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EC number: 200-076-7 | CAS number: 51-03-6
- Life Cycle description
- Uses advised against
- Endpoint summary
- Appearance / physical state / colour
- Melting point / freezing point
- Boiling point
- Density
- Particle size distribution (Granulometry)
- Vapour pressure
- Partition coefficient
- Water solubility
- Solubility in organic solvents / fat solubility
- Surface tension
- Flash point
- Auto flammability
- Flammability
- Explosiveness
- Oxidising properties
- Oxidation reduction potential
- Stability in organic solvents and identity of relevant degradation products
- Storage stability and reactivity towards container material
- Stability: thermal, sunlight, metals
- pH
- Dissociation constant
- Viscosity
- Additional physico-chemical information
- Additional physico-chemical properties of nanomaterials
- Nanomaterial agglomeration / aggregation
- Nanomaterial crystalline phase
- Nanomaterial crystallite and grain size
- Nanomaterial aspect ratio / shape
- Nanomaterial specific surface area
- Nanomaterial Zeta potential
- Nanomaterial surface chemistry
- Nanomaterial dustiness
- Nanomaterial porosity
- Nanomaterial pour density
- Nanomaterial photocatalytic activity
- Nanomaterial radical formation potential
- Nanomaterial catalytic activity
- Endpoint summary
- Stability
- Biodegradation
- Bioaccumulation
- Transport and distribution
- Environmental data
- Additional information on environmental fate and behaviour
- Ecotoxicological Summary
- Aquatic toxicity
- Endpoint summary
- Short-term toxicity to fish
- Long-term toxicity to fish
- Short-term toxicity to aquatic invertebrates
- Long-term toxicity to aquatic invertebrates
- Toxicity to aquatic algae and cyanobacteria
- Toxicity to aquatic plants other than algae
- Toxicity to microorganisms
- Endocrine disrupter testing in aquatic vertebrates – in vivo
- Toxicity to other aquatic organisms
- Sediment toxicity
- Terrestrial toxicity
- Biological effects monitoring
- Biotransformation and kinetics
- Additional ecotoxological information
- Toxicological Summary
- Toxicokinetics, metabolism and distribution
- Acute Toxicity
- Irritation / corrosion
- Sensitisation
- Repeated dose toxicity
- Genetic toxicity
- Carcinogenicity
- Toxicity to reproduction
- Specific investigations
- Exposure related observations in humans
- Toxic effects on livestock and pets
- Additional toxicological data
Biodegradation in soil
Administrative data
Link to relevant study record(s)
- Endpoint:
- biodegradation in soil: simulation testing
- Type of information:
- experimental study
- Adequacy of study:
- key study
- Study period:
- 1991
- Reliability:
- 1 (reliable without restriction)
- Rationale for reliability incl. deficiencies:
- guideline study
- Principles of method if other than guideline:
- EPA Guideline, Subdivision N, Section 162-2
- GLP compliance:
- yes
- Test type:
- laboratory
- Radiolabelling:
- yes
- Oxygen conditions:
- anaerobic
- Soil classification:
- not specified
- Soil type:
- sandy loam
- % Clay:
- 56
- % Silt:
- 26
- % Sand:
- 18
- % Org. C:
- 1.6
- pH:
- 6.8
- CEC:
- 11.6 meq/100 g soil d.w.
- Details on soil characteristics:
- The particle size distribution of the Sandy Loam is constituted by: 56% w/w of sand, 26% w/w of silt and 18% w/w of clay
The percentage of organic matter is 1.6% w/w .
The cation exchange capacity is 11.6 meq/100 g.
The Bulk density is 1.51 gm/cm3.
The total hardness is 264
The Sandy Loam Contains the following exchangeable cations: K (227 ppm), Mg (202 ppm) and Ca (1221 ppm).
The pH of Sandy Loam is 6.8
The water content at 0.33 bar is 17.37% w/w - Soil No.:
- #1
- Duration:
- 70 d
- Initial conc.:
- 10 mg/kg soil d.w.
- Based on:
- test mat.
- Parameter followed for biodegradation estimation:
- CO2 evolution
- Temp.:
- 25 ± 1°C
- Microbial biomass:
- was conducted on day 0 and 10 following aerobic initiation and at day 15 and 60 following anaerobic initiation.
- Details on experimental conditions:
- MATERIALs & METHODS
An anaerobic soil metabolism study with 14C-Piperonyl Butoxide (purity = 99.1 %) applied to a sandy loam soil from Ashland, Nebraska dosed at a nominal 10 µg/g rate was conducted. The study lasted 70 days in the dark in an environmental chamber regulated at 25 ± 1°C. Following one half-life (10 days), the aerobically aged samples were flooded with well water and purged with nitrogen to induce anaerobic conditions. Samples were taken at days 0, 1, 3, 7 and 10 following aerobic initiation and at days 15, 30, 45 and 60 following anaerobic initiation. Day 0 samples were analysed in duplicate. The radioactivity level of aqueous soluble and extractable 14C-residues was determined by LSC. Soil extracts were characterized for parent compound by TLC. The level of bound 14C-residues was determined by combustion radioanalysis of the post-extracted samples. Radioactivity in the trapping solutions was also analysed by LSC. Possible degradation products were analysed by HPLC (detection limit of < 0.3 %) and EI-MS for identification. The half-life of Piperonyl Butoxide for the aerobic and anaerobic incubation period was calculated by means of linear regression analysis. Furthermore the microbial analysis was conducted on day 0 and 10 following aerobic initiation and at day 15 and 60 following anaerobic initiation.
APPLICATION OF TEST ITEM
In the preliminary study sandy loam soil was dosed at a nominal 10 µg/g rate of 14C-Piperonyl Butoxide and incubated in an environmentally controlled chamber at 25 ± 1°C in the dark.
To 35 of the silanized culture tubes containing the study soil and water, 83 µL of a 1214 mg/L solution of 14C-Piperonyl Butoxide was added. The initial measured dose was 10.1 µg Piperonyl Butoxide equivalents/g soil. The remaining 16 sample tubes were not dosed and served as control. The samples, excluding the day 0 and stability samples, were placed into metabolism vessels within the environmental chamber. 14 control samples were placed in the control vessel, 14 dosed samples were placed in the Replicate I test vessel and 11 dosed samples were placed in the Replicate II test vessel.
DURATION OF TEST
10 days aerobic and 60 days anaerobic incubation period
TEMPERATURE/LIGHT
All tubes were maintained in the dark and at a temperature of 25 ± 1°C.
SAMPLING
Preliminary study samples were collected and analysed at 0, 4 and 10 days after aerobic initiation and 1, 4 and 7 days after anaerobic initiation. Trapping solutions were analysed on days 4 and 10 following aerobic initiation and on days 1, 4 and 7 following anaerobic initiation.
Test samples were collected for analysis at days 0, 1, 3, 7 and 10 following aerobic initiation and at days 15, 30, 45 and 60 following anaerobic initiation. Day 0 samples were analysed in duplicate. Appropriate analysis was conducted on each Replicate I sample. Replicate II samples were placed in a freezer at approximately -22°C. Trapping solutions were collected on the days that samples were removed. Microbial analysis was conducted on day 0 and 10 following aerobic initiation and at day 15 and 60 following anaerobic initiation.
After the removal of the day 10 aerobic samples, all remaining sample tubes were removed from their respective metabolism vessel. A 30 mL aliquot of well water and a 0.1 g aliquot of glucose were added to each tube and vortexed to remove any trapped air. The sample tubes were returned to their appropriate metabolism vessels in the environmental chamber and connected to traps for 14C-volatile degradates. The vessels were then flushed with nitrogen to induce anaerobic conditions.
Extraction
During the analysis of the anaerobic samples, each sample tube containing the soil and water samples was centrifuged for approximately 10 min at 2000 rpm. The water layer was decanted and, if necessary, the volume was adjusted to 30 mL. Triplicate 1.0 mL aliquots of the test water were analysed by LSC.
The soil was triplicate extracted with 15 mL methanol. After 30 min shaking, 10 min centrifuging and decanting the extracts were combined and, if necessary, adjusted to 45 mL. Triplicate aliquots at 1.0 mL were analysed by LSC. The soil was then extracted with 25 mL 0.1 M NaOH:methanol (3:1, v:v). The sample was shaken for 4 hours, centrifuged for 10 min and the re-extract was decanted. Then the soil was rinsed twice with 10 mL aliquot of 0.1 M NaOH:methanol (3:1, v:v) and again centrifuged for 10 min. The rinses were combined with the re-extract and adjusted to 50 mL. Triplicate aliquots at 1.0 mL were analysed by LSC.
For analysing the organic phase a 25 mL aliquot of the re-extract was transferred to a separate 50 mL culture tube. The pH was adjusted to 2.0 with the dropwise addition of 6 N HCl. Then the re-extract was partitioned into 2 phases by adding a 10 mL aliquot of ethyl acetate. The final volumes of both the organic and the aqueous phase were measured and triplicate 1.0 mL aliquots of both phases were analysed by LSC.
For analysing the non extractable 14C-residues, triplicate aliquots of post-extracted soil were combusted and analysed by LSC. Each trapping solution was analysed by triplicate 1.0 mL LSC analysis. - DT50:
- 10 d
- Type:
- not specified
- Remarks on result:
- other: T not specified
- Key result
- DT50:
- 144 d
- Type:
- not specified
- Remarks on result:
- other: when flooding occurs
- Transformation products:
- yes
- No.:
- #1
- Details on transformation products:
- AEROBIC AGING
In addition to the evolution of 14CO2, 3 possible degradation products were observed during TLC analysis of water and soil extracts. The only degradate exceeding 10 % of the applied radioactivity was definitely identified and named as Metabolite F (origin). This non-mobile 14C-residue at the origin of the TLC plate obtained a maximum concentration of 28.5 % at day 10. The identities of the other two degradation products that accounted for <5 % of the applied radioactivity were theorised based on relative polarities. According to it, the second degradate with a maximum concentration of 1.16 % at day 3 was supposed to be Intermediate II (Rf = 0.05) and the third degradate with a concentration of 3.76 % at day 10 was most probably Intermediate I.
ANAEROBIC AGING
In addition to the evolution of 14CO2, 4 possible degradation products were observed during TLC analysis of water and soil extracts. The only degradate exceeding 10 % of the applied radioactivity was definitely identified and named as Metabolite F. This non-mobile 14C-residue at the origin of the TLC plate obtained a maximum concentration of 27.9 % at day 10. Two of the remaining 3 degradations products that accounted for <5 % of the applied radioactivity were theorised based on relative polarities. According to it, the second degradate with a maximum concentration of 2.91 % at day 3 was supposed to be Intermediate II (Rf = 0.05) and the third degradate with a concentration of 4.12 % at day 10 was most probably Intermediate I (Rf = 0.1). A degradate having a maximum concentration of 2.16 % of the applied radioactivity could not be identified (Rf = 0.2).
The proposed degradation pathway of 14C-Piperonyl Butoxide:
Parent compound --> Intermediate I --> Intermediate II --> Metabolite F --> 14CO2 + non-extractable 14C-residues.
All results are listed in the table "Degradation of Piperonyl Butoxide" attached in background material.
The proposed degradation pathway of 14C-piperonyl butoxide during the anaerobic soil metabolism study is reported in the scheme "Proposed degradation pathway " attached in background material - Evaporation of parent compound:
- yes
- Volatile metabolites:
- yes
- Residues:
- yes
- Details on results:
- The results of the study have demonstrated that piperonyl butoxide undergoes microbial and/or chemical degradation under aerobic soil conditions to eventually mineralize to CO2 (t½ = 10.0 days). However, the degradation rate is reduced when flooding occurs and anaerobic conditions are induced (t½ = 144 days).
RECOVERY
The mean 14C-mass accountability for the study was 96.1 % based on the percent of initial 14C-residues measured following dosing.
MINRALIZATION
Just a small amount of 14C-volatiles evolved during the study and could be trapped (aerobic: 1.45 % at day 10, anaerobic: 1.57 % at day 60). The majority of 14C-volatiles generated (98-99 %) were trapped in the KOH traps and could be confirmed to be 14CO2.
IDENTIFICATION of RADIOACTVITY
Based on TLC analysis of the aerobic soil samples, parent compound accounted for 48.6 % of the applied radioactivity at day 10. Parent compound of the anaerobic soil samples accounted for 35.2 % of the applied radioactivity at day 60 confirmed by HPLC.
As non-extractable 14C-residues obtained concentrations of >10% of the applied radioactivity, an organic matter fractionation analysis of the day 10 (aerobic) and day 60 (anaerobic) samples was conducted. The majority were observed in the fulvic acid fraction.
DEGRADATION KINETICS
The half-life of Piperonyl Butoxide under aerobic and anaerobic conditions was calculated to be 10 days and 144 days, respectively. The kinetic constant for the degradation of the parent compound was obtained by means of a linear regression analysis.
aerobic conditions: y = 4.66-0.0693x, r = 0.966
anaerobic conditions: y = 3.81-0.00481x, r = -0.876
MICROBIAL VIABILITY
The bacterial and fungal plate count analysis indicated that the microbial viability was sufficient throughout the study. - Conclusions:
- The results of the study have demonstrated that Piperonyl Butoxide undergoes microbial and/or chemical degradation under aerobic soil conditions to eventually mineralize to CO2 (half-life: 10 days). The degradation rate is reduced when flooding occurs and anaerobic conditions are induced (half-life: 144 days).
Reference
Parent compound: Based on TLC analysis of the aerobic soil samples, parent compoundaccounted for 48.6 % of the applied radioactivity at day 10. Parent compound of the anaerobic soil samples accounted for 35.2 % of the applied radioactivity at day 60 confirmed by HPLC.
Non-extractable residues
As non-extractable 14C-residues obtained concentrations of >10% of the applied radioactivity, an organic matter fractionation analysis of the day 10 (aerobic) and day 60 (anaerobic) samples was conducted. The majority were observed in the fulvic acid fraction.
Description of key information
Aerobic soil degradation: a normalised geometric mean value of 58.3 days should be considered for risk assessment purposes.
Anaerobic soil degradation: a DT50of 144 days has been calculated.
Key value for chemical safety assessment
- Half-life in soil:
- 58.3 d
Additional information
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