Stuerman, and D. Malorin. 1998. Early life-stage toxicity
test of Fathead Minnow, Pimephales promelas, under flow-through conditions. Unpublished
study conducted by ABC Laboratories, Inc., Columbia, Missouri. ABC Study No. 44607. Study
sponsored by Gowan Company, Yuma, AZ. Study completed December 10, 1998.
MRID 45063401. Kranzfelder, J.A., L. Stuerman, and D. Malorin. 1998. Life-cycle toxicity test
of Daphnia magna under flow-through conditions. Unpublished study conducted by ABC
Laboratories, Inc. Columbia, Missouri. ABC Study No. 44606. Study sponsored by Gowan
Company, Yuma, AZ. Study completed December 14, 1998.
MRID 45334101. Madsen, T.J. andM. Goble. 2001. Toxicity of Bensulide Technical to
Duckweed, Lemna gibba G3 Determined Under Static Test Conditions. Unpublished study
conducted by ABC Laboratories, Inc., Columbia, Missouri. ABC Study No. 46422. Study
sponsored by Gowan Company, Yuma, AZ. Study completed January 30, 2001.
MRID 49001601. Leak, T. 2012. Besulide: Life-cycle Toxicity test with the Fathead Minnow,
Pimephales promelas, Under Flow-through Conditions. Unpublished study conducted by ABC
Laboratories, Inc. Columbia, Missouri. Laboratory Report ID 67498. Study sponsored by Gowan
Company, Yuma, AZ. Study completed October 30, 2012.
MRID 49110401. Rebstock, M. 2013. Bensulide: Chronic Toxicity Test with the Cladoceran,
Daphnia magna, Exposed Under Static-Renewal Conditions. Unpublished study performed by
ABC Laboratories, Inc., Columbia, MO. Laboratory Study No. 69125. Study sponsored by
Gowan Company, Yuma, AZ. Study initiated September 25, 2012 and completed April 24, 2013.
263
-------
MRID 49378102. Leak, T. 2011. Bensulide: Life-cycle Toxicity Test with the Fathead Minnow
Pimephales promelas, Under Flow-through Conditions. Unpublished study conducted by ABC
Laboratories, Inc., Columbia, Missouri. Study ID No. 67498. Study sponsored by Gowan
Company, Yuma, AZ. Amended study completed May 7, 2014.
U.S. Environmental Protection Agency. Pesticide Ecotoxicity Database (Formerly:
Environmental Effects Database (EEDB)). Environmental Fate and Effects Division, U.S.EPA,
Washington, D.C., 1992. ECOREF #344
U.S. Environmental Protection Agency. 2024. Draft Comparison of Aquatic Life Protective
Values Developed for Pesticides under the Federal Insecticide, Fungicide, and Rodenticide Act
(FIFRA) and the Clean Water Act (CWA). EPA-820-D-24-002.
264
-------
2.1.5 Comparison of Aquatic Life Toxicity Values for Glyphosate: Data Sources and
Considerations
Data used in the Draft Comparison of Aquatic Life Protective Values Developedfor Pesticides
under the Federal Insecticide, Fungicide, andRodenticide Act (FIFRA) and the Clean Water Act
('CWA) (U.S. EPA 2024) were obtained from the Office of Pesticide Programs (OPP) registration
review document for gylphosate (U.S. EPA 2009).
2.1.5.1 Glyphosate Acute Toxicity Data
Acute data for glyphosate are shown in Table 1. Ranked invertebrate GMAVs from all data
sources are listed in Table 2.
Table 1. Acute toxicity data of glyphosate to freshwater aquatic organisms.
(MDR specifies OW minimum data requirements under t
ie Guidelines.)
OW
MDRa
Species
LC50
SMAV
GMAV
MRID
REF
Plant
Plant
Cyanobacterium (Anabaena
flos-aquae)
11720
15000
13259
13259
40236904
44320639
F
Midge (Chironomus
plumosus)
13000
13000
13000
162296
D
Water Flea (Daphnia magna)
134000
134000
134000
44320631
Plant
Plant
Plant
Duckweed (Lemna gibba)
11900
24000
25500
19384
19384
44320638
45773101
40236905
B
Bluegreen sunfish (Lepomis
macrochirus)
45000
45000
45000
44320630
Plant
Diatom (Navicula peliculosa)
39900
22400
29896
29896
40236902
44320641
A
A
Rainbow Trout
(Oncorhynchus mvkiss)
77,600
134000
101973
101973
44125705
44320629
B
Fathead Minnow (Pimephales
promelas)
67900
67900
67900
44125704
Plant
Plant
Plant
Green algae (Raphidocelis
subcapitata)
12100
12540
14000
12855
12855
4023690
40236901
44320637
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
wannwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
265
-------
OPP Acute Benchmark Values
The OPP nonvascular plant benchmark value for glyphosate is 11,400 |ig/L, which is the LC50
for the Green algae (Raphidocelis subcapitata). The OPP vascular plant benchmark value is
11,900 |ig/L, which is the LC50 for L. gibba.
The OPP invertebrate acute benchmark value is 26,600 |ig/L, which is V2 the LC50 for C.
plumosis.
OPP fish acute benchmark value is 21,500 |ig/L, which is V2 the LC50 for L. macrochirus.
GLI Tier II Acute Value Calculation
The acceptable acute dataset for propazine fulfills four of the eight MDRs, corresponding to the
use of a Secondary Acute Factor (SAF) of 7. Applying the SAF to the lowest, most sensitive
GMAV regardless of taxa (i.e., 12,855 |ig/L for the Green algae (Raphidocelis subcapitata)), the
calculated Secondary Acute Value (SAV) is 3,213 |ig/L. The Secondary Maximum Criterion
(SMC), which is calculated as half the SAV, is 1,607 |ig/L.
Detailed calculations for the SMC are shown below:
Lowest GMAV
12,855
SAV = —-— = 3,213 |xg/L
SAV
SMC =
2
3 213
SMC = = 1,607 |xg/L
Modified Acute HC05
The genus-level modified acute HC05 calculated following the U.S. EPA (1985) methodology for
the four most sensitive genera regardless of taxa (Table 2) in the glyphosate dataset was 9,816
|ig/L (Table 3).
Table 2. Glyphosate SMAVs and GMAVs (iig/L).
(ioniis
Species
S\1 AY
(IMAY
(;may
kiink
MIJR
(J roup
Daphina
magna
134,000
134,000
9
D
Oncorhynchus
mykiss
101,973
101,973
8
A
Pimephales
promelas
67,900
67,900
7
B
Lepomis
macrochirus
45,000
45,000
6
B
Navicula
peliculosa
29,896
29,896
5
Plant
Lemna
gibba
19,384
19,384
4
Plant
Anabaena
flos-aquae
13,259
13,259
3
Plant
Chironomus
plumosus
13,000
13,000
2
F
Raphidocelis
subcaptata
12,855
12,855
1
Plant
266
-------
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
wannwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
Table 3. Modified acute HCos for glyphosate calculated following the U.S. EPA (1985)
N
Rank
GMAV
ln(GMAV)
ln(GMAV)2
P=R/(N+1)
sqrt(P)
9
4
19,384
9.872
97.46
0.4000
0.6325
3
13,259
9.492
90.11
0.3000
0.5477
2
13,000
9.473
89.73
0.2000
0.4472
1
12,855
9.461
89.52
0.1000
0.3162
Sum:
38.30
366.8
1.000
1.944
S2 =
2.13
L =
8.865
A =
9.192
FAV =
9,816
Table 4. Comparison of acute values for glyphosate.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
ratio >1 indicates the OPP value is hig
ier than the OW value.
Pesticide
OPP Most Sensitive ALB
(Year published, species)
OW GLI Tier II value
(# of MDRs filled, magnitude
relative to ALB)
OW Modified HCos/2
(# of MDRs filled,
# of genera available,
magnitude relative to ALB)
Glyphosate
11,900 (ig/L
(2016; Lemna gibba;
vascular plant)
1,607 ng/L
(GLI Tier II; 4 MDRs filled,
7.4X)
4,908 (ig/L
(4 MDRs, 9 genera, 2.4X)
Figure 1 shows a genus-level sensitivity distribution for the glyphosate dataset. Major taxonomic
groups are delineated by different symbols. Lines denoting the OPP acute benchmark values,
GLI Tier II calculated acute value, and modified HCos value are included.
267
-------
1,000,000
100,000
cuo
3
0)
+¦"
ro
en
o
Q.
_>
10,000
1,000
~
Fish
A
Insect
X
Invertebrate
•
Nonvascular plant
¦
Vascular plant
- Modified HC05/2
— *
• GLI Tier II
¦¦ Vascular Plant ALB
- Invertebrate ALB
r Raphidocelis
A.
0.0
0.1
0.2
X
Navicula
Lemna
j-Anabaena ¦ |nvertebrate alb = 12,100 ng/L
Invertebrate ALB = 12,100 |ig/L
Vascular Plant ALB = 11,900 |ig/L
Modified HC05/2 = 4,908 ng/L
GLI Tier II = 1,607 ng/L
r
0.3 0.4 0.5 0.6 0.7
Acute Sensitivity Centile
0.8
0.9
1.0
Figure 1. Glyphosate genus-level acute SD.
Symbols represent Genus Mean Acute Values (GMAVs) calculated using all available data from the Office of Pesticide Programs
(OPP) registration review document for glyphosate (U.S. EPA 2009).
268
-------
2.1.5.2 Glyphosate Chronic Toxicity Data
Data Sources and Considerations
Chronic toxicity data for glyphosate were obtained from OPP's registration review document for
glyphosate (U.S. EPA 2009). The final chronic glyphosate dataset consisted of NOECs/LOEC
for six species (Table 5).
Table 5. Chronic toxicity data of glyphosate to freshwater aquatic organisms. (MDR
specifies OW minimum data requirements under the Guidelines.)
MDR
Species
NOAEC
LOAEC
SMCV
GMCV
MRID
Plant
Plant
Cyanobacterium
(Anabaena fios-aquae)
12000
12000
12000
40236904
44320639
D
D
Waterflea
(Daphnia magna)
49900
240000
95700
69104
69104
124763
Plant
Plant
Plant
Duckweed
(Lemna gibba)
7560
14100
7560
7560
44320638
45773101
40236905
Plant
Plant
Diatom
(Navicula peliculosa)
18000
18000
18000
40236902
44320641
B
Fathead Minnow
(Pimephales promelas)
>25700
> 25700
> 25700
108171
Plant
Plant
Plant
Green algae
(Raphidocelis subcapitata)
10000
10000
10000
4023690
40236901
44320637
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
wannwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. a planktonic crustacean (e.g., cladoceran, copepod, etc.)
E. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
H. a family in any order of insect or any phylum not already represented.
OPP Chronic Benchmark Values
The OPP vascular plant benchmark value for glyphosate is 1,300 |ig/L. There is no OPP
nonvascular benchmark plant value for glyphosate.
The OPP invertebrate chronic benchmark value is 49,900 |ig/L, which is the NOEC for Daphnia
magna.
269
-------
The OPP fish chronic benchmark value is 25,700 |ig/L, which is the NOEC for Pimephales
promelas.
GLI Tier II Chronic Value Calculation
Paired quantitative acute and chronic toxicity data were available for Pimephales promelas and
D. magna / C. plumosus allowing for the calculation of two ACRs. Per the GLI Tier II
methodology, the default value of 18 was used to fulfill the remaining one ACR. The resulting
Pimephales promelas and D. magna / C. plumosus ACR are 3.77 and 1.94, respectively, and the
final SACR is 5.09. Dividing the SAV of 1,607 |ig/L by the SACR of 5.09 results in a Secondary
Continuous Value of 315.6 |ig/L, and a Secondary Continuous Concentration of 316 |ig/L.
Detailed calculations for the SCV are shown below:
SACR = Geometric Mean of the ACRs
SACR = V3.77# 1.94# 18 = 5.09
SCV =
SACR
1,607
5CK = W = 316 V9/1
Modified Chronic HCos
The genus-level modified chronic HC05 calculated following the U.S. EPA (1985) methodology
for the four most sensitive genera regardless of taxa (Table 6) in the glyphosate dataset was
5,087 |ig/L (Table 7).
Table 6. Glyphosate SMCVs and GMCVs (^ig/L).
(Ion us
Species
SMC V
(;m( y
(IMC V
kiink
MDR
(iroup
Daphnia
magna
69,104
69,104
6
D
Pimephales
promelas
>25,700
>25,700
5
B
Navicula
peliculosa
18,000
18,000
4
Plant
Anabaena
flos-aquae
12,000
12,000
3
Plant
Raphidocelis
subcapitata
10,000
10,000
2
Plant
Lemna
gibba
7,560
7,560
1
Plant
a OW MDR Groups - Freshwater:
A. the family Salmonidae in the class Osteichthyes
B. a second family in the class Osteichthyes, preferably a commercially or recreationally important
warmwater species (e.g., bluegill, channel catfish, etc.)
C. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an amphibian, etc.)
D. aplanktonic crustacean (e.g., cladoceran, copepod, etc.)
E. abenthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
F. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)
G. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
270
-------
H. a family in any order of insect or any phylum not already represented.
Table 7. Modified chronic HCos for glyphosate calculated following the U.S. EPA (1985)
methodology.
N
Rank
GMCV
ln(GMCV)
ln(GMCV)2
P=R/(N+1)
sqrt(P)
6
4
18,000
9.798
96.00
0.5714
0.7559
3
12,000
9.393
88.22
0.4286
0.6547
2
10,000
9.210
84.83
0.2857
0.5345
1
7,560
8.931
79.76
0.1429
0.3780
Sum:
37.33
348.8
1.429
2.323
S2 =
5.00
L =
8.035
A =
8.534
FCV =
5,087
Table 8. Summary and comparison of chronic values for glyphosate.
Magnitude relative to ALB is the OPP ALB/OW value, the ratio for the OPP value/OW value for
each value comparison. A ratio <1 indicates the OPP value is lower than the OW value and a
Pesticide
Most Sensitive
OPP ALB
(Year published and
species)
OW GLI Tier II value
(# of ACRs filled, magnitude
relative to ALB)
OW Modified HCos
(# of MDRs filled, # of genera
available, magnitude relative
to ALB)
Glyphosate
1,300 pg/L
(Lemna gibbet;
vascular plant)
316 pg/L
(GLI Tier II; 2 ACRs filled,
4.IX)
5,087 pg/L
(2, MDRs, 6 genera, 0.26X)
Figure 2 shows a chronic genus-level sensitivity distribution for the glyphosate dataset. Major
taxonomic groups are delineated by different symbols. Lines denoting the OPP chronic
benchmark values, GLI Tier II calculated chronic value, and modified HCos value are included.
271
-------
100,000
-I
~
Fish
A
Invertebrate
j
•
Nonvascular plant
1
¦
Vascular plant
1
- Modified HC05
j
—, .
GLI Tier II
1
........
* Lowest NOAEC, Vascular Plant
- Anabaena
10,000
m
m
re
w
o
Q. 1,000
>
w
¦ Lemna
Raphidocefis
^- Navicula
r Lowest NOAEC, Vascular Plant = 7,560 pg/L
Modified HC05 = 5,087 pg/L
/I
GLI Tier II = 316 pg/L
100
0.0
0.1
0.2 0.3 0.4 0.5 0.6 0.7
Chronic Sensitivity Centile
0.8
0.9
1.0
Figure 2. Glyphosate genus-level chronic SD.
Symbols represent Genus Mean Chronic Values (GMCVs) calculated using all available data from the Office of Pesticide Programs
(OPP) registration review document for glyphosate (U.S. EPA 2009).
272
-------
2.1.5.3 Glyphosate References
MRID 108171. Chronic toxicity of glyphosate to the Fathead Minnow (Pimephales promelas
Rafinesque). Unpublished study conducted by EF& G Bionomics Aquatic Toxicology
Laboratory, Wareham, MA. Study sponsored by Monsanto Company, St Louis, Missouri. 0178-
041-06/097759-5-8.
MRID 124763. McKee, R.J., W.A McAllister, andM. Schofield. 1982. Chronic Toxicity of
Glyphosate (AB-82-036) to Daphnia magna Under Flow-through Test Conditions. Unpublished
study conducted by Analytical Bio-Chemistry Laboratories, Columbia, Missouri. Report No.
AB-82-036.Study sponsored by Monsanto Chemical Company, St. Louis, Missouri. Study
completed September 9, 1982.
MRID 162296. Folmar, L.C., H. O. Sanders and A.M. Julin. 1979. Toxicity of the herbicide
glyphosate and several of its formulations to fish and aquatic invertebrates. Arch. Environn.
Contam. Toxicol 8: 269-278.
MRID 4023690. Incomplete MRID (see MRID 40236901).
MRID 40236901. Hughes, J.S. 1987. Volume I: The Toxicity of Glyphosate Technical to
Selenastrum capricornutum. Unpublished study conducted by Maclolm Pirnie, Inc., White
Plains, NY. Laboratory Project ID 1092-02-1100-1. Study sponsored by Monsanto Agricultural
Company, Chesterfield, Missouri. Study completed April 27, 1987.
MRID 40236902. Hughes, J.S. 1987. Volumen II: The Toxicity of Glyphosate Technical to
Navicula pelliculosa. Unpublished study conducted by Maclolm Pirnie, Inc., White Plains, NY.
Laboratory Project ID 1092-02-1100-2. Study sponsored by Monsanto Agricultural Company,
Chesterfield, Missouri. Study completed April 20, 1987.
MRID 40236904. Hughes, J.S. 1987. Volume IV: The toxicity of Glyphosate Technical to
Anabaena flos-aquae. Unpublished study conducted by Malcolm Pirnie, Inc. White Plains, NY.
Laboratory Project ID 1092-02-1100-4. Study sponsored by Monsanto Agricultural Company,
Chesterfield, Missouri. Study completed April 20, 1987.
MRID 40236905. Hughes, J.S. 1987. Volume V: The Toxicity of Glyphosate Technical to
Lemna gibba. Unpublished study conducted by Maclolm Pirnie, Inc., White Plains, NY.
Laboratory Project ID 1092-02-1100-5. Study sponsored by Monsanto Agricultural Company,
Chesterfield, Missouri. Study completed April 13, 1987.
MRID 44125704. Ward, T.J., J.P. Magazu and R.L. Boeri. 1996. Acute toxicity of Glygran
WDG to the Fathead Minnow. Pimephales promelas. Unpublished study conducted T.R. Wilbury
Laboratories, Inc, Marblehead, MA. Study No. 1008-LP. Sponsored by Lewis and Harrison,
Washington, DC. Study complected August 2, 1996.
MRID 44125705. Boeri, R.L., J.P. Magazu, and T.J. Ward. 1996. Acute Toxicity of Glygran
WDG to the Rainbow Trout, Oncorhynchus mykiss. Unpublished study conducted by T.R.
Wilbury Laboratories, Inc, Marblehead, MA. Study No. 1056-LH. Sponsored by Lewis and
Harrison, Washington, DC. Study complected August 2, 1996.
273
-------
MRID 44320629. Kent, S.J., D.S. Morris, J.E. Caunter and S.K. Comish. 1995. Glyphosate
Acid: Acute Toxicity to Rainbow Trout (Oncorhynchus mykiss). Unpublished study conducted
by Brixham Environmental Laboratory, ZENACA Limited, Devon, UK. Laboratory ID
BL5552/B. Study sponsored by ZENECA Ag Products, Wilmington, DE. Study completed on
September 15, 1995.
MRID 44320630. Kent, S.J., J.E. Caunter, D.S. Morris, and P.A. Johnson. 1995. Glyphosate
Acid, Acute Toxicity to Bluegill Sunfish (Lepomis macrochirus). Unpublished study conducted
by Brixham Environmental Laboratory, ZENACA Limited, Devon, UK. Laboratory ID
BL5553/B. Study sponsored by ZENECA Ag Products, Wilmington, DE. Study completed on
November 24, 1995.
MRID 44320631. Morris, D.S., S.J. Kent, A.J. Banner, and S.J. Wallace. 1995. Glyphosate Acid:
Acute Toxicity to Daphnia magna. Unpublished study conducted by Brixham Environmental
Laboratory, Zenaca Limited, Devon, UK Laboratory Project ID BL5551/B. Study sponsored by
ZENACA Ag Products, Wilmington, DE. Study completed July 26, 1995.
MRID 44320637. Smyth, D.V., S.J. Kent, D.S. Morris, D.J. Morgan, and S.E. Magor. 1995.
Unpublished study conducted by Brixham Environmental Laboratory, ZENACA Limited,
Devon, UK. Laboratory ID BL5550/B. Study sponsored by ZENECA Ag Products, Wilmington,
DE. Study completed on August 12, 1995.
MRID 44320638. Smyth, D.V., S.J. Kent, D.S. Morris, S.K. Comish, andN. Shillabeer. 1996.
Glyphosate Acid: Acute Toxicity to Duckweed (Lemna gibba). Unpublished study conducted by
Brixham Environmental Laboratory, Zenaca Limited, Devon, UK Laboratory Project ID
BL5662/B. Study sponsored by ZENACA Ag Products, Wilmington, DE. Study completed
January 31, 1996.
MRID 44320639. Smyth, D.V., N. Shillabeer, D.S. Morris, and S.J. Wallace. 1996. Glyphosate
Acid: Toxicity to Blue-green alga (Anabaena flos-aquae). Unpublished study conducted by
Brixham Environmental Laboratory, Zenaca Limited, Devon, UK. Laboratory Project ID
BL5698/B. Study sponsored by ZENACA Ag Products, Wilmington, DE. Study completed
March 9, 1996.
MRID 44320641. Smyth, D.V., S.J. Kent, D.S. Morris, P.A. Johnson, andN. Shillabeer. 1996.
Glyphosate Acid: Toxicity to the Freshwater Diatom (Navicula pelliculosa). Unpublished study
conducted by Brixham Environmental Laboratory, ZENACA Limited, Devon, UK. Laboratory
ID BL5673/B. Study sponsored by ZENECA Ag Products, Wilmington, DE. Study completed on
February 3, 1996.
MRID 45773101. Boeri, R.L. and T.J. Ward. 2002. Glyphosate Acid: Toxicity to the Duckweed,
Lemna sp. Unpublished study conducted by T.R. Wilbury Laboratories, Inc, Marblehead, MA.
Study Number 2066-LH. Study sponsored by Industria Prodotti Chimici, S.p.A, Milanese, Italy.
Study completed July 9, 2002.
Saka, M., N. Tada, and Y. Kamata. Chronic Toxicity of 1,3,5-Triazine Herbicides in the
Postembryonic Development of the Western Clawed Frog Silurana tropicalis. Ecotoxicol.
Environ. Saf. 147:373-381, 2018. ECOREF #178499
274
-------
U.S. Environmental Protection Agency. Pesticide Ecotoxicity Database (Formerly:
Environmental Effects Database (EEDB)). Environmental Fate and Effects Division, U.S.EPA,
Washington, D.C., 1992. ECOREF #344.
U.S. Environmental Protection Agency. 2024. Draft Comparison of Aquatic Life Protective
Values Developed for Pesticides under the Federal Insecticide, Fungicide, and Rodenticide Act
(FIFRA) and the Clean Water Act (CWA). EPA-820-D-24-002.
275
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