Registration Dossier
Registration Dossier
Diss Factsheets
Use of this information is subject to copyright laws and may require the permission of the owner of the information, as described in the ECHA Legal Notice.
EC number: 500-209-1 | CAS number: 68412-54-4 1 - 2.5 moles ethoxylated
- 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)
Description of key information
Studies in sludge-amended soils suggest that NPEO degrades in soil under aerobic conditions, partly mineralising and partly resulting in formation of NP. Anaerobic conditions slow down or impede breakdown in the soil. Studies on NP show that it may persist in landfills under anaerobic conditions; however, it does not appear to be persistent in soil under aerobic conditions. The half-life of NP in soil depends on parameters such as environmental conditions, isomer profile and the type of soil (Environment Canada, 2001; JRC, 2002).
Key value for chemical safety assessment
Additional information
Concentrations of NP, NPE-1 and NPE-2 were followed in sludge-amended soil. The soil samples were collected from the upper 5 cm of planted grassland from an experimental plot in Liebefeld, Switzerland. This site was part of a long-term field study and had received anaerobically digested sludge at an average application rate of 13.5 tonnes/ha year (dry weight) since 1976. The sludge was applied to the surface soil as a liquid spread, 4-6 times per year. During the morning of 16 May 1986, 2.5 t/ha of sludge were spread over the experimental plot. A few hours after application, the first samples were collected. The initial concentrations of NP, NPE-1 and NPE-2 in the amended soil were 4.7, 1.1 and 0.1 mg/kg dry weight (dw), respectively. These rapidly decreased to 20% of their initial levels during the first 3 weeks. In an additional 70 days, a level was reached that remained constant during the next 130 days. The residual mean concentrations of NP, NPE-1 and NPE-2 in soil 320 days after test start were 0.5, 0.12 and 0.01 mg/kg dw, respectively (Marcomini et al.,1989).
The mineralization of 14C-labelled NPE-2 was investigated in different domestic wastewater treatment plant sludge-soil mixtures and soils (coarse-sandy / sandy / clayey) collected in Denmark. Experiments were conducted with 6 g wet weight samples in glass tubes maintained at 40 – 80% water holding capacity (WHC) and 15°C in the dark for 2 months. The presence of oxygen was the most important parameter determining mineralisation of the substances. NP and NPE-2 were rapidly mineralised in aerobic sludge-soil mixtures while only a minor part was mineralised in sludge dominated by anaerobic conditions. Mineralization of NP and NPE-2 was not affected by the soil type since the percentage of compound mineralized (49.7 – 63.7 and 55.2 – 64.4%, respectively) after two months was not different between any of the test mixtures (Gejlsbjerg et al., 2001).
The degradation of an NPE-1/NPE-2 mixture (2, 60 and 308 mg/L) in landfilled sludge receiving anaerobic digestor sludge from a pulp plant and landfilled municipal solid waste (Sweden) was determined under methanogenic conditions for 150 days. The inocula were incubated in 123 ml bottles at 30 or 37°C. In both inocula, at a concentration of 2 mg/L, the added NPE-1/NPE-2 was transformed to NP by anaerobic microorganisms. The background level of NP in the landfilled municipal solid waste was so high that a transformation of NPE-1/NPE-2 only increased the indigenous NP concentration by 5-10%. Significant decrease of NPE-1 and NPE-2 was observed within 22 days. An increase to 81% during 53 days was observed in samples with landfilled sludge. At a concentration of 60 mg/L NPE-1/NPE-2, approximately 20% NP was formed during 40 (landfilled municipal solid waste) and 80 days (landfilled sludge). The concentration of formed NP remained constant until Day 150. At 308 mg/L, less than 1% of the added NPE-1/NPE-2 was transformed into NP (Ejlertsson et al., 1999).
Microcosm experiments were conducted to evaluate the mineralization of 14C-labelled NP, NPE-4 and NPE-9 in a soil/biosolids (99.5:0.5 w/w) environment planted with crested wheatgrass (Agropyron crestatum). The column microcosms (7.5 x 36 cm) were located in a greenhouse with a 18:6-h light:dark photoperiod and a day/night temperature of 20±1/16±1°C. Soil moisture was maintained at 60 – 80% of field capacity. Experimental duration was 150 days. The biosolids, containing approximately 1,000 mg/kg NP, were obtained from a treatment plant receiving industrial, commercial and domestic wastewater. Three inital nominal concentrations (6, 24, 47 mg/kg dw) of NP, NPE-4 and NPE-9 were tested. Unplanted and soil-poisoned controls were run in parallel. In viable soils, 6-10% of NP, 12-29% of NPE-4 and 17-28% of NPE-9 mineralized to14CO2 within 150 days. The final percent of mineralisation was not significantly affected by difference in the initial concentrations of the substances in the soil/biosolids mixture. No statistical difference was shown between planted and unplanted systems (Dettenmaier E and Doucette WJ, 2007).
Information on Registered Substances comes from registration dossiers which have been assigned a registration number. The assignment of a registration number does however not guarantee that the information in the dossier is correct or that the dossier is compliant with Regulation (EC) No 1907/2006 (the REACH Regulation). This information has not been reviewed or verified by the Agency or any other authority. The content is subject to change without prior notice.
Reproduction or further distribution of this information may be subject to copyright protection. Use of the information without obtaining the permission from the owner(s) of the respective information might violate the rights of the owner.
