Test CAS RN Common Structure % CAS Name

15-25

Category Sub-Category Test Test Substance Report Result Summary

Mammalian 

Toxicity

Acute Oral ALD (rats) = > 5000 mg/kg 1988c).

A single dose of suspended in corn oil

was administered by oral gavage to one male rat per dose level. Dose levels

were 450, 670, 1000, 1500, 2300, 3400, 5000, 7500, and 11,000 mg/kg.

Following administration of the test material, rats were observed for clinical

signs of toxicity. Surviving rats were weighed and observed daily until signs of

toxicity subsided, and then at least 3 times per week for 14 days after dosing.

Observations for mortality were made daily throughout the study. 

The lowest dose of test material which resulted in death was 2300 mg/kg.

Deaths occurred up to 5 days after dosing. The animal dosed at 3400 mg

survived. Animals dosed at 5000 mg/kg and greater died. The survival of the

animal dosed at 3400 mg/kg was attributed to animal variability, and did not

change the ALD. The only clinical sign of toxicity observed at nonlethal doses

was yellow-stained perineum in the rat dosed at 3400 mg/kg 4 days after

dosing. Moderate to severe weight losses were observed in all rats up to 4

days after dosing. 

Under conditions of this study, the ALD for

was 2300 mg/kg. This material was considered to be slightly toxic when

administered as a single oral dose to male rats 1988c).

Mammalian 

Toxicity

Acute Dermal was evaluated for skin irritation potential

in New Zealand White rabbits. A 0.5 g aliquot of the test substance,

moistened with dimethyl phthalate, was applied directly to a 2-inch gauze

square that was then placed on the shaved test site. The patch was held in

place with tape. Rubber sheeting was then wrapped around the animal and

secured for an occlusive dressing. The rabbits were exposed to the test

substance for 24 hours after which the test substance was removed by gentle

washing with warm water. The test substance was moistened with dimethyl

phthalate, but did not dissolve. Therefore, some of the compound may have

fallen from the test site during the exposure period. Approximately 24 and 48

hours after application of the test material, the test sites were evaluated for

erythema, edema and other evidence of dermal effects and were scored

according the Draize scale. The adjacent areas of the untreated skin were

used for comparison. 

No erythema or edema was observed in any of the treated rabbits. Under

conditions of this study, was not a skin

irritant ( 1988b).

Test Result Summary

Toxicology Summary

The toxicological information summarized below is NOT on the PMN substance, 

but on a related substance that may be of interest to the Agency. 

Full study reports can be provided upon request.
Mammalian 

Toxicity

Acute Eye was evaluated for acute eye irritation

potential in 2 male New Zealand White rabbits. A 0.01 g aliquot of test

substance was administered to 1 eye of each animal. Both eyes of 1 animal

remained unwashed. Approximately 20 seconds after the test material was

administered, both eyes of the remaining animal were rinsed for 1 minute with

lukewarm tap water. The conjunctiva, iris, and cornea of each eye were

evaluated for evidence of eye irritation approximately 1 and 4 hours and 1, 2

and 3 days following administration of the test substance. At each

observation, the treated eyes were examined using illumination and

magnification and scored according to the Draize scale. The untreated eye of

each animal was also examined and used for comparison. Fluorescein dye

was used to evaluate corneal ulceration at the 1-, 2-, and 3-day observation.

Biomicroscopic examinations for corneal injury were conducted at the 1-, 2-,

and 3-day observation and scored according to a numerical scale.

produced no irritation in either treated

rabbit eye. Fluorescein stain and biomicroscopic examinations were negative

for corneal injury in both treated eyes. Under the condition of this study,

was not an eye irritant ( 1988a).

Ecotoxicology Aquatic Studies Fish 96-hour LC50 (fathead minnow, Pimephales promelas) = > 1000 mg/L

( 1989).

The acute toxicity of to the fathead

minnow, Pimephales promelas was determined in an unaerated, 96-hour,

static test. The study was conducted with 3 concentrations of test material and

a dilution water control at a temperature of 21.7 - 22.6°C. Exposure of fathead

minnows to the dilution water control and nominal test material concentrations

of 360, 600, and 1000 mg/L resulted in no mortalities at the end of 96 hours.

All test solutions (from 360 to 1000 mg/L) were milky with undissolved test

material floating on the surface and settling to the bottom. The solubility of

was less than 360 mg/L, as there was

undissolved test material in all test concentrations.

was found to exhibit no acute toxicity at test concentrations above

its solubility in water ( 1989). 

** Toxicological Studies also available for

1.

2.

3.

4.
CAS RN Common Name Structure % CA Index Name

59587-38-1 Perfluorohexylethylsu

lfonic acid

F(CF2) 6CH2CH2SO3-

K+

100 1-Octanesulfonic acid, 3,3,4,4,5,5,6,6,7,7,8,8,8-tridecafluoro, potassium salt 

(1:1)

Category Sub-Category Test Result Summary

Mammalian Toxicity Acute Oral LD50 (rat; Probit method) = 2000 mg/kg 

LD50 (rat; Arcsinus method) = 2400 mg/kg 

5 male and 5 female rats per group were administered 0.5, 1, 2, or 4 g/kg

of the test substance ( tested in solid form) in olive oil.

They were observed during the first hours after intubation and then for 14

days. Clinical signs of toxicity observed included nasal and/or eye

congestion and polyuria (>500 mg/kg), red-stained fur (>1000 mg/kg),

ptosis (1000 and 2000 mg/kg), apathy (2000 mg/kg), prostration (>2000

mg/kg), difficult locomotion (2000 mg/kg), diarrhea (4000 mg/kg), weight

loss (>2000 mg/kg), moribund (4000 mg/kg), and piloerection (4000

mg/kg) ( 1977a).

Mammalian Toxicity Acute Dermal The test substance ( tested in solid form) was not a skin

irritant in rabbits.

The test substance (0.3 g) was applied to the surface of the scarified or

non scarified skin of 6 male New Zealand white rabbits via gauze

squares. The gauze squares were held in place with an occlusive

adhesive patch. Then tape was wound around the rabbit to complete the

fixing of the patches. The rabbits were then placed in restraining devices

for 24 hours. After 23 hours, the patches were removed, and 1 hour later

the primary irritation index was evaluated. Another reading was made 48

hours later. The primary cutaneous irritation score was 0 (

1977a).

Mammalian Toxicity Acute Eye The test substance ( tested in solid form) was classified

as very irritating to the rabbit eye.

Six male New Zealand white rabbits were tested. The test substance (0.1

g) was introduced into the rabbit’s left eye, and the right eye served as a

control. The eyelid was held closed for several seconds, giving a slight

massage to avoid loss of the substance. The eyes were not washed after

administration. Evaluations were performed at 1 and 24 hours, and at 2,

3, 4, and 7 days after administration. The index of acute ocular irritation

(IOA) was 15.67 and the average index of ocular irritation after 4 days

(IOM) was 3.33. The test substance was classified as very irritating to the

rabbit eye ( 1977a).

The toxicological information summarized below is for PMN Substance #2

Toxicology Summary

(Test Substance)
Mammalian Toxicity Subchronic Oral A biopersistence screening 10-dose oral gavage study in rats with a

recovery period was conducted. Two groups of 5 male rats each were

given 25 mg/kg/day of the test substance ( tested

in solid form) for 10 consecutive days. Approximately two hours after

dosing on test days 1 and 5, blood was collected from the orbital sinus of

each rat from one five-dose group. Approximately 2 hours after the last

dose, these rats were euthanized and blood, livers, and fat were

collected. Blood was collected from the remaining five rats on test days

13, 24, and 52. These rats were euthanized on test day 94, and blood,

livers, and fat were collected. Body weight and clinical signs were

recorded on each dosing day, and then weekly during the recovery

period. On selected days (5, 10, 13, 24, 52, and 94), five rats per group

were euthanized and the blood and livers collected. Body weights and

clinical signs were recorded on each day of dosing and then

approximately every other week during the recovery period. Additionally,

one negative control, deionized water, and two positive controls were

tested. 

No deaths occurred during the study. No compound-related clinical signs

of toxicity were observed in the rats dosed with the test substance. The

mean body weights and mean body weight gains of the test rats were

comparable to the negative controls and equal to or greater than the

positive controls. The mean relative liver weights of rats dosed with the

test substance was 12% higher than the negative control at day 10 and

6% higher at day 94. The mean relative liver weights of rats dosed with

the positive control materials were 38 and 88% higher on test day 10, but

were comparable to control on test day 94. The increased liver weights

appear to be associated with increased liver concentrations of fluorine

equivalents of test or positive control substances, particularly on day 10.

The test substance normalized μm equivalents in rat blood increased

during the dosing period and did not appear to reach steady-state. The

area under the curve 

(estimated to infinity) was calculated and normalized

for fluorine content for the test substance and each positive control and

further normalized to dose. The AUCINF/D for the fluorine component of

the test substance was 17,865 compared to AUCINF/D values of 522,474

and 81,507 for the positive controls. 

The concentrations in fluorine in the livers from rats dosed with the test

substance was 423.64 μM equivalents on day 10. On day 10, the mean

μM equivalent concentrations of fluorine in the fat from rats dosed with

the positive control materials were approximately 24-fold and 7-fold

greater than the fluorine concentration in fat from rats treated with the test

substance. By day 94, excess fluorine was below the limit of

quantification in fat of rats dosed with the test substance or one positive

control. Some retention of fluorine was evident in the fat from rats dosed

with the other positive control material.

The mean μM equivalents of fluorine in the liver from animals dosed with

the test substance were higher than levels in the blood and fat.

Under the conditions of this study, absorption of the test substance by

rats following oral gavage administration was evident based on

quantification of fluorine in the blood, liver, and fat. A very minimal

increase in relative liver weights was observed for the test substance.

Changes in relative liver weights were greater for the positive controls,

and were associated with greater concentrations of fluorine in the liver

particularly at day 10. The tissue concentrations declined after cessation

of dosing with some retention of fluorine in the blood and liver based on

quantification on the end (day 94) of the study. However, fluorine

concentrations and the AUCINF/D were significantly lower than those in

rats dosed with the positive control materials ( 2008a). 
Ecotoxicology Environmental 

Fate

Bioaccumulation/ 

Bioconcentration

An in vitro trout hepatocyte bioaccumulation screen was performed with

the test substance ( tested in solid form). Two

experiments with the test substance and 1 experiment with each control

was performed. Two replicates per experiment for the test, positive

control (4-nonylphenol), and dead cell control were performed. The cell

concentration was 2x106 cells/mL, in a dose vehicle of acetonitrile, at a

pH of 7.8, incubation temperature of 10-12°C, and final concentration of 5

μM (2.33 ppm). The time points examined were 5, 15, 30, 60, 120, and

240 minutes.

No apparent loss of the parent compound was observed within 4 hours of

incubation. These results suggest that the bioaccumulation potential of

this test substance would not be significantly affected by fish metabolism

( 2007i).

Ecotoxicology Environmental 

Fate

Bioaccumulation / 

Bioconcentration

Rainbow trout, Oncorhynchus mykiss, were exposed to

under flow-through conditions for 56 days during the uptake

(exposure) phase of the study followed by a 28-day depuration phase in

clean dilution water. Two nominal aqueous test substance concentrations

(1 and 10 μg/L), a single nominal spiked diet concentration (10 μg/kg),

and a dilution water control were used for testing with 60 fish per

exposure treatment and control. An error in preparation of the aqueous

test concentrations and delay in analytical confirmation of the test

substance concentrations resulted in the day 1-13 uptake phase aqueous

test substance concentrations being below the analytical method limit of

detection of 0.06 μg/L. This error was corrected upon discovery as

reflected in the aqueous test substance concentrations for study days 14

through 56.

The mean, measured concentrations of in the aqueous

test solutions from days14-56 were 1.08 μg/L and 9.32 μg/L and the

measured concentration in the spiked trout chow diet used for

the duration of the dietary uptake phase of the study was 13.1 μg/Kg. One

day after initiation of the depuration phase there were no detectable

levels of present in the aqueous test solution test chambers.

The dilution water control and the control trout chow diet contained no

detectable concentrations of during the study. Fish tissue

residue concentrations of 

reached steady-state equilibrium within 42 days or earlier

in both aqueous and dietary exposures. The k1 values (uptake rate

constant) for days 14-56 of the aqueous exposures in whole fish based

on measured tissue residues were 4.462 and 0.452 per day for the

nominal 1 and 10 μg/L nominal aqueous test concentrations while the day

14-56 depuration rate constants, k2, in whole fish based on measured

tissue residues were 0.125 and 0.177 per day, respectively. After a

maximum of 24 days of depuration, the measured concentrations in the

whole fish were approximately 95% or less of the whole fish tissue

concentrations at the end of the uptake phase. However, measured

concentrations in whole fish at the end of the uptake phase on day 56

were already less than 50% of the maximum uptake phase concentration

in whole fish for both aqueous test concentrations and the dietary

exposure concentration of The steady-state

bioconcentration factors (BCF) for the nominal 1 and 10 μg/L aqueous

test substance concentrations were 22 and 3, respectively. The

respective kinetic bioconcentration factors were 36 and 3,

respectively, for the nominal 1 and 10 μg/L aqueous test substance

concentrations. The dietary assimilation efficiency for the

growth corrected half-life, and the dietary biomagnification factor (BMF)

for the dietary exposure were 0.435, 23.5 days, and 0.295, respectively.

All test acceptance criteria were met ( 2009b).
Ecotoxicology Aquatic Studies Fish 96-hour LC50 (rainbow trout, Oncorhynchus mykiss) >107 mg/L.

The acute toxicity of the test substance ( tested in

solid form) to rainbow trout was determined in an unaerated, 96-hour

toxicity test following OECD Guideline 203. Nominal concentrations

tested were 0, 7.5, 15, 30, 60, and 120 mg/L. The mean water

temperature was 12.1°C (range of 11.9 12.3°C). One test chamber was

used per test concentration with 10 fish in each chamber. Control fish

ranged from 3.0 to 3.3 cm in standard length and 0.260 to 0.352 g in wet

weight, blotted dry, at test end. Dilution water loading at test end was

0.3041 g/L.

Mean measured concentrations were none detected (limit of detection

0.0008 mg/L), 6.82, 14.6, 27.7, 53.4, and 107 mg/L for the 0, 7.5, 15, 30,

60, and 120 mg/L concentrations, respectively. No mortality was

observed at any concentration. Dilution water quality was acceptable

based on OECD criteria and specifications. All chemical and physical

parameters were within the expected ranges. Total alkalinity, EDTA

hardness, and conductivity of the dilution water control and highest test

substance concentration at test start ranged from 48 to 49 mg/L as

CaCO3, 133 to 137 mg/L as CaCO3, and 230 to 255 μmhos/cm,

respectively. During the test, dissolved oxygen concentrations ranged

from 8.5 to 10.4 mg/L, pH ranged from 7.4 to 7.6, and mean temperature

was 12.1°C with a range of 11.9 to 12.3°C ( 2007e).

Ecotoxicology 90-day early life-stage toxicity NOEC (rainbow trout, Oncorhynchus

mykiss) = 2.62 mg/L.

The effect of the test substance ( tested in solid

form) on hatching, growth, and survival of rainbow trout embryos, alevins,

and fingerlings were assessed in an intermittent renewal 90-day early lifestage toxicity test in accordance with OECD Guideline 201 and US EPA

OPPTS 850.1400. Nominal test concentrations were 0, 0.625, 1.25, 2.5,

5, and 10 mg/L. A total of 80 embryos were exposed per concentration

(20 embryos per embryo cup, 2 cups per replicate, 2 replicates per

concentration) at test start. On day 40, after swim-up had begun in the

control, the fingerlings were thinned to a total of 30 fish per concentration

(15 fish per replicate, 2 replicates per concentration). Analytical

verification of test substance concentrations were made on test solutions

sampled on day -3, day 0, once weekly, and on day 90 at test end. Test

solutions were supplied to each replicate test chamber at a rate of

approximately 1.25 L of test solution per test chamber each hour,

resulting in approximately 5 test solution volume additions of 6 L (30 L

total) every 24 hours. Embryos and alevins were held in relative

darkness until day 39, and then held under a photoperiod of 16 hours light

and 8 hours darkness (which included 30 minutes of transitional light

between light and dark intervals) for the remainder of the study. Test

solutions were maintained between 11.9 and 12.9°C (mean 12.2°C).

Daily observations were made for assessment of number of dead eggs at

hatching, first and last day of hatching, first day of swim up, survival and

abnormalities from hatching to thinning, and survival and abnormalities

from thinning to test end. Standard length and blotted wet weight of

surviving fingerlings were determined at test end.

Mean measured test concentrations were 0, 0.857, 1.66, 2.62, 4.85, and

8.70 mg/L at the 0, 0.625, 1.25, 2.5, 5, and 10 mg/L concentrations,

respectively. The NOEC was 2.62 mg/l based on mean, measured

concentrations and first day of hatching values. The LOEC (lowest

observed effect concentration) and MATC (maximum acceptable toxicant

concentration) for the same endpoint were 4.85 and 3.56, respectively.

The NOEC values were 4.85 mg/L for percent eggs hatching and first day

of swimup and >8.7 for the other test endpoints ( 2007f).

Aquatic Studies Fish
Ecotoxicology Aquatic Studies Invertebrates The acute toxicity of the test substance ( tested in

solid form) to unfed Daphnia magna neonates, less than 24 hours old at

test start was determined in an unaerated, 48 hour toxicity test following

OECD Guideline 202. Nominal concentrations tested were 0, 7.5, 15,

30, 60, and 120 mg/L. The mean water temperature was 19.9°C (range

of 19.5-20.1°C). Four replicates with five daphnids per replicate were

used per test substance concentration and control. 

Mean measured concentrations were none detected (limit of detection

0.01 mg/L), 7.09, 14.3, 27.8, 53.4, and 109 mg/L for the 0, 7.5, 15, 30, 60,

and 120 mg/L concentrations, respectively. Immobility at the end of 48

hours was 0, 25, 15, 25, 30, and 50% at 0, 7.09, 14.3, 27.8, 53.4, and 109

mg/L, respectively. Dilution water quality was acceptable based on

OECD criteria and specifications. All chemical and physical parameters

were within the expected ranges. Total alkalinity, EDTA hardness, and

conductivity of the dilution water control and highest test substance

concentration at test start ranged from 50 to 52 mg/L as CaCO3, 134 to

136 mg/L as CaCO3, and 280 to 315 μmhos/cm, respectively. During

the test, dissolved oxygen concentrations ranged from 7.5 to 8.7 mg/L,

pH ranged from 7.6 to 8.1, and mean temperature was 19.9°C with a

range of 19.5 to 20.1°C ( 2007g).
72-hour EbC50 (green alga, Pseudokirchneriella subcapitata) > 96 mg/L

(cell count and area under the curve).

0-72-hour EbC50 (green alga, Pseudokirchneriella subcapitata) > 96

mg/L (area under the curve).

72-hour ErC50 (green alga, Pseudokirchneriella subcapitata) > 96 mg/L

(growth rate).

The toxicity of the test substance ( tested a solid

form) to the green algae was determined in a 72 hour, static toxicity test

following OECD Guideline 201. The study was conducted with a blank

control, an abiotic control, and 5 nominal concentrations of the test

substance (6.25, 12.5, 25, 50, and 100 mg/L) at a mean lighting intensity

of 8498 lux (range of 8200 to 8670 lux), a mean temperature of 23.5°C

(range of 23.5-23.6°C), and a shaking speed of 104 rpm. Synthetic algalassay-procedure (AAP) nutrient medium was used as the test diluent and

blank control. Test solutions were not renewed. Three replicates were

used per test concentration and 6 replicates were used for the blank

control. A single test flask was used for the abiotic (stability) control.

Healthy cell count, area under the growth curve, and growth rate were

determined at 24-hour intervals over the 72-hour test.

Mean measured concentrations were none detected (limit of detection

0.006 mg/L), 6.20, 12.4, 24.2, 47.6, 96, and 99.3 mg/L for the blank

control, 6.25, 12.5, 25, 50, 100, and abiotic control (100 mg/L)

concentrations, respectively. Inhibition of growth expressed as biomass

(cell number) of Pseudokirchneriella subcapitata exposed to nominal

concentrations of 6.25, 12.5, 25, 50, and 100 mg/L for 72 hours was -8, 2,

14, 3, and 20%, respectively. Inhibition of growth expressed as area

under the growth curve was -9, 4, 19, -1, and 14%, respectively.

Inhibition of growth expressed as the average specific growth rate was -1,

0, 2, 0, and 4%, respectively. Healthy cell counts increased in the blank

control by at least a factor of 16 in 72 hours and the coefficient of

variation of average specific growth rates during the whole test period (0-

72 hour) in replicate control cultures did not exceed 7%, thereby

satisfying the appropriate test acceptance criteria ( 2007h).

Ecotoxicology Aquatic Studies Other
Test Substance CAS RN Common Name Structure % CA Index Name

35.6

30

N/A

30

>99

100% (based on 

testing done on solid 

form)

N/A

Category Sub-Category Test Test Substance Report Number Result Summary

Mammalian 

Toxicity

Acute Oral LD50 (rat; Probit method) = 1871 mg/kg 

LD50 (rat; Litchfield and Wilcoxon) = 1871 mg/kg 

LD50 (rat; Arcsinus method) = 2000 mg/kg 

5 male and 5 female rats per group were administered 0.5, 1, 2, or 4 g/kg of 

the test substance ( tested in solid form) in olive oil. They 

were observed during the first hours after intubation and then for 14 days. 

Clinical signs of toxicity observed included red-stained fur (>1000 mg/kg), 

prostration (>1000 mg/kg), nasal congestion (2000 mg/kg), moribund (4000 

mg/kg), and piloerection (4000 mg/kg) ( 1977b).

Mammalian 

Toxicity

Acute Dermal The test substance ( tested in solid form) was a slight skin 

irritant in rabbits.

Undiluted test substance (0.3 g moistened with 0.5 mL water) was applied to 

the surface of the scarified or non-scarified skin of 6 male New Zealand white 

rabbits via gauze squares. The gauze squares were held in place with an 

occlusive adhesive patch. Then tape was wound around the rabbit to 

complete the fixing of the patches. The rabbits were then placed in restraining 

devices for 24 hours. After 23 hours, the patches were removed, and 1 hour 

later the primary irritation index was evaluated. Another reading was made 48 

hours later. The primary cutaneous irritation score was 0.71 ( 1977b).

The toxicological information summarized below is NOT on the PMN substance, 

but on a related substance that may be of interest to the Agency. 

Full study reports are submitted with this PMN. 

Publically available literature studies will not be submitted.

(Test Substance)

Toxicology Summary

*STN's CAS Registry Database has given a CAS RN to a product name. Test substance is CAS RN
The test substance ( tested in solution) was not a 

dermal sensitizer in the local lymph node (LLNA) assay in mice.

Five groups of 5 female CBA/JHsd mice were dosed for 3 consecutive days 

with 0, 5, 25, 50, or 75% of the test substance on both ears following OECD 

and US EPA OPPTS 870.2600 guidelines. N,N-dimethylformamide (DMF) 

was the diluting vehicle. One group of 5 female mice was dosed for 3 

consecutive days with 25% hexylcinnamaldehyde (HCA) in DMF as a positive 

control. On test day 5, mice received 3H-thymidine by tail vein injection and 

were sacrificed approximately 5 hours later. The cell proliferation in the 

draining auricular lymph nodes of the ears was evaluated. 

No differences in mean body weights or body weight gains were observed. 

No clinical signs of toxicity were observed. Statistically significant increases in 

cell proliferation measurements compared to control were observed at the 25, 

50, and 75% test concentrations. Stimulation indices (SIs) of less than 3.0 

were observed at all test concentrations. Therefore, the EC3 value (the 

estimated concentration required to induce a threshold positive response, i.e., 

SI = 3) for the test substance under the conditions of this study was not 

calculable. A 25% concentration of the positive control produced a dermal 

sensitization response in mice. Therefore, the test substance did not produce 

a dermal sensitization response in mice ( 2007a).

Mammalian 

Toxicity

Acute Dermal

Mammalian 

Toxicity

Acute The test substance ( tested in solid form) produced irritation 

with necrosis of the epithelium in the rabbit eye.

Six male New Zealand white rabbits were tested. The test substance (0.1 g) 

was introduced into the rabbit’s left eye, and the right eye served as a control. 

The eyelid was held closed for several seconds, giving a slight massage to 

avoid loss of the substance. The eyes were not washed after administration. 

Macroscopic examination of the eyes was impossible because of the presence

of large edemas of the palpebral conjunctiva. Therefore, the treated eyes of 2 

rabbits per time point were removed at 1, 24, and 48 hours, and were fixed 

and examined microscopically. Marked irritation was observed on the level of 

the cornea after application of 0.1 g of the test substance to the surface of the 

eye. Necrosis followed by disappearance of the epithelial surface was 

observed and was accompanied by alteration in the corneal stroma. At the 

level of the stroma there was pyctonic cores of fibroblastic cells and 

polynuclear infiltrates. Irritation increased over time, as the test substance 

penetrated more deeply into the corneal stroma ( 1977b).

Eye
Mammalian 

Toxicity

Subchronic Oral The test substance ( was incorporated into nutritionally adequate 

chow and fed to male Crl:CD-1®BR mice for 14 consecutive days. Diets 

contained 0, 3, 30, 300, or 3000 ppm of the test substance. Mice were 

weighed and observed for clinical signs of toxicity once each week. At the 

end of the two-week feeding period, all mice were euthanized and necropsied. 

The livers were weighed, and liver weight/final body weight ratios were 

calculated.

No deaths occurred during the study. Other than a body weight effect in mice 

from the 3000 ppm dose group, no adverse clinical signs of toxicity were 

observed during the study. Significant increases in mean absolute and 

relative liver weights were observed in mice from the 300 and 3000 ppm dose 

groups. 

The no-observable-adverse-effect level (NOAEL) was determined to be 30 

ppm based on the increases in mean absolute and relative liver weight 

observed in the 300 and 3000 ppm dose groups and the decreases in body 

weight and body weight gains observed in the 3000 ppm dose group (

1995c).

Mammalian 

Toxicity

Subchronic Oral Groups of 20 male rats (Crl:CD®BR) were fed diets containing 0, 30, or 300 

ppm of the test substance ( for 14 consecutive days. Rats were 

sacrificed at the end of the feeding period and on recovery days seven, 28, 

and 56. Livers were removed and weighed. Blood samples were taken for 

fluoride concentration analysis from rats sacrificed at the end of the feeding 

period and on recovery day seven.

No mortalities occurred during the study. No clinical signs of toxicity were 

observed. Significant increases in mean liver weights were observed in rats 

from the 30 and 300 ppm groups sacrificed at the end of the feeding period. 

No other liver effects were observed in these rats during the study.

Mean blood fluoride concentrations of rats sacrificed on recovery day 0 were 

0.30 ppm in control rats, 5.30 ppm in the 30 ppm rats, and 8.19 ppm in the 

300 ppm rats. On recovery day seven, mean blood fluoride concentrations 

were 0.94 ppm in control rats, 0.58 ppm in the 30 ppm rats, and 0.56 ppm in 

the 300 ppm rats ( 1995d).

Mammalian 

Toxicity

Subchronic Dermal Three male rabbits were exposed dermally to the test substance (

 tested in solution) for 90 days with a 7-day recovery period at a dose of 

2000 mg/kg (30% aqueous solution). The test substance was applied daily (5 

days out of 7) for 13 weeks on the shaved skin of the whole of the right flank 

of each rabbit. The left flank served as a control. The test substance was 

applied and given a light massage of about 30 seconds to ensure maximal 

penetration. After the massage, excess material that had not penetrated the 

skin was wiped off with gauze. Body weights were recorded weekly. The skin 

was examined daily before application of the test substance, and a mean 

index of irritation was determined each week for each animal. After 90 days of 

repeated application, two samples of skin were removed by sterile biopsy and 

evaluated histologically. No effects were observed upon macroscopic or 

microscopic examination. No evidence of allergic reaction was observed. 

The average index of irritation for the 3 rabbits was 0.17 in the 1st, 5th, 6th, 

and 8th weeks. All other time points, the average index of irritation was 0. 

Under the conditions of this study, it was concluded that repeated dermal 

application of a 30% aqueous solution of the test substance for 90 days was 

well tolerated by rabbits ( 1977b).
Mammalian 

Toxicity

Gentic Toxicity In Vitro The test substance ( tested in solution) was not mutagenic in 

the bacterial reverse mutation test with Salmonella typhimurium.

A preliminary toxicity test was performed to define the dose levels to be used 

for the mutagenicity study. The test substance was then tested in two 

independent experiments, with and without a metabolic activation system, S9 

mix, prepared from a liver microsomal fraction (S9 fraction) of rats induced 

with Aroclor 1254. Both experiments were performed according to the direct 

plate incorporation method except for the second test with S9 mix, which was 

performed according to the preincubation method. Five strains of Salmonella 

typhimurium (TA1535, TA1537, TA98, TA100, and TA102) were used. Each 

strain was exposed to five dose levels (three plates per dose). After 48-72 

hours of incubation at 37°C, the revertant colonies were scored. The 

evaluation of the toxicity was performed on the basis of the observation of the 

decrease in the number of revertant colonies and/or a thinning of the bacterial 

lawn. The test substance was dissolved in distilled water. Sodium azide 

(NaN3), 9-aminoacridine (9AA), 2-nitrofluorene (2NF), mitomycin C (MMC), 

and 2-anthramine (2AM) were used as positive controls. 

The number of revertants for the vehicle and positive controls was as 

specified in the acceptance criteria. Since the test substance was freely 

soluble and almost non toxic in the preliminary test, the highest dose for the 

main test was 5000 μg/plate, according to the criteria specified in the 

international guidelines. The selected treatment levels were 312.5, 625, 1250, 

2500, and 5000 μg/plate, for both mutagenicity experiments with and without 

S9 mix. No toxicity was observed, both with and without S9 mix. No increase 

in the number of revertants, both with and without S9 mix, in any of the five 

strains was observed. Therefore, under the conditions of this study, the test 

substance does not show any mutagenic activity in the bacterial reverse 

mutation test with Salmonella typhimurium, with and without S9 mix up to 500

0

μg/plate as active material ( 2002).
Mammalian In Vitro

Toxicity

Gentic Toxicity The test substance ( tested in solution) was positive for the 

induction of structural chromosome aberrations and negative for the induction of 

numerical chromosome aberrations in CHO cells in both non-activated and S9 

activated test systems, following OECD Guideline 473, EC Commission Directive 

2000/32/EC Annex 4A-B10 no. L 136, and US EPA OPPTS Guideline 870.5375. A 

preliminary toxicity test was performed to establish the dose range for the 

chromosome aberration assay. The chromosome aberration assay was used to 

evaluate the clastogenic potential of the test substance.

Water was used as the test substance solvent based on the solubility of the test 

substance and compatibility with target cells. The test substance was soluble in water 

at a concentration of approximately 50 mg/mL, the maximum concentration tested for 

solubility.

In the preliminary toxicity assay, the maximum dose tested was 4280 μg/mL (10 

mM). The test substance was soluble in water at all concentrations tested. Visible 

precipitate was observed in the treatment medium at dose levels >1284 μg/mL and 

dose levels >428 μg/mL were soluble in the treatment medium at the beginning and 

conclusion of the treatment period. Selection of dose levels for the chromosome 

aberration assay was based on cell growth inhibition relative to the solvent control. 

Substantial toxicity (i.e., at least 50% cell growth inhibition, relative to the solvent 

control) was observed at dose levels >428 μg/mL in all three treatment groups. 

Based on these findings, the doses chosen for the chromosome aberration assay 

ranged from 12.5 to 300 μg/mL for all three treatment groups.

In the initial chromosome aberration assay, the cells were treated for 4 and 20 hours 

in the non-activated test system and for 4 hours in the S9-activated test system. All 

cells were harvested 20 hours after treatment initiation. The test substance was 

soluble in water and in the treatment medium at all dose levels tested at the 

beginning and conclusion of the treatment period. Selection of doses for microscopic 

analysis was based on toxicity (the lowest dose with at least 50% reduction in cell 

growth and the next two lower doses) in the S9-activated 4-hour and the nonactivated 20-hour exposure groups.

The percentage of cells with structural aberrations in the S9-activated 4-hour 

exposure group was statistically increased (21.0%) above that of the solvent control 

at 300 μg/mL (p<0.01, Fisher's Exact test). The Cochran-Armitage test was also 

positive for a dose response (p<0.05). The percentage of cells with numerical 

aberrations was statistically increased above that of the solvent control at dose levels 

50 and 150 μg/mL (p<0.01 and p<0.05, respectively, Fisher's Exact test). However, 

the percentages of cells with numerical aberrations at 50 and 150 μg/mL (6.5% and 

6.0%, respectively) were within the historical solvent control range of 0.0% to 10.0%. 

Therefore, they ware not considered to be biologically significant. The percentage of 

cells with structural or numerical aberrations in the non-activated 20-hour exposure 

group was not significantly increased above that of the solvent control at any dose 

level (p>0.05, Fisher's Exact test).

Due to lack of a dose level with close to 50% reduction in cell growth or mitotic index, 

the chromosome aberration assay was repeated in the non-activated 4-hour 

exposure group. Although the dose levels selected for the repeat assay were 25, 

100, 300, 325, 350, 375, 400 and 415 μg/mL, the repeat assay was inadvertently 

tested at the same doses used in the initial assay (12.5, 25, 50, 100, 150, 200, 250 

and 300 μg/mL). Since the toxicity data from the repeat assay showed a shift in 

toxicity (50% reduction in cell growth and mitotic index was achieved), the study 

director concluded that the alternate doses tested in the repeat assay had no 

adverse effect on the outcome of the study. In the repeat chromosome aberration 

assay, the cells were treated for 4 hours in the non-activated test system. All cells 

were harvested 20 hours after treatment initiation. The test substance was soluble in 

water and in the treatment medium at all dose levels tested at the beginning and 

conclusion of the treatment period. Selection of doses for microscopic analysis was 

based on toxicity (the lowest dose with at least 50% reduction in cell growth and the 

next two lower doses) in the non-activated 4-hour exposure group.

The percentage of cells with structural aberrations in the non-activated 4-hour 

exposure group was statistically increased (23.0%) above that of the solvent control 

at 300 μg/mL (p<0.01, Fisher's Exact test). The Cochran-Armitage test was also 

positive for a dose response (p<0.05). The percentage of cells with numerical 

aberrations in the test substance-treated group was not significantly increased above 

that of the solvent control at any dose level (p>0.05, Fisher's Exact test) (

2007b).
The test substance ( tested in solution) was negative 

in the Unscheduled DNA Synthesis (UDS) test in mammalian cells in vivo, 

following OECD Guideline 486; EC Annex V to Directive 67/548/EEC, 

Directive 2000/32/EC, B.39; OPPTS Guideline 870.5550; ICH S2A document 

April 24, 1996; and ICH S2B document November 21, 1997.

For the pilot toxicity assay, the test substance was administered via oral 

gavage to male rats at 10, 100, 1000, and 2000 mg/kg body weight in a total 

volume of 10 mL/kg bw. All animals treated with <1000 mg/kg appeared 

normal less than 4 hours following dosing, and 1, 2, and 3 days following 

dosing. All animals treated with 2000 mg/kg appeared normal less than 4 

hours following dosing. However, on Day 1 following administration, they were 

lethargic, with 3 animals having crusty noses and 1 animal having crusty eyes. 

On Day 2, one animals was found dead, while the remaining appeared normal 

on Days 2 and 3. Based on the information from the pilot toxicity assay, the 

high dose for the UDS assay was set at the maximum tolerated dose, which 

was 2000 mg/kg, accompanied by two lower doses of 500 and 1000 mg/kg.

In the UDS test, the test substance was administered to 5 male rats per dose 

for 2 to 4 hours and 12 to 16 hours at doses of 500 and 1000 mg/kg. The test 

substance was administered to 7 male rats for 2 to 4 hours and 12 to 16 hours 

at 2000 mg/kg to ensure that at least three animals would be available for 

UDS evaluation. Two additional groups of 5 rats each, for each time point, 

received a single oral dose of distilled water or 35 mg/kg dimethylnitrosamine 

(DMN), which served as the vehicle and positive control, respectively. The 

vehicle control, positive control, and test substance were administered at a 

constant volume of 10 mL/kg bw by a single oral gavage injection. No 

mortality or clinical signs were observed in any of the test substance or control

-

treated harvested animals immediately following dosing or prior to harvest. 

The group mean net nuclear grain (NG) counts for animals treated with the 

test substance were not increased when compared to the vehicle control. For 

the 2 to 4 hour time point, the group mean NG counts for the test substancetreated animals were -5.1, -6.5, and -7.2 with 1% of cells in repair (cells with 

>5 NG) for the 500, 1000, and 2000 mg/kg animals, respectively. The group 

mean NG count for the vehicle control was -5.8 with 0% of cells in repair. For 

the 12- to 16-hour time point, the group mean NG counts for the test 

substance-treated animals were -4.5, 4.6, and -4.2 with <3% of cells in repair 

(cells with >5 NG) for the 500, 1000, and 2000 mg/kg animals, respectively. 

The group mean NG count for the vehicle control was -7.1 with 1% of cells in 

repair. The positive control group mean NG counts were 14.3 and 13.8 for the 

2 to 4 and the 12 to 16 hour, respectively. The percentage of cells in repair 

for the positive control group was 92% and 93% for the 2 to 4 hour and 12 to 

16 hour, respectively. The test substance did not induce a significant increase 

in the mean number of net nuclear grain counts (i.e., an increase of at least 5 

counts over the vehicle control group) in hepatocytes isolated either 2 to 4 

hours or 12 to 16 hours after dose administration ( 2007c).

Mammalian Gentic Toxicity In Vivo

Toxicity
Mammalian Gentic Toxicity In Vivo

Toxicity

The test substance ( tested in solution) was negative for 

clastogenicity in the micronucleus and chromosome aberration assays, following 

OECD Guidelines 474 and 475; EC Commission Directive 2000/32/EC Annex 4B 

B11 and 4C-B12 No. L 136; and US EPA OPPTS Guideline 870.5395 and 870.5385. 

The study was performed in two phases. The first phase, the pilot toxicity study, was 

designed to assess the toxicity of the test substance and to set dose levels for the 

definitive phase of the study. The second phase, the definitive study, was designed 

to evaluate the potential of the test substance to increase the incidence of 

chromosome aberrations in bone marrow cells (chromosome aberration assay) and 

the incidence of micronucleated polychromatic erythrocytes in bone marrow 

(micronucleus assay) of male and female ICR mice. Sterile water was used as the 

test substance vehicle. In the definitive phase of the study, water was used as the 

vehicle (negative) control substance and cyclophosphamide monohydrate (CP), at a 

dose of 50 mg/kg, as the positive control substance. In both phases of the study, test 

or control substances were administered as a single oral gavage.

In the pilot toxicity study, two male mice each were exposed to the test substance at 

1, 10, 100, or 1000 mg/kg while five male and five female mice were exposed at 

2000 mg/kg. No mortality was observed. Piloerection was seen in all males at doses 

>10 mg/kg and all females at 2000 mg/kg. Also at 2000 mg/kg lethargy (males and 

females) and hunched position (females) were observed. All males at 1 mg/kg 

appeared normal following dose administration and throughout the observation 

period. Reductions in the mean group animal body weights were observed in some 

of the groups during the course of the study. In the absence of mortality in the pilot 

toxicity study, the high dose for the definitive study was set at 2000 mg/kg.

The definitive phase of the study consisted of four treatment groups, each containing 

10 male and 10 female mice with the exception of the high dose group that had total 

of 15 animals/sex. Doses were 0, 500, 1000, or 2000 mg/kg. Five male and five 

female mice per each treatment group were euthanized 24-hour post-dose and the 

remaining five animals per sex and treatment were euthanized at 48 hour post-dose. 

An additional 5 male and 5 female mice were dosed with the positive control 

substance (CP) and were euthanized 24-hour post-dose. From each animal, at the 

time of euthanasia, bone marrow from one femur was collected and processed for 

micronucleus analysis and the bone marrow from the other femur was processed for 

analysis of chromosome aberrations.

Bone marrow cells [polychromatic erythrocytes (2000 PCEs/animal)] from all 24 hour 

groups and the vehicle and the high dose 48-hour groups were examined 

microscopically for the presence of micronuclei (MPCEs). One thousand total 

erythrocytes were evaluated for cytotoxicity. Numerical and structural chromosome 

aberrations were analyzed in 100 metaphase cells per animal from all 24-hour 

groups and the vehicle and high dose 48-hour groups. In addition, the mitotic index 

was recorded as the percentage of cells in mitosis based upon a total of 1000 cells 

per animal.

No mortality was observed during the definitive study. Piloerection was seen in 3/15 

males at 2000 mg/kg. All other males at 2000 mg/kg and all males and females 

treated with the lower doses or the control substances appeared normal following 

dose administration and throughout the course of the study. No statistically 

significant or biologically relevant reductions in the PCEs/ECs ratio or incidence of 

structural or numerical chromosome aberrations in test substance-treated groups 

relative to the respective vehicle control groups in male or female mice at 24 or 48 

hours after dose administration was observed. Dose-dependant reductions in the 

mitotic index relative to the vehicle control groups of up to 54.2% and 51.7% in the 

male and female 24-hour test substance-treated groups, respectively, were 

observed. At 48-hour post-dose, a reduction in the mitotic index of 25.4% was 

observed in the male test substance-treated group. The observed reductions in 

mitotic index suggest that the test substance reached the target cells. CP, the 

positive control, induced a statistically significant increase in the incidence of 

micronucleated PCEs and a statistically significant increase in the incidence of 

structural chromosome aberrations in both male and female mice. The incidence of 

micronucleated PCEs and chromosome aberrations in the vehicle control groups did 

not exceed the historical vehicle control range. Based upon this, all criteria for a valid 

test were met as specified in the protocol.

In conclusion, under the conditions described in this report, a single oral 

administration of the test substance at doses up to and including 2000 mg/kg, did not 

induce a significant increase in the incidence of micronucleated polychromatic 

erythrocytes or structural or numerical chromosome aberrations in bone marrow of 

male or female ICR mice. This indicates that the test substance was negative for 

induction of chromosome aberrations in bone marrow cells and micronucleated 

polychromatic erythrocytes in bone marrow and therefore was concluded to have no 

genotoxic/clastogenic potential. The test substance was concluded to be negative in 

this in vivo study ( 2007d).
Mammalian 

Toxicity

Metabolism 

Studies

Male and female rats were given single oral doses (10 or 30 mg/kg) the test 

substance ; tested in solution) in a biopersistence and 

pharmacokinetic screen. Three rats per sex per dose level were used. Blood 

was collected at 0, 0.25, 0.5, 1, 2, 4, 8, 12, 24, 48, 72, 96, 120, 144, and 168 

hours. Fat and liver were analyzed for parent compound to provide an 

estimate of tissue:plasma ratio.

At sacrifice, fat:plasma ratio in females was below the limit of quantification 

(LOQ). The ratios in males given 10 or 30 mg/kg were <0.1 and 0.1, 

respectively. At sacrifice, liver:plasma ratios in females were calculated since 

plasma values were below the LOQ. The ratios in males given 10 or 30 

mg/kg were 3 and 3.1, respectively ( 2007j).

Mammalian 

Toxicity

Metabolism 

Studies

The rate and extent of urinary elimination of the test substance 

 tested in solution) found in male rat urine 96 hours after dosing was 

studied. Three male rats were given a single oral dose of 73 μM/kg. Urine 

was sampled at 6, 24, 48, 72, and 96 hours. Recovery was 68% by LC/MS 

and 65% by NMR. The urine t1/2 was 23.7 and 20.9 hours determined by 

LC/MS and NMR, respectively ( 2007k).

Mammalian 

Toxicity

Metabolism 

Studies

Live and heat inactivated male rat liver S9 (2 mg/mL protein concentration) 

fractions were exposed to 2.5uM ( for a total of two 

hours. At the end of two hours, the reaction was quenched by the addition of 

acetonitrile (1:2, sample:acetonitrile) and analyzed for parent compound by 

LC/MS. The final concentration of was 129.1 (+/- 22.6) and 

106.7 (+/- 6.0) mg/mL from the live and heat inactivated control samples 

respectively. was not metabolized by male rat liver S9 under 

the conditions of this assay ( 2009a). 

Ecotoxicology Environmental 

Fate

Biodegradation The ready biodegradability was determined with a non-adapted activated 

sludge for over a test period of 29 days in the Modified Sturm Test. 

was tested at a concentration of 150 mg/L in duplicates, 

corresponding to a carbon content (TOC) of 10.1 mgC/L in the test vessels. 

The biodegradation of was followed by titrimetric analyses of the 

quantity of CO2 produced by the respiration of bacteria. The degradation was 

finished on day 28 by acidification, the last titration was made on day 29, after 

the soluble CO2 was turned out over a period of 24 hours. The percentage 

CO2 production was calculated in relation to the theoretical CO2 (ThCO2) of 

The biodegradation was calculated for each titration time. To check 

the activity of the test system, sodium acetate was used as the functional 

control. For sodium acetate, the pass level of 60% was reached after 8 days 

therefore showing the validity of the test system.

For the 10% level (beginning of biodegradation) was reached after 

13 days. The pass level of 60% was not reached, neither in the 10-day 

window nor after 28 days. The mean biodegradation of came to a 

maximum of 42% after 28 days and therefore, should be regarded as not 

readily biodegradable ( 2006).
Ecotoxicology Environmental 

Fate

Biodegradation Not Applicable Environ. Sci. 

Technol., 32:2283-

2287.

Partial defluorination was observed in an isolate of Pseudomonas sp. strain 

D2 under aerobic, sulfur limiting conditions in mineral medium in a laboratory 

study (Key et al., 1998).

Key BD, Howell RD, and Criddle CS (1998). Defluorination of organofluorine 

sulfur compounds by Pseudomonas sp. strain D2. Environ. Sci. Technol., 

32:2283-2287.

Ecotoxicology Aquatic 

Studies

Fish 96-hour LC50 (rainbow trout, Oncorhynchus mykiss) >108 mg/L.

The acute toxicity of the test substance ( tested in 

solution) to rainbow trout was determined in an unaerated, static acute 96-

hour limit test following OECD Guideline 203. Nominal concentrations tested 

were 0 and 120 mg/L. The mean water temperature was 12.4°C (range of 

12.3-12.5°C). One test chamber was used per test concentration with 10 fish 

in each chamber. Control fish ranged from 3.3 to 4.3 cm in standard length 

(mean 3.93 cm) and 0.380 to 0.938 g in wet weight, blotted dry (mean 0.707 

g) at test end. Control loading at test end was 0.354 g/L.

Mean measured concentrations were none detected (limit of detection 0.4 

μg/L) and 108 mg/L for the 0 and 120 mg/L concentrations, respectively. No 

mortality or sublethal effects were observed at any concentration. Dilution 

water quality was acceptable based on OECD criteria and specifications. All 

chemical and physical parameters were within the expected ranges. Total 

alkalinity, EDTA hardness, and conductivity of the dilution water control and 

highest test substance concentration at test start ranged from 47 to 48 mg/L 

as CaCO3, 102 to 121 mg/L as CaCO3, and 245 to 255 μmhos/cm, 

respectively. During the test, dissolved oxygen concentrations ranged from 

7.6 to 9.9 mg/L, pH ranged from 7.0 to 7.2, and mean temperature was 12.4°C 

with a range of 12.3 to 12.5°C ( 2008b).

Ecotoxicology Aquatic 

Studies

 Invertebrates 48-hour EC50 (Daphnia magna) > 112 mg/L.

The acute toxicity of the test substance ( tested in 

solution) to unfed Daphnia magna neonates, less than 24 hours old at test 

start was determined in an unaerated, static, acute, 48 hour limit test following 

OECD Guideline 202. Nominal concentrations tested were 0 and 120 mg/L. 

The mean water temperature was 19.8°C (range of 19.6-19.9°C). Four 

replicates with five daphnids per replicate were used per test substance 

concentration and control. 

Mean measured concentrations were none detected (limit of detection 0.7 

μg/L) and 112 mg/L for the 0 and 120 mg/L concentrations, respectively. No 

immobility or sublethal effects were observed at any concentration at the end 

of the 48-hour limit test. Dilution water quality was acceptable based on 

OECD criteria and specifications. All chemical and physical parameters were 

within the expected ranges. Total alkalinity, EDTA hardness, and conductivity 

of the dilution water control and highest test substance concentration at test 

start ranged from 49 to 50 mg/L as CaCO3, 121 to 123 mg/L as CaCO3, and 

245 to 250 μmhos/cm, respectively. During the test, dissolved oxygen 

concentrations ranged from 8.5 to 9.2 mg/L, pH ranged from 7.2 to 8.0, and 

mean temperature was 19.8°C with a range of 19.6 to 19.9°C (

2008c).
Ecotoxicology Terrestrial 

Studies

Soil Dwelling 

Organisms

6:2 fluorotelomer sulfonate 

(6:2 FTS)

Not Applicable BCF were determined for both adults and offspring and was 3.0 and 2.7, 

respectively (SFT, 2006).

Statens forurensningstilsyn (Norwegian Pollution Control Authority) [SFT] 

(2006). Økotoksikologiske effekter av PFOS, PFOA og 6:2 FTS på 

meitemark (Eisenia fetida), TA-2212/2006 (December) 

(http://www.sft.no/publikasjoner/kjemikalier/2212/ta2212.pdf ; accessed 

January 7 2009).

Ecotoxicology Terrestrial 

Studies

Soil Dwelling 

Organisms

6:2 fluorotelomer sulfonate 

(6:2 FTS)

Not Applicable Exposing earthworms to soils from the four fire training facilities resulted in 

mean bioaccumulation factors (BAFs) for 6:2 fluoroteleomer sulphonate (6:2 

FTS), PFOS and PFOA of 2.4 (0.76-6.7), 2.6 (0.49-6.4) and 5.9 (0.31-14.0), 

respectively (SFT, 2008).

Statens forurensningstilsyn (Norwegian Pollution Control Authority) [SFT] 

(2008). Screening of polyfluorinated organic compounds at four fire training 

facilities in Norway (http://www.klif.no/publikasjoner/2444/ta2444.pdf).

Ecotoxicology Terrestrial 

Studies

Soil Dwelling 

Organisms

Not Applicable Accumulation experiments using standard soil (OECD-soil) have shown that 

earthworms bioaccumulate PFOS, PFOA and 6:2 FTS encountering BAFs of 

about 1-3. 6:2 FTS had somewhat higher BAFs than PFOS and PFOA 

(Stubberud, 2006).

Stubberud, H. 2006. Økotoksikologiske effecter av PFOS, PFOA og 6:2 FTS 

på meitemark

(Eisenia fetida). (in Norwegian, English summary). Report TA 2212/2006. 

Norwegian State

Pollution Control Authority, PB 8100 Dep, 0032 Oslo (cited in SFT, 2008).

72-hour EbC50 (green alga, Pseudokirchneriella subcapitata) > 125 mg/L (cell 

count).

0-72-hour EbC50 (green alga, Pseudokirchneriella subcapitata) > 125 mg/L 

(area under the curve).

72-hour ErC50 (green alga, Pseudokirchneriella subcapitata) > 125 mg/L 

(growth rate).

The toxicity of the test substance ( tested in solution) 

to the green algae was determined in a 72 hour, static limit test following 

OECD Guideline 201. The study was conducted with a blank control, an 

abiotic control, and 1 nominal concentration of the test substance (125 mg/L) 

at a mean lighting intensity of 7250 lux (range of 6760 to 7570 lux), a mean 

temperature of 24.0°C (range of 24.0-24.1°C), and a shaking speed of 104 

rpm. Synthetic algal-assay-procedure (AAP) nutrient medium was used as the

test diluent and blank control. Test solutions were not renewed. Six 

replicates were used for the limit test concentration and blank control. A 

single test flask was used for the abiotic (stability) control. Healthy cell count, 

area under the growth curve, and growth rate were determined at 24-hour 

intervals over the 72-hour test.

Mean measured concentrations were none detected (limit of detection 0.2 

μg/L), 125, and 121 mg/L for the blank control, 120 mg/L, and abiotic control 

(120 mg/L) concentrations, respectively. Inhibition of growth expressed as cell 

count (density), area under the growth curve (biomass), and average specific 

growth rate of Pseudokirchneriella subcapitata exposed to a mean, measured 

limit test concentration of 125 mg/L for 72 hours was 20, 22, and 4%, 

respectively. Healthy cell counts increased in the blank control by at least a 

factor of 16 in 72 hours and the coefficient of variation of average specific 

growth rates during the whole test period (0-72 hour) in replicate control 

cultures did not exceed 7%, and the mean coefficient of variation for sectionby-section specific growth rates (days 0-1, 1-2, and 2-30 in the blank control 

replicates did not exceed 35%, thereby satisfying the appropriate test 

acceptance criteria ( 2008d).

Ecotoxicology Aquatic 

Studies

Other