2-Pentene, 1,1,1,2,3,4,5,5,5-nonafluoro-4-(trifluoromethyl)-, (E)-

Ecotoxicological Summary

Hazard for aquatic organisms

Freshwater

Hazard assessment conclusion:

PNEC aqua (freshwater)

PNEC value:

0.012 µg/L

Assessment factor:

1 000

Marine water

Hazard assessment conclusion:

PNEC aqua (marine water)

PNEC value:

0.001 µg/L

Assessment factor:

10 000

STP

Hazard assessment conclusion:

PNEC STP

PNEC value:

10 mg/L

Assessment factor:

100

Sediment (freshwater)

Hazard assessment conclusion:

PNEC sediment (freshwater)

PNEC value:

3.16 µg/kg sediment dw

Extrapolation method:

equilibrium partitioning method

Sediment (marine water)

Hazard assessment conclusion:

PNEC sediment (marine water)

PNEC value:

0.316 µg/kg sediment dw

Extrapolation method:

equilibrium partitioning method

Hazard for air

Air

Hazard assessment conclusion:

PNEC air

PNEC value:

0.2 µg/m³

Hazard for terrestrial organisms

Soil

Hazard assessment conclusion:

PNEC soil

PNEC value:

0.369 µg/kg soil dw

Extrapolation method:

equilibrium partitioning method

Hazard for predators

Secondary poisoning

Hazard assessment conclusion:

no potential for bioaccumulation

Additional information

PNEC derivations for persistent degradation products:

 

Hydrogen Fluoride (CAS# 7664-39-3): Using available aquatic toxicity data(1) PNECs were calculated to be 0.4 mg/L for freshwater and 0.04 mg/L for marine water. Acute and chronic results were available for three taxonomic groups. For the calculation of the Freshwater PNEC a 21-day LC05 (equivalent to NOEC) of 4.0 mg/L was obtained from a study with Oncorhynchus mykiss. Therefore, an AF of 10 was applied to the fish NOEC, which is the lowest of the three long-term NOECs. Although there are acute data available for marine species, there are no chronic data and there is acute data available for only one additional taxa (mollusk). Therefore, the PNEC derived from the most sensitive chronic study conducted in freshwater is divided by 10 to derive the marine PNEC. For the STP PNEC, a NOEC of 510 mg/L was available for activated sludge respiration inhibition.  An assessment factor of 10 was applied to the NOEC to derive a PNEC of 51 mg/L for STP. No test results for FW Sediment were available. PNEC was extrapolated using the equilibrium partitioning method (EPM) with the freshwater PNEC. PNECsed = (0.783 + (0.0217 x Koc)) x PNECfreshwater, where the Koc was 0.063 and the freshwater PNEC was 0.4 mg/L. PNEC converted to dry weight: (PNEC mg/kg ww) x 4.6 = PNEC of 1.44 mg/kg dry wt. No test results for Marine Sediment were available. PNEC was extrapolated using the equilibrium partitioning method (EPM) with the marine PNEC. PNECmarinesed = (0.783 + (0.0217 x Koc)) x PNECmarinewater, where the Koc was 0.063 and the marine PNEC was 0.04 mg/L. PNEC converted to dry weight: (PNEC mg/kg ww) x 4.6 = PNEC of 0.144 mg/kg dry wt.

A large data set of fumigation studies with vegetation was evaluated. Data from studies with a 7-month exposure period were used to derive the PNECair. The lowest value calculated as protective of vegetation was 0.2 ug/m3. Because of the large data set and the long exposure period, no application factor was applied to this protective value to derive the PNEC of 0.2 ug/m3. A great number of soil studies were available. Data from the most sensitive endpoints from long-term studies from three trophic levels were evaluated. An application factor of 10 was applied to the most sensitive NOEC of 106 mg/kg for soil microbe NO3 mineralization. PNEC converted to dry weight: (PNEC mg/kg ww) x 1.13 = PNEC of 12 mg/kg dry weight. HF is an inorganic acid and thus not considered PBT by the REACh criteria. Because this substance is an inorganic acid, and because the Kow value indicates low bioconcentration potential, secondary poisoning is not relevant. Log Kow = -1.4.

(1) European Chemicals Bureau European Union Risk Assessment: Hydrogen Fluoride, 2001.

 

Trifluoroacetic acid (CAS#76-05-1): Using available aquatic toxicity data(1, 2) PNECs were calculated to be 0.0064 mg/L for freshwater and 0.00064 mg/L for marine water. Acute results were available for three taxonomic groups. For the calculation of the Freshwater PNEC a 72-hour ErC50 value of 6.4 mg/L was obtained from a study with Pseudokirchneriella subcapitata. Chronic studies were not conducted. Therefore, an AF of 1000 was applied to the algae ErC50, which is the lowest of the acute EC/LC50 values. One study was available on toxicity to marine organisms. The marine diatom Phaeodactylum tricornutum 72-hr ErC50 was reported as > 97.5 mg TFA/L. The freshwater alga P. subcapitata was found to be more sensitive, therefore an additional factor of 10 was applied to the Freshwater PNEC to derive the Marine Water PNEC. For the STP PNEC, a NOEC of 10 mg/L was available for respiration inhibition in an aerobic soil microcosm study(3).  An assessment factor of 10 was applied to the NOEC to derive a PNEC of 1.0 mg/L for STP. No test results for FW Sediment were available. PNEC was extrapolated using the equilibrium partitioning method (EPM) with the freshwater PNEC. PNECsed = (0.783 + (0.0217 x Koc)) x PNECfreshwater, where the Koc was 0.023 and the freshwater PNEC was 0.0064 mg/L. PNEC converted to dry weight: (PNEC mg/kg ww) x 4.6 = PNEC of 0.023 mg/kg dry wt. No test results for Marine Sediment were available. PNEC was extrapolated using the equilibrium partitioning method (EPM) with the marine PNEC. PNECmarinesed = (0.783 + (0.0217 x Koc)) x PNECmarinewater, where the Koc was 0.023 and the marine PNEC was 0.00064 mg/L. PNEC converted to dry weight: (PNEC mg/kg ww) x 4.6 = PNEC of 0.0023 mg/kg dry wt.

No experimental data available for air. As this study is not a standard information requirement in REACH and there is no indication from the CSA on the need to investigate further the atmospheric compartment, no PNEC air was derived. Multiple studies of long-term toxicity to plants were available, but plants were the only trophic level evaluated (1). Therefore an application factor of 100 was applied to the most sensitive long-term study result (0.83 mg/kg dry weight in soil), to derive a PNECsoil of 0.0083 mg/kg. TFA is expected to remain in the soil water and not sorb to soil. Plants exposed hydroponically showed more sensitivity than those where soil was dosed. PNEC was also determined using the equilibrium partitioning method (EPM) and the freshwater PNEC: PNECsoil = (0.174 + (0.0104 x Koc)) x PNECwater, where the Koc was 0.023 and the freshwater PNEC was 0.0064 mg/L. This value was then converted to dry weight: (PNEC mg/kg ww) x 1.13 = PNEC of 0.0013 mg/kg dry weight. The PNEC derived using the equilibrium method was lower than that derived using application factors. Because this value was the lesser of the two and because TFA is expected to remain in the soil water, the PNEC derived with the EPM method, 0.0013 mg/kg dw, will be the definitive value. TFA is not readily biodegradable. However, Bioconcentration was evaluated using TFA uptake data from several aquatic studies and terrestrial plant studies (1). BCF values ranged from 1.0 - 43. It is thought that uptake into terrestrial plants is in part due to translocation of dissolved TFA in the tissue water (1). None of these studies demonstrated that TFA would be considered bioaccumulative. In addition, the log Kow was reported to be -2.1. Therefore, bioaccumulation of TFA in terrestrial or aquatic organisms is not expected and secondary poisoning does not need to be considered further in this assessment.

(1)Boutonnet (Ed.), 1999.   Environmental Risk Assessment of Trifluoroacetic Acid.   Human and Ecological Risk Assessment:   Vol. 5, No. 1, pp. 59-124.  

(2) Mark L. Hanson, Keith R. Solomon. Haloacetic acids in the aquatic environment.Part I: macrophyte toxicity. Environmental Pollution 130 (2004) 371-383

(3) Benesch, J.A. et al., 2002. Investigation of effects of trifluoroacetate on vernal pool ecosystems. Environmental Toxicology and Chemistry, Vol. 21, No. 3, pp. 640-647.

 

Iso Perfluorobutyric acid (CAS 335-10-4): Using available aquatic toxicity data, the freshwater PNEC was found to be 2.6 mg/L and the marine PNEC 0.26 mg/L. Acute results from testing perfluorobutyric acid were available for 12 species in at least three taxonomic groups and chronic for three species in two taxonomic groups. As per R.10, Table R.10-4 footnote (d): one can reduce the AF to 10 in cases where it is possible to determine with high probability that the most sensitive species has been examined, i.e. that a further long-term result (e.g. EC10 or NOEC) from a different taxonomic group would not be lower than the data already available. This is also appropriate because perfluorobutyric acid does not bioaccumulate (BCF reported as < 3 - 6 at the 0.02 mg/L exposure and < 28 at the 0.2 mg/L exposure in a BCF test with carp). P. subcapitata has an ErC50 nearly one order of magnitude lower than and a NOEC more than one order of magnitude lower than all other organisms tested, including the green alga C. vulgaris. This extreme sensitivity of P. subcapitata has been seen with other small chain pefluorinated acids (i.e. trifluoroacetic acid). An AF of 10 will be taken in this case due to the evidence from the large data set for this substance and the evidence for testing with trifluoroacetic acid. For the calculation of the Freshwater PNEC a 72-hour ErC10 value of 26 mg/L was obtained from a study with Pseudokirchneriella subcapitata. An AF of 10 was applied to this algae ErC10. There is no additional data available on marine taxonomic groups. An additional factor of 10 was applied to the Freshwater PNEC to derive the Marine Water PNEC. For the STP PNEC, a NOEC of 1000 mg/L was available for activated sludge respiration inhibition.  An assessment factor of 10 was applied to the NOEC to derive a PNEC of 100 mg/L for STP. No test results for freshwater sediment were available. PNEC was extrapolated using the equilibrium partitioning method (EPM) with the freshwater PNEC. PNECsed = (0.783 + (0.0217 x Koc)) x PNECfreshwater, where the Koc was 1.0 L/kg and the freshwater PNEC was 2.6 mg/L. PNEC converted to dry weight: (PNEC mg/kg ww) x 4.6 = PNEC of 9.61 mg/kg dry wt. No test results for Marine Sediment were available. PNEC was extrapolated using the equilibrium partitioning method (EPM) with the marine PNEC. PNECmarinesed = (0.783 + (0.0217 x Koc)) x PNECmarinewater, where the Koc was 1.0 L/kg and the marine PNEC was 0.26 mg/L. PNEC converted to dry weight: (PNEC mg/kg ww) x 4.6 = PNEC of 0.961 mg/kg dry wt.

No experimental data available on air. As this study is not a standard information requirement in REACH and there is no indication from the CSA on the need to investigate further the atmospheric compartment, no PNEC was derived. No test results for Soil were available. PNEC was extrapolated using the equilibrium partitioning method (EPM) including the freshwater PNEC, PNECsoil = (0.174 + (0.0104 x Koc)) x PNECwater, where the Koc was 1.0 L/kg and the freshwater PNEC was 2.6 mg/L. PNEC converted to dry weight: (PNEC mg/kg ww) x 1.13 = PNEC of 0.541 mg/kg dry weight. Although PFBA is not readily biodegradable, the bioconcentration factor was found to be < 28 in a laboratory study with fish. This substance is not considered bioaccumulative.  Therefore, the PNEC oral is not applicable and was not derived.

Conclusion on classification

For HFP Kinetic Dimer:

CLP Aquatic acute: Acute 1

M-Factor: 10

Aquatic chronic: Chronic 2

M-factor chronic: N/A 

Ozone Depletion: HFP Kinetic Dimer is not listed in the Montreal Protocol on Substances that Deplete the Ozone Layer. It does not contain reactive halogens (chlorine or bromine) that could play a role in ozone depletion. HFP Kinetic Dimer is not hazardous to the ozone layer. Conclusive although not sufficient for classification.

 

 

Trifluoroacetic acid degradation product (CAS# 76 -05 -01):

CLP: Aquatic acute: Not classified - conclusive although not sufficient for classification.

M-factor acute: N/A

Aquatic Chronic 3

M-factor chronic: N/A 

Ozone Depletion: Trifluoroacetic acid is not listed in the Montreal Protocol on Substances that Deplete the Ozone Layer. It does not contain reactive halogens (chlorine or bromine) that could play a role in ozone depletion. TFA is not hazardous to the ozone layer. Conclusive although not sufficient for classification.

 

Hydrogen fluoride degradation product (CAS# 7664 -39 -3):

CLP: Aquatic acute: Not clasified - conclusive although not sufficient for classification.

M factor acute: N/A

Aquatic chronic: Not classified - conclusive although not sufficient for classification.

M factor chronic: N/A

Ozone Depletion: HF is not listed in the Montreal Protocol on Substances that Deplete the Ozone Layer. It does not contain reactive halogens (chlorine or bromine) that could play a role in ozone depletion. HF is not hazardous to the ozone layer. Conclusive although not sufficient for classification.

 

Iso Perfluorobutyric acid degradation product (CAS# 335 -10 -4)

CLP: Aquatic acute: Not classified - conclusive although not sufficient for classification.

M-factor: N/A

Aquatic chronic: Not classified - conclusive although not sufficient for classification.

M-factor: N/A

Ozone depletion: Iso Perfluorobutyric acid is not listed in the Montreal Protocol on Substances that Deplete the Ozone Layer. It does not contain reactive halogens (chlorine or bromine) that could play a role in ozone depletion. HF is not hazardous to the ozone layer. Conclusive although not sufficient for classification.