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

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

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

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

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

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.