Environmental - Adverse Effects
Fluorinated and Fluoride Pesticides
beginning with
A-E • F-G H-P Q-Z
 
 

Note: This is not an exhaustive list.
When time allows more information will be added.

Fenazaflor - Insecticide - CAS No. 14255-88-0

LC50 guppies 0.2 ppm/24 hr [Martin, H. and C.R. Worthing (eds.). Pesticide Manual. 4th ed. Worcestershire, England: British Crop Protection Council, 1974. 267]
Ref: From Hazardous Substance Data Bank for LOVOZAL [a synonym for Fenazaflor] CASRN: 14255-88-0 at
Toxnet

Ref: Fenazaflor: from PAN Pesticides Database - Chemical Toxicity Studies on Aquatic Organisms.
http://www.pesticideinfo.org/PCW/List_AquireAcuteSum.jsp?CAS_No=14255-88-0&Rec_Id=PC38094&Taxa_Group=Fish
Fish
Bluegill Lepomis macrochirus 370.0 Highly Toxic
Largemouth bass Micropterus salmoides 340.0 Highly Toxic
Rainbow trout,donaldson trout Oncorhynchus mykiss 290.0 Highly Toxic

Fentrifanil - Acaracide, Insecticide - CAS No. 62441-54-7

Ref: Pesticide Action Network. Summary of Acute Toxicity for Organism Group - Fentrifanil
http://www.pesticideinfo.org/Detail_Chemical.jsp?Rec_Id=PC37409
Avg Species LC50 (ug/L)
Fish 
Sheepshead minnow Cyprinodon variegatus 9.00 Very Highly Toxic
Also see:
Initial Toxicological Assessment of Ambush, Bolero, Bux, Dursban, Fentrifanil, Larvin, and Pydrin: Static Acute Toxicity Tests with Selected Estuarine. Authors: Borthwick, P.W., and G.E. Walsh. Journal: EPA 600/4-81-076, U.S.EPA, Gulf Breeze, FL :9 Year: 1981 AQUIRE Reference No: 3644.

Fipronil - Acaricide, Insecticide, Wood Preservative - CAS No.120068-37-3

-- 2004. Louisiana crawfish farmers and landowners who suffered severe losses due to Icon contamination receive $45 million in a Class Action settlement. See:
A little background on the geneology and events of the insecticide Icon
Index to some documents and reports pertaining to the Class Action
News Items related to the settlement

-- Crawfish farmers upset with Aventis
August 1, 2001
-- St. Landry Parish District Court Judge James Genovese gave hundreds of Louisiana crawfish farmers a major victory in their case against Aventis, the manufacturer of the rice seed treatment Icon. In a July 30, 2001, ruling, the court granted certification for a class of crawfish farmers, finding they met all legal requirements for class certification in the lawsuit filed in Opelousas last year. According to Pat Morrow, an Opelousas attorney representing the farmers, "Crawfish farmers who feel their crawfish harvests have been damaged by Icon contamination can now come forward and join this class action suit."
However, the court denied class status for local seed distributor defendants. The class certification hearing began in April and concluded in June.
Judge Genovese's ruling allows anyone claiming financial losses and damages as a result of their crawfish crop's exposure to Icon beginning in January 1999 to join the lawsuit if he or she:

-- Purchased Icon-treated seed for rice operations in Louisiana, or
-- Farmed crawfish in Louisiana, or
-- Participated in a sharecropping arrangement for the farming of crawfish in Louisiana.

During the four days of trial, 36 witnesses testified, mainly crawfish farmers and experts. More than a dozen farmers told the same tale - once their crawfish crop was contaminated by Icon, the crawfish died. They became contaminated either because the crawfish were harvested in Icon-treated rice fields or because tailwater containing Icon or its metabolites flooded the crawfish crop.
Icon, the product name for the chemical fipronil, was commercially introduced in 1999. In 2000, Louisiana's crawfish production dropped 40 percent. Although its purpose is to kill the water weevils attacking rice plants, Icon, according to the trial testimony of farmers and experts, also kills crawfish.
Lousiana State University (LSU) scientists last year announced a possible link between Icon and crawfish mortality. In a survey of more than 90 commercial ponds, LSU scientists were told that in ponds where Icon-treated rice had been seeded the year before, crawfish production was generally well below average, says Dr. Greg Lutz, an aquaculture specialist with the Louisiana Agricultural Center. The survey was conducted in the 12 parishes that have the greatest share of both rice fields and crawfish ponds.
Dr. Ray McClain, professor at the LSU Ag Center's Rice Research Station in Crowley, tested a worst-case scenario for crawfish exposed to water that contained Icon-treated rice seed and found that most did not survive.
"This was a study under extreme conditions that are unlikely to occur in a natural setting," Dr. McClain says. "But we felt if the crawfish could survive these simulated conditions, then this would put to rest part of the controversy over Icon. But it didn't."
McClain in 1999 conducted similar experiments in which water containing Icon-treated seed did not significantly affect crawfish. "We simulated normal crawfish-growing conditions with the predominantly recommended rate of Icon," McClain said of his 1999 research. These results were corroborated by 1999 Aventis research. But in 2000, McClain increased the temperature of the water, used the maximum allowable rates of Icon and held the crawfish in the water longer.
Ref: AgJournal.com

http://www.fluorideaction.org/pesticides/fipronil.class.action.2002.htm

•••• Note: In the last 3 years several papers have been published on adverse environmental effects. See abstracts

Fipronil is considered highly toxic to rainbow trout and very highly toxic to bluegill
sunfish with an LC50 of 0.246 ppm and 0.083 ppm, respectively
. In early life-stage studies on rainbow trout fipronil affected larval growth with a NOEC of 0.0066 ppm and a LOEC (Lowest Observable Effect Concentration) of 0.015 ppm. The sulfone metabolite is 6.3 times more toxic to rainbow trout and 3.3 times more toxic than the parent compound to bluegill sunfish. Fipronil demonstrates a high toxicity toward freshwater aquatic invertebrates as well. In acute daphnia life cycle studies, fipronil affected growth: daphnid length was decreased at concentrations greater then 9.8 ppb. The sulfone metabolite is 6.6 times more toxic and the desulfinyl photodegradate 1.9 times more toxic on an acute basis to freshwater invertebrates than the parent compound (U.S. EPA 1996).
-- according to the ecological effects data on upland game birds, fipronil is highly toxic on an acute oral basis and very highly toxic on a sub-acute dietary basis. The oral LC50 for Bobwhite quail is 11.3 mg/kg, and the LC50 for 5-day dietary is 49 mg/kg (U.S EPA, 1996).
-- The sulfone metabolite is more toxic than the parent compound to certain bird species. This metabolite has shown a very high toxicity toward upland game birds and moderate toxicity toward waterfowl on an acute oral basis (U.S. EPA 1996, Bobe et al., 1997).
Ref:
December 2001 - ENVIRONMENTAL FATE OF FIPRONIL by Pete Connelly. Environmental Monitoring Branch, Department of Pesticide Regulation, California Environmental Protection Agency.

Vitellogenin (VTG) has been widely used as a biomarker of estrogenic exposure in fish, leading to the development of standardized assays for VTG quantification ... Stage-I juvenile copepods were individually reared to adults in aqueous microvolumes of the phenylpyrazole insecticide, fipronil, and whole-body homogenate extracts were assayed for VTN levels. Fipronil-exposed virgin adult females, but not males, exhibited significantly higher levels of VTN relative to control males and females. This crustacean VTN ELISA is likely useful for evaluating endocrine activity of environmental toxicants in copepods and other crustacean species.
Ref: Environ Toxicol Chem. 2004 Feb;23(2):298-305. An enzyme-linked immunosorbent assay for lipovitellin quantification in copepods: a screening tool for endocrine toxicity; by Volz DC, Chandler GT.

... One of its main degradation products, fipronil desulfinyl, is generally more toxic than the parent compound and is very persistent. There is evidence that fipronil and some of its degradates may bioaccumulate, particularly in fish. Further investigation on bioaccumulation is warranted, especially for the desulfinyl degradate. The suitability of fipronil for use in IPM must be evaluated on a case-by-case basis. In certain situations, fipronil may disrupt natural enemy populations, depending on the groups and species involved and the timing of application. The indications are that fipronil may be incompatible with locust IPM; hence, this possibility requires further urgent investigation. It is very highly toxic to termites and has severe and long-lasting negative impacts on termite populations. It thus presents a long-term risk to nutrient cycling and soil fertility where termites are "beneficial" key species in these ecological processes. Its toxicity to termites also increases the risk to the ecology of habitats in which termites are a dominant group, due to their importance as a food source to many higher animals. This risk has been demonstrated in Madagascar, where two endemic species of lizard and an endemic mammal decline in abundance because of their food chain link to termites. Fipronil is highly toxic to bees (LD50 = 0.004 microgram/bee), lizards [LD50 for Acanthodactylus dumerili (Lacertidae) is 30 micrograms a.i./g bw], and gallinaceous birds (LD50 = 11.3 mg/kg for Northern bobwhite quail), but shows low toxicity to waterfowl (LD50 > 2150 mg/kg for mallard duck). It is moderately toxic to laboratory mammals by oral exposure (LD50 = 97 mg/kg for rats; LD50 = 91 mg/kg for mice). Technical fipronil is in toxicity categories II and III, depending on route of administration, and is classed as a nonsensitizer. There are indications of carcinogenic action in rats at 300 ppm, but it is not carcinogenic to female mice at doses of 30 ppm. The acute toxicity of fipronil varies widely even in animals within the same taxonomic groups. Thus, toxicological findings from results on standard test animals are not necessarily applicable to animals in the wild. Testing on local species seems particularly important in determining the suitability of fipronil-based products for registration in different countries or habitats and the potential associated risk to nontarget wildlife. Risk assessment predictions have shown that some fipronil formulations present a risk to endangered bird, fish, and aquatic and marine invertebrates. Great care should thus be taken in using these formulations where they may impact any of these endangered wildlife groups. Work in Madagascar has highlighted field evidence of this risk. The dose levels at which fipronil produces thyroid cancer in rats are very high and are unlikely to occur under normal conditions of use. There is also dispute as to whether this is relevant to human health risk. However, as fipronil is a relatively new insecticide that has not been in use for long enough to evaluate the risk it may pose to human health, from data on human exposure to the product, a precautionary approach may be warranted. The use of some fipronil-based products on domestic animals is not recommended where handlers spend significant amounts of time grooming or handling treated animals. In general, it would appear unwise to use fipronil-based insecticides without accompanying environmental and human health monitoring, in situations, regions, or countries where it has not been used before, and where its use may lead to its introduction into the wider environment or bring it into contact with people. Further work is needed on the impacts of fipronil on nontarget vertebrate fauna (amphibians, reptiles, birds, and mammals) in the field before the risk to wildlife from this insecticide can be adequately validated. Further field study of the effects of fipronil on the nutrient cycling and soil water-infiltration activities of beneficial termites is required to assess the ecological impacts of the known toxicity of fipronil to these insects.
Ref: Fipronil: environmental fate, ecotoxicology, and human health concerns; by Tingle CC, Rother JA, Dewhurst CF, Lauer S, King WJ. Rev Environ Contam Toxicol. 2003;176:1-66.

Copepods are the most abundant arthropods on earth and are often the most important secondary producers in estuarine/marine food webs. The new GABA (gamma-aminobutyric acid)-disrupting insecticide fipronil (FP) induces unique sex-specific reproductive dysfunction in male meiobenthic copepods, leading to trans-generational population depression at environmentally realistic concentrations (0.63 microg/L). Using a newly developed 96-well microplate lifecycle bioassay, more than 700 individual Stage-I juveniles were reared to adulthood in as short as 12 days in only 200 microL of control (CTL) or 0.63 microg-FP/L seawater solution. Individual virgin male: female pairs were then cross-mated for all possible combinations within and across rearing treatments and allowed to mate for an additional 12 days in CTL or 0.63 microg-FP/L solution. FP at 0.63 microg/L caused no significant lethality to any mating combinations but evoked 73% or 89% inhibition of reproduction when FP-reared males were mated with either a control- or FP-reared female in FP solution, respectively. In contrast, when CTL-reared males were mated with FP-reared females in FP solution, there was no difference in reproductive success compared to FP-free controls. When FP-reared males were mated with either female group in FP-free solution, these mating pairs displayed a 3-day delay in time to brood sac extrusion but ultimately did reproduce. As fipronil (1) has a high K(ow), (2) is persistent in sediments where meiobenthic copepods live, and (3) has been detected in estuarine waters >0.7 microg/L, it may pose high risk to copepod production in estuarine systems.
Ref: Environ Sci Technol. 2004 Jan 15;38(2):522-8. Phenylpyrazole insecticide fipronil induces male infertility in the estuarine meiobenthic crustacean Amphiascus tenuiremis; by Cary TL, Chandler GT, Volz DC, Walse SS, Ferry JL

Excerpt from Abstract: ... Because the presence of sublethal doses or concentrations may also alter the behavior of foraging insects, we attempted to devise a quantifiable and accurate protocol for evidencing various alterations in free-flying bees. Such a protocol was illustrated by testing new classes of systemic insecticides. The protocol focused on video recording to quantify the foraging activity of small colonies of honey bees confined in insect-proof tunnels ... Two plant-systemic insecticides were tested at contamination levels 70 times lower than the 50% of the lethal concentration. Imidacloprid, at 6 microg/kg, clearly induced a decrease in the proportion of active bees. Fipronil, at 2 microg/kg, induced an additional decrease in attendance at the feeder. Such levels are still higher than the corresponding lowest observable effect concentration (LOEC). Our protocol, which provided intermediate conditions between field and laboratory conditions, allowed the quantification, with an enhanced level of sensitivity, of sublethal effects on foraging bees.
Ref: A method to quantify and analyze the foraging activity of honey bees: relevance to the sublethal effects induced by systemic insecticides. By Colin ME et al. Arch Environ Contam Toxicol. 2004 Oct;47(3):387-95

Reptiles in arid and semiarid zones are frequently exposed to insecticides sprayed to control locusts and grasshoppers. We evaluated the toxicity and pathogenicity of new biological and chemical control agents to the fringe-toed lizard Acanthodactylus dumerili in Mauritania, West Africa ... The second agent tested was fipronil (Adonis), a phenylpyrazole insecticide. A single dose of 30 microg fipronil/g body weight was administered via contaminated prey or stomach instillation. The percentage of dead or moribund lizards at four weeks posttreatment was 62.5% in animals fed contaminated prey and 42.0% in gavaged animals. In both tests, survivors showed significantly reduced feeding activity, food consumption, body weight, and organ-to-body-weight ratios (liver and/or fat body). The high toxicity of fipronil to lizards was not previously known, suggesting that follow-up studies (e.g., subacute dietary tests) are needed to provide adequate data for risk assessment.
Ref: Environ Toxicol Chem. 2003 Jul;22(7):1437-47. Toxicity and pathogenicity of Metarhizium anisopliae var. acridum (Deuteromycotina, Hyphomycetes) and fipronil to the fringe-toed lizard Acanthodactylus dumerili (Squamata: Lacertidae); by Peveling R, Demba SA.

Flocoumafen - Rodenticide - CAS No. 90035-08-8

In a laboratory study, radiolabelled flocoumafen was applied at a nominal rate of 50 mg/kg to 3 different soil types. After 217 days, 84 to 89% of the applied activity remained as unchanged flocoumafen, 2-4% was recovered as carbon dioxide and 3-5% remained as unextractable residue... Hydrolysis was only studied at 50C, at which temperature flocoumafen was not readily broken down. The half-life at pH5 was 30-31 days, pH7 447 days and pH9 445 days...
Toxicity to Aquatic Organisms.
Technical flocoumafen was highly toxic to fish when dispersed in acetone with 96 h LC values of 0.091 mg/l (daily water change) and 0.32 mg/l (static) in rainbow trout and 0.22 mg/l (static) in carp... Flocoumafen was highly toxic to the water flea (Daphnia magna), the 49 h EC 50 for technical in acetone being 0.66 mg/l, and 280 mg formulation/1 (equivalent to 1.4 mg ai/l). The 96 h EC 50 for technical flocoumafen to Selenastrum capricornutum (planktonic algae) was 1.1 mg/l.
Effect on Non-target species:
The following trials have been carrid out by MAFF using 0.005% flocoumafen on medium oatmeal and/or whole wheat base prepared from 0.1% concentrate.

(a) Surplus baiting technique, Welshpool area, R-norvegious infestations - 6 sites. 3 non-target casualties were recorded during these trials including a grey squirrel, a rabbit and a robin).
(b) Minimal baiting technique, Welshpool area,
R-norvegious infestations - 6 sites. These have not yet been reported.
(C) Surplus baiting technique, Hampshire, suspected Difenacoum resistant R-norvegious infestations - 6 sites. Two of these farm sites were frequented by larged mixed flocks of finches and these were observed to enter bait boxes and to feed on bait. More than 30 bird casualties were recorded, these included 4 pheasants, 1 partridge, 1 moorhen and numerous passerine birds. Post-mortem of these birds revealed severe hemorrhaging or blue colouration of the bill. No residues data for these casualties were supplied.
(D) Surplus baiting technique, West Sussex, Mus musculus infestations - 10 sites (granaries, feed stores, utility barm). Mice died from 3 to 10 days after start of baiting. This was an efficacy trial only and so non-target casualties were not reported.

Three further trials were carried out at Kent farms by Shell Research Limited in December 1984 using a bait formulation of 0.005% flocoumafen on a cut wheat base. Surplus baiting was carried out for 3 weeks using an agreed wildlife monitoring protocol. A total of 67 dead non-target birds and 17 dead non-target mammals (mice, voles and 1 grey squirrel) were found around farm buildings. Of these, 28 were judged to have resulted from flocoumafen poisoning based on haemorrhaging found at post-mortem. These 28 deaths comprised small passerine birds. Residue analysis of these carcases has not yet been reported. Few birds were found during the baiting and early post-baiting period other than 21 house sparrows at 1 site. The majority of dead birds were not found until 2 to 4 weeks after baiting finished, a period which also had more severe weather conditions. One dead robin was found during the third week of baiting lying beside a bait tray underneath the protective cover. Flocoumafen residues in 25 dead rats found above ground indicated whole body residues varied generally between 0.5 and 4.3 mg/kg bw. Between 20 and 40% of the total body burden of flocoumafen was found in the rat livers.
Ref: Evaluation on Flocoumafen. April 1987. UK Department for Environment, Food and Rural Affairs, Pesticides Safety Directorate, Mallard House, Kings Pool 3 Peasholme Green, York YO1 7PX. Also available at
http://www.pesticides.gov.uk/citizen/evaluations/evallist.htm

In the mid to late 1970s, a group of compounds known as the "second generation" anticoagulants were developed. These compounds include bromadiolone, difenacoum, brodifacoum, flocoumafen and difethialone, and are considerably more toxic, killing rodents that are resistant to the first generation anticoagulants. With these compounds rodents may eat enough to kill them in a single day or in some cases in a single feeding, but they still will take several days to die. While very successful and widely used, these compounds and particularly the latter three have quite a high toxicity to non-target animals and pose a significant secondary hazard threat. In a sense, they lack some of the advantages of the first-generation anticoagulants. Some resistance has also been documented to second-generation anticoagulants in a few areas.
Ref: Advances in IPM Rodent Control in Agriculture. CISSE W. SPRAGINS, Rockwell Laboratories Ltd., Minneapolis, MN, USA. http://www.sustdev.org/journals/edition.01/download/01.135.pdf

Florasulam - Herbicide - CAS No. 145701-23-1

European Union: Only uses as herbicide may be authorised. For the implementation of the uniform principles of Annex VI, the conclusions of the review report on florasulam, and in particular Appendices I and II thereof, as finalised in the Standing Committee on the Food Chain and Animal Health on 19 April 2002 shall be taken into account. In this overall assessment Member States: Ñ should pay particular attention to the potential for groundwater contamination, when the active substance is applied in regions with vulnerable soil and/or climatic conditions. Conditions of authorisation must include risk-mitigation measures, where appropriate.
Ref: COUNCIL DIRECTIVE of 15 July 1991 concerning the placing of plant protection products on the market 91/414/EEC - amended by 2003/5/EC (OJ No. L 8, 14.01.2003, p. 7)
http://www.uksup.sk/download/oso/20030409_smernica_rady_91_414_eec.pdf

Fluazifop-butyl - Herbicide - CAS No. 69806-50-4

Highly toxic to Zooplankton.
Ref:
Pesticide Action Network Acute Aquatic Ecotoxicity Summaries.

-- Environmental Bioconcentration: An estimated BCF of 1500 was calculated for fluazifop-butyl(SRC), using a measured log Kow of 4.5(1) and a recommended regression-derived equation(2). According to a classification scheme(3), this BCF suggests that bioconcentration in aquatic organisms is very high(SRC).
-- Environmental Fate/Exposure Summary: ... If released into water, this compound is expected to adsorb strongly to suspended solids and sediment in the water column based on its estimated Koc. Volatilization from water surfaces is not expected to be an important fate process based on the estimated Henry's Law constant for this compound. The potential for bioconcentration in aquatic organisms is very high based on an estimated BCF of 1500. Hydrolysis half-lives of 2.2 years and 79 days have been estimated for fluazifop-butyl at pHs 7 and 8, respectively. Abiotic hydrolysis of fluazifop-butyl has been observed to be catalyzed by soil colloids. (SRC)
-- AQUATIC FATE: ... According to a classification scheme(5), an estimated BCF of 1500(3,SRC), from a measured log Kow(2), suggests that bioconcentration in aquatic organisms is very high(SRC). Biodegradation of fluazifop-butyl in aquatic systems may be important(SRC), given its microbial degradation in moist soils(6). Hydrolysis half-lives of 2.2 years and 79 days have been estimated for fluazifop-butyl at pHs 7 and 8, respectively(7)...
-- TERRESTRIAL FATE: ... Biodegradation of fluazifop-butyl in soil is expected to be important(SRC); fluazifop-butyl is rapidly biodegraded in moist soils, with a half-life of less than 1 week; the major degradation product being fluazifop(4).
-- Soil Adsorption/Mobility: ... Fluazifop-butyl is of low mobility in soil(4). Fluazifop-butyl has been found to bind strongly with homoionic clays(5).
Ref: Hazardous Substance Data Bank for FLUAZIFOP-BUTYL CASRN: 69806-50-4 from Toxnet.

Fluazifop-P-butyl - Herbicide - CAS No. 79241-46-6

3.3 Environmental Degradation. Environmental fate studies indicate that fluazifop-P-butyl is not mobile and not persistent. The predominant environmental fate process appears to be microbially-assisted hydrolysis to fluazifop acid and 5-trifluoromethyl-2-pyridone [major metabolites], which are considered to be mobile and therefore, can potentially reach surface and ground waters. Aerobic soil metabolism studies showed that the half-life of the parent ester is on the order of a few hours. The properties of fluazifop acid, namely high mobility and long persistence in water (78-day hydrolysis half-life at pH 7) and anaerobic soil (half-life 1 to 3 years, MRID# 92067033) indicate that it might persist from year to year in the subsurface, and move with flowing ground water. The degradate 5 trifluoromethyl-2-pyridone does not sorb to soil, indicating very high mobility. A minor degradate is 2-(4-hydroxyphenyl)-5-trifluromethylpyridine. There are no data on its mobility, but it is expected to be similar to that of fluazifop acid. ... Water softening, in which the alkalinity is raised to pH 10 or 11 by the addition of lime or soda ash, will rapidly degrade the parent fluazifop-P-butyl to fluazifop acid (page 11-12).
Ref: December 10, 2004. US EPA> Fluazifop-P-butyl: Revised HED Chapter of the Tolerance Reassessment Eligibility Decision (TRED) Document. EPA Docket number: OPP-2004-0347-0003
http://www.fluorideaction.org/pesticides/f-p-b.opp-2004-0347-0003.pdf
-- see also: http://www.fluorideaction.org/pesticides/f-p-b.opp-2004-0347-0011.pdf

Effects on aquatic organisms: Fluazifop-p-butyl may be highly to moderately toxic to fish, but only slightly toxic to other aquatic species, such as invertebrates. The reported 96-hour LC50 values for the technical product in fish species are 0.53 mg/L in bluegill sunfish and 1.37 mg/L in rainbow trout [5], indicating very high to high toxicity. The 48-hour LC50 in Daphnia magna (an aquatic invertebrate) is reported as greater than 10 mg/L [5], indicating only slight toxicity.
Ref: Fluazifop-p-butyl. E X T O X N E T Pesticide Information Profiles. Revised June 1996.
http://ace.ace.orst.edu/info/extoxnet/pips/fluazifo.htm

Fluazinam - Fungicide - CAS No. 79622-59-6

-- Ecological Effects Summary:
a. Aquatic (Acute/Chronic Hazard Summary) Fluazinam is considered to be very highly toxic to highly toxic to fish (freshwater and estuarine/marine) on an acute basis (LC50 = 0.036 - 0.11 ppm). Chronic freshwater NOAEC/LOAEC values were calculated at 0.0053 - 0.00069 ppm and 0.010 - 0.014 ppm, respectively, with larval survival, reduced number of spawns, and growth as the endpoints affected. Acute toxicity values for aquatic invertebrates suggest that fluazinam is highly toxic to freshwater invertebrates (Daphnia EC50 = 0.18 - 0.22 ppm) and very highly toxic to estuarine/marine invertebrates (oyster EC50 = 0.0047 and mysid shrimp EC50 = 0.039 ppm ). Chronic toxicity to invertebrates are only represented through the Daphnia magna life cycle where the NOAEC was calculated at 0.068 ppm and the LOAEC at 0.140 ppm.. The endpoints affected for this study were reproductive (reduced number of young per female) and growth effects. No acceptable data have been submitted to assess the chronic effects of fluazinam to estuarine/marine fish or invertebrates. An estuarine/marine fish life-stage toxicity test (Guideline 72-4a) and an estuarine/marine invertebrate life-cycle toxicity test (Guideline 72-4b) are required to fulfill these requirements.
-- b. Risk to Aquatic Organisms (Acute/Chronic) The risk assessment suggests that exposure of this compound to fish (freshwater and estuarine/marine) through the proposed use patterns (peanuts and potatoes) can result in acute (restricted use and endangered species concern category) and chronic risk. Exposure to aquatic invertebrates (freshwater and estuarine/marine) from peanut use can result in acute risk (restricted use and endangered species concern category). No acute or chronic exceedences are expected for freshwater invertebrates from the potato use. Chronic exposure to estuarine/marine fish and invertebrates could not be calculated at this time because of a lack of appropriate data.
-- d. Risk to Avian Species (Acute/Chronic) Although acute exposure should result in minimal toxic effects to birds, the risk assessment suggests that the proposed uses can cause chronic (reduced growth in young) effects in birds. RQ values were calculated for exposure to peanuts (maximum EECs RQ = 1.0 - 1.8 and 56 day average EECs RQ = 1.1 ppm) and potatoes (maximum EECs RQ = 1.0 - 1.5 and 56 day average(RQ = 1).
-- e. Risk to Mammalians (Acute, Chronic) The risk assessment suggests that the proposed uses can result in chronic risk to mammalians (herbivores and insectivores). RQ values were calculated for exposure to peanuts (maximum EECs RQ = 1.6 - 3.5 and 56 day average EECs RQ = 1.0 - 2.2) and potatoes (maximum EECs RQ = 1.0 - 1.9 and 56 day average EECs RQ = 1.4 - 3.0). Acute concerns appear to be focused on grass eating endangered mammals (RQ = 0.1)
Ref: US EPA Pesticide Fact Sheet. Fluazinam. August 10, 2001.

http://www.epa.gov/opprd001/factsheets/fluazinam.pdf

Fluazolate - Herbicide - CAS No. 174514-07-9

-- 5.1 - Members considered the first evaluation of a full safety and efficacy dossier supporting an application for approval of fluazolate, a new herbicide intended for pre-emergence use on winter wheat for control of annual grasses and broad-leaved weeds.
--
5.2 - The Committee confirmed that they considered two of the metabolites (M01 and M06) to be "relevant metabolites" in terms of the Uniform Principles and that there would therefore be a legal requirement to prevent these metabolites from entering groundwater at predicted concentrations above 0.1 m g/l. The Committee agreed that there may be scope to achieve this using a regulatory approach that prevented the product being used on certain soil series. However, this approach would only be viable if it were shown to be enforceable and could be audited. The Committee noted that this kind of approach might become more practical as a consequence of ongoing developments such as the DEFRA Geographical Information System (GIS) field mapping project.
5.3 - In addition to the problem of ground water contamination by metabolites, the Committee identified several other issues that would need to be resolved before approval could be recommended. Reference values could not be set due to evidence from observations in humans following a contamination incident, which suggested that fluazolate was absorbed and that a biological effect occurred at lower doses than those which produced effects in animal studies. There were also concerns over certain aspects of the reproductive toxicity studies in animals. The Committee agreed that toxicological data would be required on the metabolite M06 if significant human exposures were predicted to result from contamination of groundwater or residues in following crops. There were also concerns regarding the buffer zone distance that would be needed to manage the risk to algae in UK, and about possible risks to non-target plants and adjacent crops.
5.4 - The Committee concluded that until these various issues have been resolved, approval could not be recommended.
Ref: UK Advicory Committee on Pesticides. January 17, 2002.

http://www.fluorideaction.org/pesticides/fluazolate.uk.jan17.2002.htm

Flucarbazone-sodium - Herbicide- CAS No. 181274-17-9

Potential to Contaminate Drinking Water. Because of the high solubility and mobility of flucarbazone-sodium and the high mobility and persistence of its sulfonamide and sulfonic acid degradates, both surface and ground water contamination are likely to occur.
Aquatic: Flucarbazone-sodium is practically non-toxic to freshwater fish on an acute basis (96- hour LC50 > 96.7 ppm). With chronic exposure, flucarbazone-sodium reduces fish growth at 2.75 ppm, with a No Observable Adverse Effects Concentration (NOAEC) established at 1.25 ppm (1250 ppb). It is practically non-toxic to freshwater invertebrates on an acute basis (EC50 > 109 ppm) and does not reduce reproduction of aquatic invertebrates at the NOAEC of 115 ppm (115,000 ppb). The NOAECs for fish and aquatic invertebrates are well above the peak estimated environmental concentration (EEC) in water of 1.42 ppb.
-- Restrictions for Use on Wheat:
1. Do not apply by air.
2. Do not apply through any type of irrigation system.
3. Do not mix, load or clean spray equipment within 33 feet of well-heads or aquatic systems, including marshes, ponds, ditches, streams, lakes, etc.
4. Do not apply within 50 feet of well-heads or aquatic systems.
5. Do not apply when rain is expected within the next hour.
6. Make only one application per growing season at a maximum rate of 0.61 ou
nces of product per acre (0.027 pounds of the active ingredient, flucarbazone-sodium). 7. Observe a minimum interval to harvest of 60 days after treatment, after which wheat grain and straw from treated fields may be fed to livestock.
-- SUMMARY OF DATA GAPS
-- Environmental Fate (Field dissipation data and an aerobic aquatic metabolism study)
Ref: US EPA Pesticide Fact Sheet for Flucarbazone-sodium. September 29, 2000.
http://www.epa.gov/opprd001/factsheets/flucarbazone.pdf

Fluchloralin - Herbicide - CAS No. 33245-39-5

Abstract: The persistence, binding, and metabolism of six dinitroaniline herbicides, including trifluralin, profluralin, dinitramine, butralin, fluchloralin, and chlornidine, added to Matapeake silt loam were determined after 3, 5, and 7 months. Dinitramine was rapidly degraded during the first 5 months, while butralin and chlornidine were less persistent than fluchloralin, profluralin, and trifluralin after 7 months. The latter three herbicides were similar in persistence and binding properties. The parent herbicide was the major extractable product detected in soil at each sampling time. Degradation products were identified by cochromatography on thin-layer plates, retention times on gas-liquid and high-pressure liquid chromatography, and mass spectral analysis. Dealkylated and cyclic derivatives of the parent herbicide were detected as metabolites. The cyclic products included benzimidazole derivatives of dinitramine, trifluralin, and fluchloralin; a morpholine derivative of chlornidine; and a quinoxaline derivative of fluchloralin. A unique metabolite of butralin was derived from the parent material by the loss of one nitro substituent.
Ref: Persistence and metabolism of dinitroaniline herbicides in soils; by P. C. Kearney et al. Pesticide Biochemistry and Physiology; 6:3; 229-238 June 1976

Data from Pesticide Action Network :
http://www.pesticideinfo.org/PCW/List_AquireAcuteSum.jsp?CAS_No=33245-39-5&Rec_Id=PC33166
Common Name Scientific Name Avg Species LC50 (ug/L) LC50 Std Dev Number of Studies Avg Species Rating
FISH
Channel catfish Ictalurus punctatus 255.0 135.0 2 Highly Toxic
Bluegill Lepomis macrochirus 25,218 34,683 5 Slightly Toxic
Rainbow trout,donaldson trout Oncorhynchus mykiss 6,001 7,408 7 Moderately Toxic
INSECTS
Midge Chironomus plumosus 31.1 25.5 2 Very Highly Toxic
MOLLUSCS
Snail Bellamya bengalensis 202.5 24.5 2 Highly Toxic
ZOOPLANKTON
Scud Gammarus pseudolimnaeus 56.0   1 Very Highly Toxic

Flucofuron - Insecticide - CAS No. 370-50-3

Environmental Quality Standards (EQSs) for the protection of saltwater life have been proposed (and were put into legislation in 1989) for the following chemicals used as mothproofing agents; PCSDs; cyfluthrin; sulcofuron; flucofuron and permethrin... Data were also scarce for flucofuron and sulcofuron. However, Zabel et al (1988) concluded that they were less toxic and less likely to accumulate than PCSDs, although, based on the available data they can still be considered to be highly toxic to fish and invertebrates... toxicity of flucofuron to invertebrates and fish at concentrations above the EQS of 1 mg l-1 in the water column
Ref: UK Marine Special Areas of Conservation. Mothproofing chemicals.
http://www.ukmarinesac.org.uk/activities/water-quality/wq8_25.htm
or
http://www.fluoridealert.org/pesticides/Flucofuron.UK.Moth.water.htm

Flucythrinate - Acaricide, Insecticide - CAS No. 70124-77-5

-- Flucythrinate accumulated in the edible tissues of bluegill sunfish to 487 times the concentration in surrounding waters (11).
Ref: E X T O X N E T Pesticide Information Profile Flucythrinate.

http://www.fluoridealert.org/pesticides/Flucythrinate.Profile.PMEP.htm

Acute Aquatic Ecotoxicity Summaries for Flucythrinate on All Taxa Groups
Ref: PAN Pesticides Database - Chemical Toxicity Studies on Aquatic Organisms
http://www.pesticideinfo.org/PCW/List_AquireAcuteSum.jsp?CAS_No=70124-77-5&Rec_Id=PC33167
Common Name Scientific Name Avg Species LC50 (ug/L) LC50-Std Dev Number of Studies Avg Species Rating
Fish     
Japanese eel Anguilla japonica 8.12 1.03 4 Very Highly Toxic
Catfish Clarias lazera 4.50 - 1 Very Highly Toxic
Sheepshead minnow Cyprinodon variegatus 1.35 0.25 2 Very Highly Toxic
Common, mirror, colored, carp Cyprinus carpio 5.80 5.20 2 Very Highly Toxic
Bluegill Lepomis macrochirus 0.60 0.12 2 Very Highly Toxic
Fathead minnow Pimephales promelas 0.70 0.50 2 Very Highly Toxic
Insects     
Yellow fever mosquito Aedes aegypti 1.16 0.16 2 Very Highly Toxic
Caddisfly Brachycentrus americanus 0.04 0.02 5 Very Highly Toxic
Stonefly Pteronarcys dorsata 0.02 0.0040 6 Very Highly Toxic
Zooplankton        
Scud Gammarus lacustris 0.13 0.07 3 Very Highly Toxic

Fludioxonil - Fungicide - CAS No. 131341-86-1

-- According to the SSLRC [Soil Survey and Land Research Centre] soil persistence classification, fludioxonil is classed as 'very persistent' (page 100).
-- Fludioxonil is very persistent in soil (see Section 12), therefore, there is a chronic risk to earthworms...
--
Data on the acute toxicity of the active ingredient to aquatic organims indicate that fludioxonil is of relatively high aquatic toxicity to fish, aquatic invertebrates and aquatic plants - see Table below
Evaluation of Fludioxonil. UK Department for Environment, Food and Rural Affairs, Pesticides Safety Directorate. March 1995.
Note: this pdf document is large with no search engine.
Available at:

http://www.pesticides.gov.uk/PSD_PDFs/Evaluations/126_fludioxonil.pdf

Fludioxnol: Table 13.2 Acute Toxicity of technical fludioxonil to fish, aquatic invertebrates and algae (pages 119-120)
Ref: Evaluation of Fludioxonil. UK Department for Environment, Food and Rural Affairs, Pesticides Safety Directorate. March 1995. Note: this pdf document is large with no search engine. Available at: http://www.pesticides.gov.uk/PSD_PDFs/Evaluations/126_fludioxonil.pdf
Fish species Test type 96 hour LC50 mg ai/l NOEC mg ai/l Nominal/Acutal
Rainbow Trout static 0.50 <0.26 Actual
Bluegill Sunfish static 0.31 <0.14 Actual
Common Carp static 1.5 <1.0 Actual
Catfish static 0.63 <0.58 Actual
Rainbow Trout flow-through 0.23 <0.06 Actual
Rainbow Trout flow-through 0.47 <0.17 Actual
Sheepshead Minnow flow-through 0.54 <0.39 Actual
Sheepshead Minnow flow-through 1.3 <0.38 Actual
Aquatic Invertebrates Test Type 48 hour EC50 mg ai/l NOEC mg ai/l Nominal/Actual
Daphnia magna static 1.1 0.32 Nominal
Daphnia magna flow-through 0.90 <0.50 Actual
Daphnia magna flow-through 0.82 <0.12 Actual
Daphnia magna flow-through 0.27 [96 hr EC50] 0.075 Actual
Aquatic Plants EC50 mg ai/l NOEC mg ai/l Nominal/Actual
Scenedesmus subspicatus 72 hr EC 50 = 0.93 72 hr NOEC = 0.05 Actual
Raphidocellis subcapitata 120 hr EC 50 = 0.092 120 NOEC ² 0.028 Actual


Fluenetil (Fluenethyl) - Acaricide - CAS No. 4301-50-2

Acute Aquatic Ecotoxicity Summaries for Fluenethyl on Fish
Ref: PAN Pesticides Database - Chemical Toxicity Studies on Aquatic Organisms
http://www.pesticideinfo.org/PCW/List_AquireAcuteSum.jsp?CAS_No=4301-50-2&Rec_Id=PC37991&Taxa_Group=Fish
Common Name Scientific Name Avg Species LC50 (ug/L) LC50-Std Dev Number of Studies Avg Species Rating
Fish 
Rainbow trout, donaldson trout Oncorhynchus mykiss 962.0 78.0 2 Highly Toxic

Flufenacet - Herbicide - CAS No. 142459-58-3

Flufenacet is highly toxic to terrestrial, semi-aquatic, and aquatic plants. Adverse effects to surrounding plant communities may occur if flufenacet moves off the treatment site. Endangered mammals and plants also may be affected. Environmental hazard precautionary statements are required. Bayer Corporation will conduct a product stewardship program to assist growers in reducing the herbicide's impact on non-target organisms.
Ref: US EPA Pesticide Fact Sheet. April 1998.

http://www.epa.gov/opprd001/factsheets/flufenacet.pdf

... The study implies that, because of its moderate to high adsorption, flufenacet is likely to persist in soil for some time. However, the possibility of its movement by leaching or surface run off is less.
Ref: PubMed abstract: Gajbhiye VT et al. (2001). Adsorption-desorption behaviour of flufenacet in five different soils of India. Pest Manag Sci. Jul;57(7):633-9.

Flufenoxuron - Acaricide, Insecticide, Herbicide - CAS No. 101463-69-8

-- Environmental fate, behaviour and toxicology. Flufenoxuron does not readily break down in the environment. The most rapid form of degradation reported was aqueous photolysis, with a half-life (T 1/2) of 11 days. However the solubility of flufenoxuron, in water is extremely low (0.0040 mg.1-1 at pH7 and 25C). Flufenoxuron readily adsorbs to organic matter. Consequently it is immobile and also persists in soil (T 1/2 42 days for clay loam and >6 months for sandy loam)...
--
Flufenoxuron is extremely toxic to Daphnia (48 hour EC50 0.065 ug.1-1). This is consistent with the compound's mode of action against target pests, inhibiting chitin synthesis/deposition. No fish toxicity could be established due to flufenoxuron's low water solubility and the failure to use an appropriate solvent vehicle. Similarly, no accurate toxicity to freshwater algae was establishsed...Pond overspray studies indicated that flufenoxuron could have adverse efects on aquatic invertebrate populations, especially crustacea zooplankton. Flufenoxuron may also have the potential to bioaccumulate in fish and aquatic gastropods although this has not been confirmed in a laboratory bioaccumulation study. ... due to the acute toxicity of flufenoxuron to Daphnia and the lack of any suitable fish toxicity data, products containing the compound are to be classified 'EXTREMELY DANGEROUS TO FISH AND OTHER AQUATIC LIFE."
Ref:
December 1995. Evaluation of Flufenoxuron use as a public hygiene insecticide. UK: Health and Safety Executive, Biocides & Pesticides Assessment Unit. Available at http://www.pesticides.gov.uk/citizen/evaluations/evallist_alphabet.htm

Flumequine - Microbiocide - CAS No. 42835-25-6

-- Coyne et al. (1994) investigated the concentration of OTC in the sediment of two cages at a fish farm site, and found half-lives of 16 and 13 days. Oxytetracycline, oxolinic acid, flumequine and sarafloxacine were all found to be very persistent in sediments (Hektonen et al. 1995). In the deeper layer of the sediment hardly any degradation had occurred after 180 days and a calculated half-life of more than 300 days was estimated. The residues in the top layer of the sediment disappeared more rapidly. The removal of these substances from the sediment is most probably due to leaching and redistribution rather than degradation.
-- Samuelsen et al. (1994) showed that the toxicity of OTC to bacteria declined rapidly in sediments, although no degradation occurred. Binding to ions (Ca2+, Mg2+) and other substances were mentioned as possible explanation for the inactivation of oxytetracycline., The same study found that both oxolinic acid and flumequine sustained their antimicrobial activity over a six month period in sediment material.
Ref: Environmental Project no. 659, 2002. Environmental Assessment of Veterinary Medicinal Products in Denmark. 3. Environmental fate and occurrence of Veterinary Medicinal Products. Danish Environmental Protection Agency
.
http://www.mst.dk/udgiv/publications/2002/87-7944-971-9/html/kap03_eng.htm

ABSTRACT: Oxytetracycline, oxolinic acid and flumequine are antibacterial agents commonly used in fish farming, especially because of their broad spectrum of activity. About 80 % of these drugs reached the environment because of their administration as medicated pelleted feed and their low oral bioavailability. Under these conditions, there is a clear need in studying the impact of these treatments on the freshwater environment. A spatio-temporol study was then realised to estimate the concentration of oxolinic acid, flumequine and oxytetracycline in water, sediments and bryophytes all along a coast river. The 25 sampling points were chosen around 6 study stations. Each of these points were sampled once per season over one year. Concentrations in water were under limit of detection. The 900 analysis showed that concentrations were greater in the bryophytes than in the sediments. The greatest environmental concentrations were 120 ppb, 2000 ppb, 1500 ppb for oxolinic acid flumequine and oxytetracycline respectively. Multivariate statistical analysis were performed on the data. This study showed a real contamination of the environment by flumequine and oxytetracycline, and to a lesser extent by oxolinic acid. No seasonal difference in concentrations was noticed. The analysis of the results showed the relevance of the use of bryophytes instead of sediments in the freshwater environmental monitoring. The fine study of the results seemed to reveal a real impact of the study stations on the environment. These observations should be confirmed by more specific studies, by using moss bags for example.
Ref: Environmental Spatio-temporal monitoring of the contamination of a coast river in oxolinic acid, flumequine and oxytetracycline, by Raphael Delepee, Herve Pouliquen, Herve Le Bris. Unite mixte de recherche INTRA/ENVN 1035 Chimiotherapie Aquacole et Environment, Ecole Nationale Veterinaire de Nantes Atlanpole - Le Chantrerie - BP 40706 Nantes Cedex 03, France Abstract (Poster 7) from: Aquaculture and Environment Symposium, September 18, 2002. 7th Bordeaux Aquaculture. September 18 - 20, 2002. Bordeau.

Definition for bryophyte:
-- Any primitive plant in the division Bryophyta, includes liverworts, mosses, and hornworts.
-- Plants in which the gametophyte generation is the larger, persistent phase; they generally lack conducting tissues. Bryophytes include the Hepaticophyta (liverworts), Anthocerotophyta (hornworts), and Bryophyta (mosses). Ref: UCMP Glossary: Botany
-- any plant of the phylum Bryophyta, having stems and leaves but lacking true vascular tissue and roots and reproducing by spores: includes the mosses and liverworts. [ETYMOLOGY: 19th Century: New Latin, from Greek bruon moss + -phyte] bryophytic adjective. Ref: WordReference.com

Flumethrin - Acaricide - CAS No. 69770-45-2

12.Ecological Information: Active ingredient Daphnia toxicity Daphnia magna Strauss: 0.2 mg/l.
Ref: Material Safety Data Sheet by Bayer Animal Health (Pty) Ltd, for Bayticol EC 6% G/V

http://www.fluorideaction.org/pesticides/flumethrin.bayticol.msds.99.htm

Flumetralin - Plant Growth Regulator, Herbicide - CAS No. 62924-70-3

Rationale for US EPA to add Flumetralin to the Toxic Release Inventory : Aquatic acute toxicity values for flumetralin include a daphnid 48-hour EC 50 of greater than 2.8 ppb, a bluegill sunfish 96-hour LC 50 of greater than 3.2 ppb, and a rainbow trout 96-hour LC 50 of greater than 3.2 ppb.
EPA believes that there is sufficient evidence for listing flumetralin on EPCRA section 313 pursuant to EPCRA
section 313(d)(2)(C) based on the available environmental toxicity data for this chemical.
Ref: USEPA/OPP. Support Document for the Addition of Chemicals from Federal Insecticide, Fungicide, Rodenticide Act (FIFRA) Active Ingredients to EPCRA Section 313. U. S. Environmental Protection Agency, Washington, DC (1993). As cited by US EPA in: Federal Register: January 12, 1994. Part IV. 40 CFR Part 372. Addition of Certain Chemicals; Toxic Chemical Release Reporting; Community Right-to-Know; Proposed Rule.

Flumetralin. Ref: Acute Aquatic Ecotoxicity Summaries for Flumetralin on All Taxa Groups. PAN Pesticides Database - Chemical Toxicity Studies on Aquatic Organisms.
http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC35963
Fish
Bluegill Lepomis macrochirus 14.7 8.39 Very Highly Toxic
Rainbow trout, donaldson trout Oncorhynchus mykiss 13.6 10.4 Very Highly Toxic
Zooplankton
Opossum shrimp Americamysis bahia 94.0 - Very Highly Toxic

Flumetsulam - Herbicide - CAS No. 98967-40-9

Abstract: ... To obtain information on the occurrence of SU, SA, and IMI herbicides in the Midwestern United States, 212 water samples were collected from 75 surface-water and 25 ground-water sites in 1998. These samples were analyzed for 16 SU, SA and IMI herbicides by USGS Methods Research and Development Program staff using high-performance liquid chromatography/mass spectrometry. Samples were also analyzed for 47 pesticides or pesticide degradation products. At least one of the 16 SUs, SAs or IMIs was detected above the method reporting limit (MRL) of 0.01 microg/l in 83% of 130 stream samples. Imazethapyr was detected most frequently (71% of samples) followed by flumetsulam (63% of samples) and nicosulfuron (52% of samples)...
Ref: Battaglin WA et al (2000). Occurrence of sulfonylurea, sulfonamide, imidazolinone, and other herbicides in rivers, reservoirs and ground water in the Midwestern United States, 1998. Sci Total Environ. Apr 5;248(2-3):123-33.
http://www.fluorideaction.org/pesticides/flumetsulam.abstracts.htm

Ref: Flumetsulam. Data from Pesticide Action Network
http://www.pesticideinfo.org/PCW/List_AquireAcuteSum.jsp?CAS_No=98967-40-9&Rec_Id=PC35035
Common Name Scientific Name Avg Species LC50 (ug/L) Number of Studies Avg Species Rating
Fish
Bluegill Lepomis macrochirus 300.0 1 Highly Toxic
Atlantic silverside Menidia menidia 380.0 1 Highly Toxic
Rainbow trout, donaldson trout Oncorhynchus mykiss 300.0 1 Highly Toxic
Fathead minnow Pimephales promelas 293.0 1 Highly Toxic
Zooplankton
Marsh grass shrimp Palaemonetes vulgaris 349.0 1 Highly Toxic

Flumiclorac-pentyl - Herbicide - CAS No. 87546-18-7

Phototoxic Pesticide. Light-dependent peroxidizing herbicides (LDPHs). US EPA identified the herbicides Acifluorfen, Azafenidin, Carfentrazone-ethyl, Flumiclorac-penty, Flumioxazin, Fluthiacet-methyl, Fomesafen, Lactofen, Oxadiargyl, Oxadiazon, Oxyfluorfen, Sulfentrazone, Thidiazimin as phototoxic pesticides that act by inhibiting protoporphyringen oxidase in the heme and chlorophyll biosynthetic pathway. [10 out of the 13 pesticides that EPA identified are fluorinated pesticides].
SEE http://www.fluoridealert.org/pesticides/PHOTOTOXICITY.PAGE.htm
Ref: December 11, 2001 - US EPA. Revised Environmental Fate and Effects Division Preliminary Risk Assessment for the Oxyfluorfen Reregistration Eligibility Decision Document (also at: http://www.epa.gov/oppsrrd1/reregistration/oxyfluorfen/oxyefedchap.pdf ).

Ref: Acute Aquatic Ecotoxicity Summaries for Flumiclorac-pentyl on All Taxa Groups. PAN Pesticides Database - Chemical Toxicity Studies on Aquatic Organisms.
http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC35968
Fish    
Sheepshead minnow Cyprinodon variegatus Slightly Toxic
Rainbow trout, donaldson trout Oncorhynchus mykiss Moderately Toxic
Zooplankton    
Opossum shrimp Americamysis bahia Highly Toxic


Flumioxazin - Herbicide - CAS No. 103361-09-7

Phototoxic Pesticide. Light-dependent peroxidizing herbicides (LDPHs). US EPA identified the herbicides Acifluorfen, Azafenidin, Carfentrazone-ethyl, Flumiclorac-penty, Flumioxazin, Fluthiacet-methyl, Fomesafen, Lactofen, Oxadiargyl, Oxadiazon, Oxyfluorfen, Sulfentrazone, Thidiazimin as phototoxic pesticides that act by inhibiting protoporphyringen oxidase in the heme and chlorophyll biosynthetic pathway. [10 out of the 13 pesticides that EPA identified are fluorinated pesticides].
SEE http://www.fluoridealert.org/pesticides/PHOTOTOXICITY.PAGE.htm
Ref: December 11, 2001 - US EPA. Revised Environmental Fate and Effects Division Preliminary Risk Assessment for the Oxyfluorfen Reregistration Eligibility Decision Document (also at: http://www.epa.gov/oppsrrd1/reregistration/oxyfluorfen/oxyefedchap.pdf ).

-- Plants. Flumioxazin is highly toxic to terrestrial plants. Seedling emergence studies identified the most sensitive species to flumioxazin being lettuce (EC25 = 0.0008 pounds active ingredient/acre). Vegetative vigor studies with flumioxazin identified the cucumber as the most sensitive species (EC25 = 0.00008 pounds active ingredient/acre).
-- Environmental Hazards. This product is toxic to aquatic invertebrates.
-- Mechanism of Pesticidal Action. Flumioxazin is a light-dependent peroxidizing herbicide (LDPH) which acts by blocking heme and chlorophyll biosynthesis resulting in an endogenous accumulation of photo-toxic porphyrins. This class of herbicides are known to have a photo-toxic mode of action in plants and possibly in fish. Standard toxicity testing may not include light with the same wavelength or intensity as natural sunlight. LDPHs may be more toxic when exposed to natural sunlight, such as exposure conditions in the field.
Ref: US EPA Pesticide Fact Sheet. April 12, 2001.

http://www.epa.gov/opprd001/factsheets/flumioxazin.pdf

Fluometuron - Herbicide - CAS No. 2164-17-2

• D. Environmental Fate and Drinking Water Exposure and Risk Assessment
Fluometuron and its metabolites are mobile and persistent in the environment. The primary route of degradation of fluometuron and its main degradate CGA-41686 [1-methyl-3-(a,a,a-trifluoro-m-tolyl)urea] is microbial metabolism. However, since fluometuron and its degradates are not volatile, and these degradative processes are not rapid enough, these compounds will be available for leaching to ground water and runoff to surface water in many use conditions. Once in ground water or surface water, fluometuron is expected to persist due to its stability to hydrolysis and photolysis. (page 39)
• The significant cancer risk contributors have been identified as drinking water (direct and indirect, all sources), and several rotational crops with wheat (flour), soybean (oil), and rice (white) having the highest contributions. (page 7)
Ref. February 1, 2005. US EPA: Fluometuron: Revised HED Risk Assessment for Phase III of the Reregistration Eligibility Decision. Docket Identification Number: OPP-2004-0372-0008. 
http://www.fluorideaction.org/pesticides/fluometuron.opp-2004-0372-0008.pdf

Fluometuron is an urea herbicide used for annual grass and annual broadleaf weed control in cotton. Its use on cotton poses risks on an acute basis to both endangered and non-endangered freshwater fish, invertebrates, birds, mammals, and aquatic plants. The Agency [US EPA] was unable to assess the potential chronic risk to birds, and freshwater or estuarine/marine fish and invertebrates due to insufficient data. (page 1)
Major Conclusions
Risks to Terrestrial Organisms
• There are acute risks to avian species that feed on short grass, long grass, and broadleaf plants/small insects. C Chronic risk to birds could not be evaluated due to absence of chronic avian testing.
• There are acute risks to mammals (15 g and 35 g) that forage on short grass, long grass, and broadleaf plants/small insects. There is acute risk to large mammals (1000 g) that feed on short grass.
• There is chronic risk to mammals that forage on short grass, long grass, broadleaf plants/small insects, and fruits/pods/large insects/seeds.
Risk to terrestrial plants on land and in semi-aquatic areas is expected.
Risks to Aquatic Organisms
• The present assessment suggests potential risk on an acute basis to freshwater fish and invertebrates. These estimates were based on Mississippi (MS), Texas (TX) and North Carolina (NC) cotton scenarios (endangered and non-endangered species’ LOCs exceeded). For the California cotton scenario, only endangered species’ LOCs are exceeded for freshwater fish and invertebrates.
• Although estuarine/marine invertebrates endangered species’ LOCs are exceeded, there are currently no federally listed threatened or endangered estuarine/marine invertebrates.
• The Agency was unable to assess the potential chronic risk to freshwater and estuarine/marine fish or freshwater and estuarine/marine invertebrates due to data gaps.
• Risk to aquatic plants is expected for both non-endangered and endangered species.

D. Key Uncertainties and Information Gaps
The following uncertainties and information gaps were identified as part of the problem formulation:
Chronic data for birds were not submitted by the registrant; therefore, measurement endpoints could not be estimated.
Chronic data for freshwater fish were not submitted by the registrant; therefore, measurement endpoints could not be estimated.
Chronic data for freshwater invertebrates were not submitted by the registrant; therefore, measurement endpoints could not be estimated.
Chronic data for estuarine/marine fish were not submitted by the registrant; therefore, measurement endpoints could not be estimated .
Chronic data for estuarine/marine invertebrates and mollusks were not submitted by the registrant; therefore, measurement endpoints could not be estimated.
• Inhalation and dermal pathways for terrestrial mammals and birds were not evaluated because these routes of exposure are considered to be negligible compared to the dietary ingestion pathways. Uncertainties associated with exposure pathways for terrestrial animals are discussed in greater detail in Section IV.D.3.
• Risks to semiaquatic wildlife via consumption of pesticide-contaminated fish were not evaluated. However, given that bioaccumulation of fluometuron is low, ingestion of fish by piscivorus wildlife is not likely to be of concern.
Risks to top-level carnivores were not evaluated due to a lack of data for these receptors. Ingestion of grass, plants, fruits, insects, and seeds by terrestrial wildlife was considered; however, consumption of small mammals and birds by carnivores was not evaluated. In addition, food chain exposures for aquatic receptors (i.e., fish consumption of aquatic invertebrates and/or aquatic plants) were also not considered.
Surrogates were used to predict potential risks for species with no data (i.e., reptiles and amphibians). It was assumed that use of surrogate effects data is sufficiently conservative to apply the broad range of species within taxonomic groups. If other species are more or less sensitive to fluometuron than the surrogates, risks may be under or overestimated, respectively.

The preliminary risk assessment for endangered species indicates that fluometuron exceeds the endangered species LOCs [Level of Concern] for the following combinations of analyzed uses and species: (page 39)
• Freshwater fish (acute): Cotton (all scenarios modeled - MS, NC, TX, and CA).
• Freshwater invertebrates (acute): Cotton (all scenarios modeled - MS, NC, TX, and CA).
• Estuarine/marine invertebrates (acute): Cotton (scenarios modeled - MS, NC, and TX). CA cotton scenario does not exceed endangered species’ LOCs.
• Aquatic vascular plants (acute): Cotton (MS, TX, and NC scenarios).
• Aquatic non-vascular plants (acute): Cotton (MS, TX, and NC scenarios).
• Birds (acute) : Cotton (short grass, tall grass, and broadleaf plants/small insects).
• Mammals (acute) : Cotton (short grass, tall grass, broadleaf plants/small insects) for small (15 g) and medium (35 g) mammal and cotton (short grass) for large mammals (1000 g).
• Mammals (chronic) : Cotton ( short grass, tall grass, broadleaf plants/small insects, and fruits/pods/large insects/seeds).
• Non-target terrestrial and semi-aquatic plants (acute): Cotton (dry areas, wetland areas, and drift).
Ref. February 1, 2005. US EPA: Fluometuron: Revised HED Risk Assessment for Phase III of the Reregistration Eligibility Decision. Docket Identification Number: OPP-2004-0372-0008. 
http://www.fluorideaction.org/pesticides/fluometuron.opp-2004-0372-0008.pdf

-- /ACUTE SYMPTOMS IN MALLARDS AFTER ORAL ADMIN ARE/ ATAXIA, WING DROP OR WINGS CROSSED HIGH OVER BACK, TAIL POINTED UPWARD, FLUFFED FEATHERS, HYPEREXCITABILITY, PHONATION, FALLING. SIGNS APPEARED 15 MIN AFTER-TREATMENT & PERSISTED FOR UP TO ONE WK. [U.S. Department of the Interior, Fish and Wildlife Service. Handbook of Toxicity of Pesticides to Wildlife. Resource Publication 153. Washington, DC: U.S. Government Printing Office, 1984. 44]
-- Environmental Fate: TERRESTRIAL FATE: IT IS OF INTERMEDIATE PERSISTENCE WITH A HALF-LIFE OF 60-75 DAYS ACCORDING TO SOIL CONDITIONS. [Worthing, C.R. and S.B. Walker (eds.). The Pesticide Manual - A World Compendium. 8th ed. Thornton Heath, UK: The British Crop Protection Council, 1987. 412]
-- Environmental Bioconcentration: An estimated BCF of 15 was calculated for fluometuron(SRC), using a log Kow of 2.42 (1) and a regression-derived equation(2). According to a classification scheme(3), this BCF suggests the potential for bioconcentration in aquatic organisms is low. However, in a study of unicellular green algae (Chlorella fusca), a log BCF of 1.96(4) was determined for fluometuron, corresponding to a BCF of 91.2 and indicating a moderate potential for bioconcentration in algae. [(1) Hansch C et al; Exploring QSAR. Hydrophobic, Electronic, and Steric Constants. ACS Prof Ref Book. Heller SR, consult. ed., Washington, DC: Amer Chem Soc p. 70 (1995) (2) Meylan WM et al; Environ Toxicol Chem 18: 664-72 (1999) (3) Franke C et al; Chemosphere 29: 1501-14 (1994) (4) Manthey M et al; pp. 453-459 in The Sci of the Total Environ, Supp. Amsterdam, The Netherlands: Elsevier (1993)]
-- GROUNDWATER: Based on the records maintained in the STORET database of EPA, fluometuron was not detected in any of the 156 groundwater samples analyzed from 125 locations in the U.S.(1). Fluometuron was not detected (detection limit 0.5 ug/l) in water from 119 wells, springs and municipal drinking water supplies sampled throughout Arkansas, during 1985-1987(2). In a study of groundwater sampled in 1992-1998 from 231 wells in 14 counties in the Arkansas Delta, fluometuron was detected at high and persistent concentrations in two of the wells, at 0.4-0.9 ug/l in a well used for a machine shop and at 19-24 ug/l in a well designated for domestic use(3). [(1) USEPA; Drinking Water Health Advisory: Pesticides, Chelsea, MI: Lewis Publishers, Inc. p. 427-41 (1989) (2) Cavalier TC et al; Ground Water Monit Rev 9: 159-66 (1989) (3) Nichols T et al; Water Res Engr 98: 1242-1247 (1998)]
-- SURFACE WATER: Based on the records maintained in the STORET database of EPA, fluometuron was not detected in 14 surface water samples from 14 locations in the US(1). In a study of the Mississippi River and its tributaries in July/Aug 1991, fluometuron was detected in three tributaries and at three Mississippi River sites at concns of 9-411 ng/l(2). [(1) USEPA; Drinking Water Health Advisory: Pesticides. Chelsea, MI: Lewis Publishers, Inc. p. 427-41 (1989) (2) Pereira WE, Hostettler FD; Environ Sci Tech 27: 1542-1552 (1993)]
Ref: Hazardous Substance Data Bank for Fluometuron. Available at Toxnet

Abstract: Existing drinking water wells are widely used for the collection of ground water samples to evaluate chemical contamination. A well comparison study was conducted to compare pesticide and nitrate-N data from specially designed stainless steel research monitoring wells with data from nearby existing on-farm drinking water wells. Results could help to determine whether adequate information concerning ground water contamination can be obtained from existing drinking water wells for use in making pollutant control decisions. The study was conducted during 1993-1994 in the Little Coharie Watershed, a 158 square mile area located in the coastal plain of eastern North Carolina. Statistical analysis indicated that research monitoring wells provided a greater probability of detecting pesticides in ground water than existing on-farm wells. Atrazine was the most frequently detected pesticide found in all wells, followed in order by fluometuron, carbofuran, metolachlor, alachlor, carbaryl, butylate, chlorothalonil, linuron and simazine. Ninety-seven percent of all wells had observed concentrations of nitrate-N, ranging from 0.1 to 30.1 mg/L. There was not a significant difference between research wells and existing wells for monitoring nitrate-N. Based on results of this study, existing drinking water wells can be used for monitoring nitrate; however, specialized stainless steel monitoring wells should be used for monitoring pesticides in ground water.
Ref: Smith CN el at. (1999). A field study to compare performance of stainless steel research monitoring wells with existing on-farm drinking water wells in measuring pesticide and nitrate concentrations. Chemosphere. Feb;38(4):875-89.
http://www.fluorideaction.org/pesticides/fluometuron.pubmed.htm

Fluorapatite - US EPA Inert - CAS No. 1306-05-4

Note from EC: The fluoride concentration in the Nauru phosphate deposits has been estimated at 3.0%.

Nauru - this map and description is from "CIA - The World Factbook" website for Nauru.

Background: Nauru's phosphate deposits began to be mined early in the 20th century... Nauru is the world's smallest independent republic.
Location: Oceania, island in the South Pacific Ocean, south of the Marshall Islands
Area - comparative: about 0.1 times the size of Washington, DC

Environment - current issues: ... intensive phosphate mining during the past 90 years - mainly by a UK, Australia, and NZ consortium - has left the central 90% of Nauru a wasteland and threatens limited remaining land resources
Economy - overview: Revenues of this tiny island have traditionally come from exports of phosphates, but reserves are now depleted... The rehabilitation of mined land and the replacement of income from phosphates are serious long-term problems...

Abstract: In order to evaluate the magnitude and effect of phosphate (fluorapatite) rock particles on the distribution of fluoride in the Jordanian sector of the Gulf of Aqaba, sea water and sediment samples were collected from six stations north and south of Aqaba Port. The fluoride concentrations of the water and sediments were determined, together with the concentrations of calcium, calcium carbonate, total phosphorus, magnesium and organic matter in the sediments. Normal fluoride concentrations were found in the sea water samples, whereas abnormally high values were found in the phosphate-polluted sediments. These findings and the correlations between fluoride concentrations and those of other measured parameters are discussed.
CAS Registry Numbers:
16984-48-8 - Fluoride
14265-44-2 - Phosphate
7723-14-0 - Phosphorus
7440-70-2 - Calcium
7439-95-4 - Magnesium
1306-05-4 - Fluorapatite
471-34-1 - Calcium carbonate
Ref: Fluoride distribution in the Jordan Gulf of Aqaba (Red Sea). by ABU-HILAL AH. SCI TOTAL ENVIRON; 49 (0). 1986. 227-234.

Abstract: Literature on source of environmental pollution with F and its compounds is reviewed. Studies are cited on the accumulation of F in the soil and in plants (carrots, beets, cabbage, cucumbers, potatoes, grains, e.g. wheat and corn, fruit trees, e.g. apricots, plums, peaches and apples, pines, grasses, tea, camellias, gladioli); this leads to F accumulation in livestock (cows and pigs) fed with fodder yeast or other feed containing high F levels. Problems of endemic fluorosis and osteosclerosis in humans living in certain areas are mentioned and the negative effects of occupational exposure to F compounds on various organs and systems of the human body. A mutagenic action in rats was also indicated. In addition to increasing efforts at environmental protection and improving working conditions in industries involving F or its compounds, serious consideration should be given to lowering quantities of F in the drinking water.
CAS Registry Numbers:
16984-48-8 - Fluoride (F)
15096-52-3 - Cryolite ( Al-F6.3Na)
14542-23-5 - Fluorite (CaF2)
1318-94-1 - Muscovite ( Al.H4-O4-Si.1/3K)
1306-05-4 - Fluorapatite (Ca10-F2-O4-P and Ca5-F-O12-P3)
1302-27-8 - Biotite ( Al.F.Fe.H-O.K.Mg.O3-Si.O)
Ref: Ecological problems of the production and use of fluorine compounds. by RODIN VI. ZH VSES KHIM O-VA IM D I MENDELEEVA; 24 (1). 1979. 42-48.

Abstract: Several naturally occurring Ca-phosphate apatites which varied in crystalline structure and ionic composition were added as crystals of different particle size to P-free (< 1 mug/l total P) nutrient media. Sufficient %W%000006%% was released by the partial dissolution of apatite crystals at limnetic pH levels (pH 7.8) to support growth of several unialgal-mixed bacterial culture. The biomass produced by mixed populations increased as the amount of available apatite was increased and as the pH of the media and the particle size of the apatite crystals were decreased. Although apatite characteristically displays reduced solubility under alkaline conditions, the tons of apatite which are continuously entering aquatic environments as erosion material may be contributing to the P loading of those ecosystems. (The following algae were examined: Ankistrodesmus braunii, A. falcatus, Chlorella vulgaris, C. pyrenoidosa, Scenedesmus quadricauda, S. longus, Microcystis aeruginosa, Chlamydomonas dysosmos, C. reinhardtii, Cryptomonas sp., Ochromonas sp., Golenkinia minutissima, Closterium sp. and Staurastrum sp.)
CAS Registry Numbers:
1306-05-4 - Fluorapatite

Ref: Naturally occurring apatite as a source of orthophosphate for growth of bacteria and algae. SMITH EA, MAYFIELD CI, WONG P TS. MICROB ECOL; 4 (2). 1978 105-118.

Fluoroacetamide - Insecticide, Rodenticide - CAS No. 640-19-7
(also known as Fluoroacetamide or Compound 1081)

-- RESULTS OF LAB INVESTIGATIONS ARE REPORTED IN MASS POISONING IN WHICH ABOUT 800 DOGS DIED SHORTLY AFTER CONSUMING PURCHASED POULTRY MEAT. THE TOXICOLOGICAL & PUBLIC HEALTH IMPLICATIONS OF MASS POISONING ARE DISCUSSED.
Ref: [EGYED MN; FLUORIDE 12 (2): 76 (1979)]

-- Abstract: An account is presented of poisoning in a dairy herd grazing fields adjacent to a chemical factory which manufactured fluoroacetamide. In mid-May, three cows of a dairy herd of 26 Friesians died suddenly. In spite of the fact that a ditch and ponds running through the field were fenced off so that the cows could not drink from them, several more cows died at intervals. Clinical signs observed before death were listlessness, intermittent inappetence, incoordination and accelerated heart and respiratory rates. No nervous signs and convulsions were observed. Submaxillary edema and edema of the brisket occurred in a notable proportion of the herd. Surviving cows were lethargic, appetite remained poor and milk yield fell considerably. Several calves died at or shortly after birth. Postmortem examination did not give any indication of the nature of the poison. A neighboring farm reported infertility of their cows and at another adjoining farm several apparently healthy sheep died suddenly. An investigation of the environs together with the clinical condition of the cows provided circumstantial evidence that the cows had been poisoned by water contaminated by a toxic organic fluorine compound present in the factory effluent and draining into ditches and ponds situated on the adjoining farms. Five months after the cows were removed from access to the ditch and pond water. the survivors were still unthrifty and lethargic. The production and agricultural uses of fluoroacetamide and fluoroactate are discussed. Early in 1964, the Ministry of Agriculture, Fisheries and Food recommended that fluoroacetamide should not be used as an insecticide in agriuclture, home gardens or in food storage practice in Great Britain; proprietary products containing fluoroacetamide were subsequently withdrawn from the market.
Ref: Fluoroacetamide poisoning. I. Toxicity in dairy cattle: Clinical history and preliminary investigations.
Authors: Allcroft JSL RJones. Source: Vet. REcord; 84(16), 399-402, 1969.
[also noted: Epidemiology and Treatment 69/10/00, 346 1969]

Fluorodifen - Herbicide - CAS No. 15457-05-3

Fluorodifen. Acute Aquatic Ecotoxicity Summaries for Fluorodifen on All Taxa Groups. Ref: PAN Pesticides Database - Chemical Toxicity Studies on Aquatic Organisms. http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?CAS_No=15457-05-3&Rec_Id=PC86
Common Name Scientific Name Avg Species LC50 (ug/L) LC50 Std Dev Number of Studies Avg Species Rating
Fish
Channel catfish Ictalurus punctatus
335.0
65.0
2
Highly Toxic
Rainbow trout,
donaldson trout
Oncorhynchus mykiss
645.5
91.5
4
Highly Toxic

Fluoxastrobin - Fungicide - CAS No. 193740-76-0

Soil: Depending on the soil, fluoxastrobin was shown to be highly persistent in soil and hence it was present in rotational crops at plant back intervals up to 328 days as the major residue. Decline of fluoxastrobin residues under processing conditions does not occur (page 2)... Persistence of fluoxastrobin in soil may be very variable. Fluoxastrobin may behave as a moderate to high persistent compound. Metabolite M48-E is moderate to medium persistent in soil. Anaerobic metabolite M40 is moderately persistent in soil under aerobic conditions (page 3).
A high risk is identified to aquatic organisms. A bufferzone of 15 metres is needed to respect the Annex VI trigger value for the long term risk for the use of fluoxastrobin as a spray application in cereals (page 5). A high risk to aquatic organisms is identified which requires consideration of appropriate risk mitigation measures. A bufferzone of 15 metres is needed to respect the Annex VI trigger value for the long term risk (page 41).
Ref: Conclusion regarding the peer review of the pesticide risk assessment of the active substance fluoxastrobin finalised: August 10, 2005. European Food Safety Authority.
http://www.fluorideaction.org/pesticides/fluoxastrobin.eu.review.2005.pdf

Aquatic Animals. Toxicity: On an acute basis, Fluoxastrobin is moderately toxic to estuarine/marine fish; highly toxic to freshwater fish and invertebrates; and very highly toxic to estuarine/marine invertebrates. Chronic LOCs are also exceeded for estuarine/marine invertebrates and mollusks. Chronic effects for estuarine/marine invertebrates include reduced survival and reductions in wet weight of surviving adults following a 28-day exposure duration. No data were available to assess the chronic toxicity of fluoxastrobin to estuarine/marine mollusks. Therefore, the NOAEC value was estimated based on the acute-to-chronic ratio for mysid shrimp. .. The ecological risks to fish and invertebrates are considered conservative estimates because they are based on worst case exposure and use scenarios. Nonetheless, because of the potential for exposure and possible adverse effects of fluoxastrobin to endangered and nonendangered fish and invertebrates, the registrant is required to provide information on the proximity of Federally listed freshwater fish and invertebrates to the fluoxastrobin use sites...

Risk to Endangered Species The preliminary risk assessment for endangered species indicates that fluoxastrobin exceeds the endangered species LOCs for the following combinations of analyzed uses and species:

• Use of fluoxastrobin on the following crop scenarios indicate an exceedance of the endangered species LOC for freshwater fish: Maine potatoes (ground and aerial application), Florida tomatoes, peanuts, and turf (at the maximum application rate of 4 times per year).

• Use of fluoxastrobin on Idaho potatoes (aerial application only), Maine potatoes (ground and aerial application), tomatoes, peppers, cabbage, peanuts, and turf (at maximum [4x/year] and reduced [2x/year] application rates) indicate endangered LOC exceedances for endangered freshwater invertebrates.

• Use of fluoxastrobin on Idaho and Maine potatoes (aerial and ground application), tomatoes, peppers, cabbage, peanuts, and turf (at maximum [4x/year] and reduced [2x/year] application rates) indicate endangered acute and chronic LOC exceedances for estuarine/marine invertebrates.

• Use of fluoxastrobin on Maine potatoes (ground and aerial application), Florida tomatoes, peppers, cabbage, peanuts, and turf in Florida (at maximum [4x/year] application rates only) and Pennsylvania (for applications of both 4 and 2x/year) indicate chronic LOC exceedances for estuarine/marine mollusks.

The list of endangered/threatened freshwater fish species where potatoes, tomatoes, peppers, and peanuts are grown is comprised of 84 different species representing 36 States. The three States with the largest number of endangered/threatened freshwater fish species include California, Washington, and Oregon. Within these States, the majority of endangered/threatened fish species are salmon and steel head (Orcorhynchus sp.). The predominant endangered fish species in Florida and North Carolina, where tomatoes, peppers, and peanuts are grown, is the sturgeon (Acipenser sp.).

The list is of freshwater invertebrates is primarily comprised of bivalves (70% of all listed invertebrates; present in 20 States), crustaceans (i.e., amphipods, crayfish, and shrimp) (~19 of all listed invertebrates; present in 6 States), and snails (~11% of all listed invertebrates; present in 2 States). While the majority of listed freshwater invertebrates are bivalves, the amphipod (Gammarus acherondytes) was listed as endangered in Illinois. The identification of an endangered amphipod is a factor because this species was identified as the most sensitive freshwater invertebrate from the available effects data. It appears, however, that the endangered amphipods in Illinois are present only in caves, where pesticides are not likely to be present in water at concentrations that would cause adverse effects.

The Agency’s levels of concern for endangered and threatened freshwater fish and invertebrates and estuarine/marine invertebrates and mollusks are exceeded for the use of fluoxastrobin. However, the Agency recognizes that there are no Federally listed estuarine/marine invertebrates/mollusks.

The registrant must provide information on the proximity of Federally listed freshwater fish and invertebrates to the fluoxastrobin use sites. This requirement may be satisfied in one of three ways:

1) having membership in the FIFRA Endangered Species Task Force (Pesticide Registration [PR] Notice 2000-2);

2) citing FIFRA Endangered Species Task Force data; or

3) independently producing these data, provided the information is of sufficient quality to meet FIFRA requirements.

The information will be used by the OPP Endangered Species Protection Program to develop recommendations to avoid adverse effects to listed species. The registrant has satisfied this requirement using option #1 above.
Reference:
November 2005 - US EPA Pesticide Fact Sheet: Fluoxastrobin.
http://www.fluorideaction.org/pesticides/fluoxastrobin.epa.fact.sheet.2005.pdf

Flupyrsulfuron-methyl, sodium salt - Herbicide - CAS No. 144740-54-5

7. Particular conditions to be taken into account on short term basis by Member States in relation to the granting of authorisations of plant protection products containing Flupyrsulfuron-methy. On the basis of the proposed and supported uses, the following particular issues have been identified which require particular and short term (within 12 months at the latest) attention from the Member States, in the framework of authorisations to be granted, varied or withdrawn, as appropriate. Leaching to groundwater: Particular attention should be given to the potential for groundwater contamination, when the active substance is applied in regions with vulnerable soil and/or extreme climatic conditions.
Ref: FINAL European Commission Review report for the active substance flupyrsulfuron-methyl. Finalised in the Standing Committee on Plant Health at its meeting on 27 April 2001 in view of the inclusion of flupyrsulfuron-methyl in Annex I of Directive 91/414/EEC.
http://europa.eu.int/comm/food/fs/ph_ps/pro/eva/newactive/list2_flupyrsulfi_en.pdf

Fluquinconazole - Fungicide - CAS No. 136426-54-5

Environmental / Ecological Effects: Fluquinconazole (page 5)
Fish Toxicity:
LC50 (96 hr) rainbow trout 1.9 mg/L; bluegill sungish 1.34 mg/L; carp 1.9 mg/L
Other:
LC50 (48 hr) Daphnia >5 mg/L. ErC50 (96 hr) algae 0.046 mg/L; EbC50 (96 hr) algae 0.014 mg/L
Ref: September 2003. Material Safety Data Sheet for Vision 250 SC Fungicide. Bayer CropScience (Australia).

Fluridone - Herbicide - CAS No. 59756-60-4

1994 - The toxicity of Diquat, Endothall, and Fluridone to the early life stages of fish; by EA Paul, HA Simonin, J Symula, and RW Bauer.
J. Freshwater Ecology, Vol. 9, Num. 3 - Sept 1994 pp.229-239.

Table 2. LC50s and associated 95% confidence intervals for fluridone.
(NA = not available)

LC50 (mg/L) (95% CI)
Species Age (d) 24 h 48 h 72 h 96 h
Walleye 8-12 3.6 (3.2-4.1) 2.8 (2.4-3.1) 2.3 (2.0-2.6) 1.8 (1.4-2.0)
Smallmouth Bass 4-8 19 (17-21) 11 (9.7-13) 9.5 (8.5-11) 7.6 (6.9-8.7)
Largemouth Bass 10-14 16 (NA) 16 (NA) 14 (13-16) 13 (12-15)
Table 3. NOAECs (No-Observed-Adverse-Effect Concentrations) and LOAECs (Lowest-Observed- Adverse-Effect Concentrations) (mg/L) for fluridone.
-
24 h
48 h
96 h
Species Age (d) NOAEC LOAEC NOAEC LOAEC NOAEC LOAEC
Walleye 8-12 1.2 2.0 1.2 2.0 0.78 1.2
Smallmouth Bass 4-8 8.7 19 6.2 8.7 4.5 6.2
Largemouth Bass 10-14 12 21 12 21 9.6 12

Fluroxypyr - Herbicide - CAS No. 69377-81-7

-- The data available at this time indicate that fluroxypyr is highly phytotoxic.
-- Aquatic - Estuarine/Marine Fluroxypyr is slightly toxic to the silverside (96-hour LC 50 = 40 mg/L). Fluroxypyr acid is highly toxic to the eastern oyster (96-hour LC 50 /EC 50 = 0.068 mg/L); fluroxypyr 1-methylheptyl ester is slightly toxic to the eastern oyster (96-hour LC 50 /EC 50 = 51 mg/L). It is practically non-toxic to the grass shrimp (96-hour LC 50 /EC 50 > 120 mg/L). Fluroxypyr is highly toxic terrestrial plants. Seedling emergence studies identified the most sensitive species to fluroxypyr methylheptyl ester being the cucumber (EC 25 = 0.075 pounds active ingredient/acre). Since fluroxypyr methylheptyl ester may degrade to fluroxypyr acid before reaching non-target plants, seedling emergence studies were performed on fluroxypyr acid and identified cotton as the most sensitive species (EC 25 = 0.025 pounds active ingredient/acre). Vegetative vigor studies with fluroxypyr methlyheptyl ester also identified cotton as the most sensitive species (EC 25 = 0.0012 pounds active ingredient/acre).
Ref: US EPA. Pesticide Fact Sheet. Fluroxypyr. Reason for Issuance: Conditional Registration Date Issued: September 30, 1998.

http://www.epa.gov/opprd001/factsheets/fluroxypyr.pdf

Fluroxypyr 1-methylheptyl ester - Herbicide - CAS No. 81406-37-3

Acute Aquatic Ecotoxicity Summaries for Fluroxypyr 1-methylheptyl ester on All Taxa Groups.
Ref: PAN Pesticides Database - Chemical Toxicity Studies on Aquatic Organisms
http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC37523    
Common Name Scientific Name Avg Species LC50 (ug/L) LC50 Std Dev Number of Studies Avg Species Rating
Crustaceans     
Northern pink shrimp Penaeus duorarum 128.0   1 Highly Toxic
Fish     
Sheepshead minnow Cyprinodon variegatus 87.0 - 1 Very Highly Toxic
Bluegill Lepomis macrochirus 629.5 0.50 2 Highly Toxic 
Atlantic silverside  Menidia menidia 188.0    - Highly Toxic
Pink salmon  Oncorhynchus gorbuscha  10,333  1,700 Slightly Toxic 
Chum salmon  Oncorhynchus keta  14,333  3,682  Slightly Toxic  
Coho salmon,silver salmon  Oncorhynchus kisutch  13,667  2,867  Slightly Toxic  
Rainbow trout,donaldson trout  Oncorhynchus mykiss  15,333  2,357  Slightly Toxic  
Sockeye salmon Oncorhynchus nerka 12,667 2,055 3 Slightly Toxic 
Chinook salmon Oncorhynchus tshawytscha 12,667  2,867 3 Slightly Toxic 
Zooplankton
Daggerblade grass shrimp Palaemonetes pugio 135.0 - 1 Highly Toxic 

Flurprimidol - Plant Growth Regulator - CAS No. 56425-91-3

Potential Ground Water Contaminant
Ref: PAN
http://www.pesticideinfo.org/Detail_ChemReg.jsp?Rec_Id=PC32838

Flusilazole - Fungicide - CAS No. 85509-19-9

-- For flusilazole, no data are available to assess the impact on organic matter decomposition. Except earthworms and soil microflora, no soil-dwelling organisms have been tested. Given the persistence of flusilazole in soil and the environmental and agronomical importance of the organic matter breakdown for soil fertility, the Committee considers a risk assessment based solely on the existing data as not adequate.
-- Although fish early life-stage tests provide useful information on sensitive life stages of fish, for flusilazole in particular the risk assessment has explicitly identified fish and other aquatic species to be at risk from agricultural use of this a.s., and there is evidence that flusilazole may have specific effects on the reproductive process. Therefore the SCP cannot conclude that a NOEC based on a fish early life-stage test for a single species is necessarily adequate in this particular case to ensure sufficient protection of fish populations from adverse effects on reproduction.
-- The monograph (volume 3, pp. 230-233) identified aquatic species, and fish in particular, as possibly at risk from flusilazole. In addition, a dose-dependent decrease in serum estradiol levels by flusilazole, considered to be indicative of aromatase inhibition, was observed in studies with rats (volume 3, p. 73). Aromatase inhibition is significant for reproduction since aromatization of testosterone is the process by which oestrogen is formed in vertebrates (Trant et al. 1997). This reaction is mediated by the cytochrome P450 aromatase. It has been shown that oestrogen (i.e., oestradiol) plays a major role in the reproductive physilogy of all vertebrates, including gamete development and maturation, and induces the hepatic synthesis of the yolk precursor, vitellogenin. Studies in which fish have been exposed to aromatase inhibitors suggest that aromatase activity, specificity or expression levels vary with maturation stage and among species (Bl‡zquez et al. 2001, Zerulla et al. 2002).
-- ... Neither of the above tests was designed to investigate possible effects on reproductive output or mating behaviour of adult fish. Given that there is evidence that flusilazole is an aromatase inhibitor, there are specific concerns that reproduction could be adversely affected by this substance. Therefore potential effects on mating behaviour, time to sexual maturity, reproductive output and timing, fertilisation success, and sex ratio of offspring are also of concern and should be explicitly addressed by a test designed for this purpose.

Ref: July 2002 - Opinion of the Scientific Committee on Plants on specific questions from the Commission concerning the evaluation of flusilazole in the Council Directive 91/414/EEC. European Commission. Health & Consumer Protection Directorate-General.
http://www.fluorideaction.org/pesticides/flusilazole.eu.july.2002.pdf

"Flusilazole 85509-19-9 Withdrawn. Low degradability. 1994."
Definition: "Withdrawn. A substance which the manufacturer has either withdrawn from the market, or for which he has withdrawn his application for registration, approval, or renewed approval and when it is clear that these measures were undertaken due to the health or environmental properties of the substance."
Ref: Euopean Commission. Appendix 5. Substances which may not be included as active ingredients in approved pesticide products, Chapter 15, Section 2, subsection one.
http://www.kemi.se/lagar_eng/pdf/app5_8.pdf

Soil dissipation. The Meeting reviewed the final report of a 3-year soil dissipation study (4 applications per year) for which an interim report was reviewed by the 1989 JMPR. It confirms the 1989 observations that over 92% of the radioactivity is confined to the top 8 cm of soil over the test period, and that the predominant residues in this segment are flusilazole and its silanol metabolite IN-F7321. The author cites statistical evaluation of the data to support the view that residues will reach a steady level at 57% of yearly application levels after repeated application levels under worst-case conditions.
The report cites the steady-state conclusion, the strong adsorption to the top layers of soil, the lack of residues exceeding 0.01 mg/kg in the 24-36 cm soil depths and the weak leaching potential indicated in other studies as evidence that residues in ground water were unlikely. While the data indicate that over 92% of the radioactivity remains in the top 8 cm of the silt loam soil investigated, and indeed that residue levels are extremely low in the 24-36 cm depths, it also shows an increasing penetration by low levels of radioactivity over the test period in this soil type. The identity of these residues in the deeper soil segments was not indicated.
While the adsorption of this persistent pesticide to soil is strong, the 1989 JMPR had noted that uptake of low residue levels can occur in rotational crops and that the leaching potential would be less for silt loams (as in this study) than for more sandy soils. Because the silt loam study was under worst-case conditions (bare ground, repeated applications) and was consistent with reassuring findings of a number of other relevant studies, the Meeting accepted that ground water residues from silt loam soils were unlikely.
Ref:
1993 FAO/WHO JOINT MEETING ON PESTICIDE RESIDUES Geneva, 20-29 September 1993. PESTICIDE RESIDUES IN FOOD. REPORT OF THE 1993 JOINT FAO/WHO MEETING OF EXPERTS. 4.24 FLUSILAZOLE (165). RESIDUE AND ANALYTICAL ASPECTS.

Reproductive process -- Although fish early life-stage tests provide useful information on sensitive life stages of fish, for flusilazole in particular the risk assessment has explicitly identified fish and other aquatic species to be at risk from agricultural use of this a.s., and there is evidence that flusilazole may have specific effects on the reproductive process. Therefore the SCP cannot conclude that a NOEC based on a fish early life-stage test for a single species is necessarily adequate in this particular case to ensure sufficient protection of fish populations from adverse effects on reproduction.
-- The monograph (volume 3, pp. 230-233) identified aquatic species, and fish in particular, as possibly at risk from flusilazole. In addition, a dose-dependent decrease in serum estradiol levels by flusilazole, considered to be indicative of aromatase inhibition, was observed in studies with rats (volume 3, p. 73). Aromatase inhibition is significant for reproduction since aromatization of testosterone is the process by which oestrogen is formed in vertebrates (Trant et al. 1997). This reaction is mediated by the cytochrome P450 aromatase. It has been shown that oestrogen (i.e., oestradiol) plays a major role in the reproductive physilogy of all vertebrates, including gamete development and maturation, and induces the hepatic synthesis of the yolk precursor, vitellogenin. Studies in which fish have been exposed to aromatase inhibitors suggest that aromatase activity, specificity or expression levels vary with maturation stage and among species (Bl‡zquez et al. 2001, Zerulla et al. 2002).
-- ... Neither of the above tests was designed to investigate possible effects on reproductive output or mating behaviour of adult fish. Given that there is evidence that flusilazole is an aromatase inhibitor, there are specific concerns that reproduction could be adversely affected by this substance. Therefore potential effects on mating behaviour, time to sexual maturity, reproductive output and timing, fertilisation success, and sex ratio of offspring are also of concern and should be explicitly addressed by a test designed for this purpose.
Ref: July 2002 - Opinion of the Scientific Committee on Plants on specific questions from the Commission concerning the evaluation of flusilazole in the Council Directive 91/414/EEC. European Commission. Health & Consumer Protection Directorate-General.
http://www.fluorideaction.org/pesticides/flusilazole.eu.july.2002.pdf

Ecotoxicology (page 11)
• Acute toxicity to oysters - shell deposition
• Acute toxicity to mysid shrimp
• Acute toxicity to sheepshead minnow
• Chronic toxicity to mysid shrimp
• Chronic toxicity to sheepshead minnow
•• A waiver will be requested for the cbironomid sediment toxicity test with Chironomus tentans (a Chironomus riparius study will be submitted in support of the waiver) .Algal toxicity (Anabaena, Navicula, Skeletonema)
• Aquatic plant toxicity - Lemna
Ref: DuPont Punch (Active ingredient: Flusilazole) and DuPont Charisma (Active ingredients: Flusilazole and Famoxadone): Summary of data compiled in support of a Section 18 Emergency Exemption request for control of Asian soybean rust on soybeans. By DuPont authors: Cosgrove T, Czochor L, Dinter A, Jemberg K, Klemens A, Marcon A, McInnes B, Mullin L, Russell M, Ryan D, Singles S, Vanderbroeck V. Revision No. 1: February 2, 2005.
http://www.fluorideaction.org/pesticides/flusilazole.appendix1.pdf

Fluthiacet-methyl - Herbicide - CAS No. 117337-19-6

Phototoxic Pesticide. Light-dependent peroxidizing herbicides (LDPHs). US EPA identified the herbicides Acifluorfen, Azafenidin, Carfentrazone-ethyl, Flumiclorac-penty, Flumioxazin, Fluthiacet-methyl, Fomesafen, Lactofen, Oxadiargyl, Oxadiazon, Oxyfluorfen, Sulfentrazone, Thidiazimin as phototoxic pesticides that act by inhibiting protoporphyringen oxidase in the heme and chlorophyll biosynthetic pathway. [10 out of the 13 pesticides that EPA identified are fluorinated pesticides].
SEE http://www.fluoridealert.org/pesticides/PHOTOTOXICITY.PAGE.htm
Ref: December 11, 2001 - US EPA. Revised Environmental Fate and Effects Division Preliminary Risk Assessment for the Oxyfluorfen Reregistration Eligibility Decision Document (also at: http://www.epa.gov/oppsrrd1/reregistration/oxyfluorfen/oxyefedchap.pdf ).

-- Fluthiacet-methyl was shown to be practically non-toxic to birds, practically non-toxic to small mammals, practically non-toxic to bees and other beneficial insects, very highly toxic to fish, and moderately toxic to fresh water invertebrates. For seedling emergence, onion is the most sensitive non-target plant species and for vegetative, vigor, cucumber is the most sensitive non-target plant species. For aquatic plants, duckweed and nonvascular green algae are the most sensitive aquatic plant species. There are no acute or chronic risk to non-target endangered fish, birds, aquatic invertebrates, terrestrial or aquatic plants or endangered species. Risks to endangered terrestrial and aquatic species are expected to be minimal form the use of Action Herbicide on soybeans. Because surfactant is used with the end-use product, and may enhance the productÕs phytotoxicity, limited vegetative vigor test with onion, tomato, cucumber and an aquatic test with duckweed are a condition of the registration for Action Herbicide.
-- The following statement must appear in the Environmental Hazards section of the label of end use products: This pesticide is toxic to fish and aquatic invertebrates. Do not discharge effluent containing this product into lakes, streams, ponds, estuaries, oceans or other waters unless in accordance with the requirements of a National Pollutant Discharge Elimination System (NPDES) permit and the permitting authority has been notified in writing prior to discharge. Do not discharge effluent containing this product to sewer systems without previously notifying the sewage treatment plant authority. For guidance contact your State Water Board or Regional Office of the Environmental Protection Agency.
Ref: US EPA. Pesticide Fact Sheet. Fluthiacet-methyl Reason for Issuance: Conditional Registration Date Issued: April 1999.

http://www.epa.gov/opprd001/factsheets/fluthiacet.pdf

Flutolanil - Fungicide - CAS No. 66332-96-5

Flutolanil is very persistent and moderately mobile
Aqueous Photolysis: Flutolanil degraded slowly, 8% over the 30-day study. No half-life was indicated.
Aerobic Soil Metabolism: Flutolanil had a half-life in sandy loam of 300 days.

Anaerobic Aquatic Metabolism: Flutolanil had a half-life of >13 years.
Ref:
December 19, 2002. New York State Department of Environmental Conservation. Letter - Registration of a Major Label Change - Flutolanil (Moncoat).

http://www.fluoridealert.org/pesticides/Flutolanil.NYDEC.Dec.2002.htm

"Flutolanil 66332-96-5 Banned. Low degradability. 1995."
Definition: "Banned. A substance which for health or environmental reasons by an authority decision is either no longer approved for any area of application, or for which an approval or registration has been denied from the first instance."
Ref: Euopean Commission. Appendix 5. Substances which may not be included as active ingredients in approved pesticide products, Chapter 15, Section 2, subsection one.

http://www.kemi.se/lagar_eng/pdf/app5_8.pdf

Flutriafol - Fungicide - CAS No. 76674-21-0

Recommendations (page 51): [Flutriafol] is extremely persistent in soil and will accumulate following repeated annual applications. Soil residues also demonstrate the potential to be mobile. Although the fate and behaviour of flutriafol in water has not been evaluated and no data are available from natural water monitoring, the high spray application rate and the use on cereals, indicated that water contamination is likely.
Evaluation on: Flutriafol. October 1996. Issue No. 158, UK Department for Environment, Food and Rural Affairs, Pesticides Safety Directorate, Mallard House, Kings Pool, 3 Peasholme Green, York YO1 7PX.
http://www.pesticides.gov.uk/citizen/evaluations/158_confirm-box.htm

The Svalbard archipelago in arctic Norway receives considerable semivolatile organic contaminant (SOC) inputs from the atmosphere... The surface sample also had highest concentrations of pendimethalin (herbicide, 18.6 ng L-1) and flutriafol, the lone observed fungicide (9.6 ng L-1).
Reference: Current-Use and Legacy Pesticide History in the Austfonna Ice Cap, Svalbard, Norway. By Mark H. Hermanson et al. Environ. Sci. Technol., 39 (21), 8163 -8169, 2005. See Abstracts

Fluvalinate - Acaricide, Insecticide - CAS No. 69409-94-5

Aquatic acute toxicity values for fluvalinate include a daphnid 48- hour EC 50 of 0.40 ppb, a bluegill sunfish 96-hour LC50 of 0.9 ppb, a rainbow trout 96-hour LC50 of 2.9 ppb, and a sheepshead minnow 96-hour LC 50 of 10.8 ppb. EPA believes that there is sufficient evidence for listing fluvinate on EPCRA section 313 pursuant to EPCRA section 313(d)(2)(C) based on the available environmental toxicity data for this chemical.
Ref: USEPA/OPP. Support Document for the Addition of Chemicals from Federal Insecticide, Fungicide, Rodenticide Act (FIFRA) Active Ingredients to EPCRA Section 313. U. S. Environmental Protection Agency, Washington, DC (1993). As cited by US EPA in: Federal Register: January 12, 1994. Part IV. 40 CFR Part 372. Addition of Certain Chemicals; Toxic Chemical Release Reporting; Community Right-to-Know; Proposed Rule.

Environmental Bioconcentration: Based upon a water solubility of 0.005 mg/L at 20-25 deg C (taken from the USDA's evaluated database of pesticide properties)(1), the BCF for fluvalinate can be estimated to be 12,000 from a recommended regression-derived equation(2,SRC). This BCF value suggests that bioconcentration may be important in aquatic organisms that cannot metabolize fluvalinate(SRC). [(1) Wauchope RD et al; Rev Environ Contam Toxicol 123: 1-36 (1991) (2) Lyman WJ et al; Handbook of Chemical Property Estimation Methods Washington, DC: Amer Chem Soc p. 5-10 (1990)]
Ref: Hazardous Substances Data Bank for FLUVALINATE CASRN: 69409-94-5.
http://www.fluorideaction.org/pesticides/fluvalinate.toxnet.hsdb.htm

Ref: Acute Aquatic Ecotoxicity Summaries for Fluvalinate (stereochemistry unspecified) on All Taxa Groups. PAN Pesticides Database - Chemical Toxicity Studies on Aquatic Organisms.
http://www.pesticideinfo.org/List_AquireAcuteSum.jsp?Rec_Id=PC34785
Crustaceans
Red swamp crayfish Procambarus clarkii 0.83 0.28 Very Highly Toxic
Fish
Japanese eel Anguilla japonica 5.05 3.75 Very Highly Toxic
Common, mirror, colored, carp Cyprinus carpio 32.6 33.7 Very Highly Toxic
Bluegill Lepomis macrochirus 1.79 0.85 Very Highly Toxic
Rainbow trout, donaldson trout Oncorhynchus mykiss 5.85 2.95 Very Highly Toxic
Zooplankton
Water Flea Scapholeberis kingi 300.0 - Highly Toxic

Fomesafen - Herbicide - CAS No. 72178-02-0

Abstract: ... In mesocosms, multiple application of fomesafen, leading to maximal herbicide concentrations of 60.33 +/- 2.68 microg/L in water, resulted in reduced number of egg masses and altered glycogen metabolism in contaminated snails. These changes, as well as affected steroid-like levels in fomesafen-exposed snails, support the hypothesis of impaired neuroendocrine functions.
Ref:
Environ Toxicol Chem 2002 Sep;21(9):1876-88. Nonylphenol polyethoxylate adjuvant mitigates the reproductive toxicity of fomesafen on the freshwater snail Lymnaea stagnalis in outdoor experimental ponds; by Jumel A, Coutellec MA, Cravedi JP, Lagadic L.

-- iii. Cancer risk. Based on exposure levels for drinking water, as given above, the estimate of cancer risk is 2.7 x 10-6. This figure is an overestimate, as it was arrived at based on several very conservative assumptions. Estimates used were calculated based on data from only one small scale study conducted in NC, for use of fomesafen on soybeans at a vulnerable site. This represents a worst case scenario, so is not representative of the ``average'' conditions of use. Additionally, there is language on the product label warning of the potential of fomesafen to leach to ground water in vulnerable areas. Vulnerable areas in this case refers to areas where soils are permeable (sand and silt loams) and the water table is shallow. The majority of areas of soybean production, and potential use of fomesafen, will not likely be vulnerable sites, thus the data used from the one small scale study greatly overestimates levels which could actually occur. Further, it is assumed that this exaggerated level will occur in all drinking water throughout the US, and that each individual consumes 2 liters of drinking water per day.
Ref: Federal Register. November 19, 1997. Fomesafen; Pesticide Tolerances for Emergency Exemptions. Final Rule.

http://www.fluoridealert.org/pesticides/Fomesafen.FR.Nov.19.1997.htm

Phototoxic Pesticide. Light-dependent peroxidizing herbicides (LDPHs). US EPA identified the herbicides Acifluorfen, Azafenidin, Carfentrazone-ethyl, Flumiclorac-penty, Flumioxazin, Fluthiacet-methyl, Fomesafen, Lactofen, Oxadiargyl, Oxadiazon, Oxyfluorfen, Sulfentrazone, Thidiazimin as phototoxic pesticides that act by inhibiting protoporphyringen oxidase in the heme and chlorophyll biosynthetic pathway. [10 out of the 13 pesticides that EPA identified are fluorinated pesticides].
SEE http://www.fluoridealert.org/pesticides/PHOTOTOXICITY.PAGE.htm
Ref: December 11, 2001 - US EPA. Revised Environmental Fate and Effects Division Preliminary Risk Assessment for the Oxyfluorfen Reregistration Eligibility Decision Document (also at: http://www.epa.gov/oppsrrd1/reregistration/oxyfluorfen/oxyefedchap.pdf ).

 
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