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EC number: 947-999-8 | CAS number: -
- 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
Endpoint summary
Administrative data
Description of key information
No studies were available on the aquatic toxicity of the test substance. Therefore, read across is performed using studies from the related substance benzenesulfonic acid (LABS Na).
Short-term aquatic toxicity
Fish
Two studies are presented to characterize the potential short-term aquatic toxicity to fish of LABS Na. In a 96-hour acute toxicity study (key study), bluegill sunfish (Lepomis macrochirus) were exposed to LABS Na under static conditions. The measured concentrations were 79 % of nominal concentrations but were not reported. The 96-hour LC50 value, based on measured concentrations, was 1.67 mg a.i./L. In a second study, 48-hour acute toxicity tests with fathead minnows (Pimephales promelas) were conducted on high molecular weight LAS, individual pure homologues, non-linear LAS components (dialkyl tetralin or indane sulfonates, DTIS), and model biodegradation intermediates (sulfophenylundecane, SOU) in order to determine whether biodegradation decreases toxicity. All of the toxicity tests were conducted in 5 L of 100 mg/L hardness water using 5 fathead minnows per concentration. Results indicated that the length of the alkyl chain is the most important factor influencing acute toxicity, which increases as the alkyl chain increases. These longer alkyl chain homologues are the first constituents of the LABS Na mixture to degrade. The nonlinear components (DTIS) showed 1/2 to 1/10 the toxicity of LABS Na with the same carbon chain length. Therefore, toxicity of biodegradation intermediates is significantly less than the parent LABS Na.
Aquatic invertebrates
Five studies characterize the potential for short-term toxicity to aquatic invertebrates using LABS Na. In the key study used for chemical safety assessment (Hooftman and van Drongelen-Sevenhuijsen 1990),Daphnia magnawere exposed for 48 hours to LABS Na at nominal concentrations of 0 (Control), 3.2, 5.6, 10, 18, 32, 56 and 100 mg/L under static conditions. The sample was 12.1% active ingredient, and results were adjusted to the active ingredient basis. The resultant 48-h EC50value based on mobility was 2.9 mg a.i./L. Three additional aquatic invertebrate studies are available, all with EC50 values greater than 2.9 mg/L. In the fifth study (Kimerle and Swisher 1977), the toxicity of high molecular weight LABS Na, individual LABS Na homologues, and nonlinear LABS Na components (DTIS) was measured in a series of aquatic toxicity tests withDaphnia magna. Results show that biodegradation of LABS Na influences the toxicity, with the remaining LABS Na becoming less toxic, confirming the results of the study (above) with fathead minnows.
Aquatic algae and cyanobacteria
Four studies characterize the potential for short-term toxicity to aquatic algae using LABS Na. The study of Muehlberg et al. (1984) obtained a 15 day LOEC of 10 mg/L for the algae Chlorella kessleri. Ward et al. (1982) obtained a 96 hour EC50 of 0.91 mg/L for the cyanobacterium Microcystis aeruginosa. Lewis al. (1986) obtained a 96 hour EC50 of 29 mg/L for the algae Pseudokirchneriella subcapitata. Scholz al. (1992) obtained a 72 hour ErC50 of 127.9 mg/L for the algae Desmodesmus subspicatus.
Long-term aquatic toxicity
Fish
Five fish studies are presented to characterize the potential long-term aquatic toxicity to fish of LABS Na. In the first study (Pickering and Thatcher 1970), fathead minnows were exposed to concentrations of 0.34, 0.63, 1.2 and 2.7 mg/L LABS Na in continuous flow systems for a total of 196 days. Results indicate that lethality of LABS Na to newly hatched fry was the most critical factor found. The 196 day NOEC level was 0.63 mg/L. In a second study (Chattopahyay and Konar 1985), the long-term toxicity of LABS Na to fish was determined usingTilapia mossambica(tilapia). Groups of 15 fish were exposed to concentrations of 0.0, 0.25, 0.38, 0.51, and 1.10 mg/L for 90 days. Based on the most reliable endpoints (GSI and fecundity), the NOEC would be 0.38 mg/L and the LOEC would be 0.51 mg/L. However, in view of certain reporting limitations as described in the dossier, and the fact that previous evaluations of this study have reported a NOEC of 0.25 mg/L (van de Plassche et al., 1999), a conservative (protective) NOEC for this study is considered to be 0.25 mg/L. In the third long-term study (Canton and Slooff 1982), groups of 50 guppies (Poecilia reticulata) were exposed to various concentrations of LABS Na for 28 days. The only effect (98% mortality at 10 mg/L) occurred within 2 days of study initiation .The 28-day NOEC normalized by van de Plassche et al. (1999) to C11.6LABS Na was 3.2 mg/L.
In the study of Marshall (2010) fertilized eggs of rainbow trout (Oncorhynchus mykiss, formerlySalmo gairdneri) were exposed to mean measured concentrations of 0.03, 0.23, 0.35, 0.63, 0.95 and 1.9 mg/L, for 72 days. The responses recorded included the survival of eggs, time to eyed egg stage, time to hatch, survival and final weight of sac-fry (eleutheroembryos), and time and extent of swim-up (external feeding). The lowest NOEC value found was 0.23 mg/L based on survival of eggs exposed from eyed stage, survival of eggs exposed from fertilization, survival of sac fry, and overall survival from fertilization to swim-up. The data are for C11.6LABS Na and no normalization is required. Finally, a long term toxicity test to juvenile bluegills (Lepomis macrochirus) was conducted on C12LABS Na (Maki 1981). Fish growth was determined after 28 days exposure in a flow-through model ecosystem to measured concentrations of 0, 0.5, 1.0, 2.0, and 4.0 mg/L. Results showed that the growth of juvenile bluegills was not affected at 0.5 and 1.0 mg LABS Na /L, but was reduced at 2.0 and 4.0 mg/L. At the end of the exposure period, fish at 1.0 mg/L LABS Na had a biomass of 44 gm/m2compared to 10.5 gm/m2for the 2.0 mg/L concentration. Based on these effects on growth rate, the NOEC was 1.0 mg/L.
Aquatic invertebrates
In the first study (Maki 1977), the toxicity of C11.8LABS Na was evaluated in a 21-day survival and reproduction test withDaphnia magna. Mean measured concentrations were 0.32, 0.59, 1.18, 2.52, and 4.85 mg/L C11.8LABS Na as active ingredient. Results, based on the mean measured concentration of the active ingredient, indicate that the 21-day NOEC was 1.18 mg/L. The 21-day LC50was 1.67 mg/L, while the EC50s, based on total young production, average brood size, and percent days reproduction occurred, were 1.50, 2.30, and 2.31 mg/L, respectively. These results were then normalized to a C11.6LABS Na according to the methods of van de Plassche et al. (1999), and the final NOEC value is 1.41 mg/L. In the second study (Taylor 1984), a 7-day chronic toxicity test on C11.8LABS Na was conducted withCeriodaphniasp. under semi-static conditions. Ceriodaphniawere fed either a yeast diet, or an algae/trout chow diet. Nominal test concentrations were 0, 0.5, 1, 2, 3.5, 5 and 7 mg/L of active ingredient. The 7-day NOEC for the yeast diet was 0.5 mg/L (based on reproduction) while the 7-day NOEC for the algae/trout chow diet was 5 mg/L (based on mortality and reproduction). When normalized to a C11.6LABS Na, the lowest NOEC is 0.59 mg/L. In the third study (Maki 1981), effects on the midge were examined. Groups ofP. parthenogenicawere exposed for 28 days to concentrations of 0.5, 1.0, 2.0, or 4.0 mg/L (nominal) of LABS Na. The LOEC was 4 mg/L based on survival and reproduction, and the NOEC was 2.0 mg/L. When normalized to C11.6LABS Na, the NOEC value becomes 2.8 mg/L. The chronic toxicity of C12.3 LABS Na was evaluated in a 2-day whole life cycle bioassay the rotifer,Brachionus calyciflorus(Procter & Gamble 1996). Six newly hatched rotifers (<3 hours old) were placed in each replicate beaker, and exposed to C12.3 LABS Na for 48 hours. Results were based on the total number of live, swimming organisms (both adults and offspring) and measured concentrations. The resultant EC10value was 1.18 mg a.i./L, the EC20was 1.4 mg a.i./L, and the EC50was 2.0 mg a.i./L. When normalized to a C11.6LABS Na, the EC10value becomes 1.69 mg/L. Finally, the chronic toxicity of C12LABS Na was determined in a 32-day test (van de Plassche et al 1999) with three aquatic invertebrates (Corbicula, Elimia, Hyalella). The invertebrates were caged in the tail pools of an environmental stream mesocosm study of C12LABS Na. Toxicity was based on water concentrations at which adverse effects were observed. Results were also calculated based on the tissue concentrations at which adverse effects were observed. All invertebrates were exposed to nominal concentrations of 0, 0.15, 0.30, 1.0, and 3.0 mg a.i./L. As mean measured concentrations were 84-99% of nominal, results are based on measured concentrations. On days 0, 8, 16, and 32, the invertebrates were examined for growth and survival. The results can be summarized as follows (all normalized to C11.6): ForCorbicula, the 32 day EC20was 0.39 mg/L based on growth (length), forElimina, the 32 day NOEC was 4.15 mg/L based on survival and forHyalellathe 24 day EC20was 1.36 mg/L based on survival.
Aquatic algae and cyanobacteria
Three studies characterize the potential for long-term toxicity to aquatic algae using LABS Na. The study of Muehlberg et al. (1984) obtained a 15 day NOEC of 3.1 mg/L for the algae Chlorella kessleri. Lewis al. (1986) obtained a 96 hour NOEC of 0.5 mg/L for the algae Pseudokirchneriella subcapitata. Scholz al. (1992) obtained a 72 hour NOEC of 2.4 mg/L for the algae Desmodesmus subspicatus.
Toxicity to aquatic plants other than algae
Two aquatic plant (other than algae) studies were conducted using LABS Na. In the first study (Maki 1981), the long term toxicity of C11.6LABS Na to the aquatic plant (Elodea canadensis) was determined in a 28 day model ecosystem test. The nominal test concentrations were 0.5, 1.0, 2.0, and 4.0 mg/L, and were confirmed by analytical measurements. Growth inhibition was not observed even at the highest tested concentration (4 mg/L). Growth throughout the exposure period approximately doubled the initial biomass of the vegetative shoots used at the start of the exposure. Hence, the NOEC was found to be>4 mg/L. The data are for C11.6 LABS Na and no normalization is required. In the second study (Bishop and Perry 1981; Bishop 1980; van de Plassche et al 1999), the duckweed,Lemna minor, was exposed to C11.8 LABS Na. Endpoints included frond count, dry weight, growth rate, and root length after a 7 day exposure period in a flow through study. The measured test concentrations were 0, 2.1, 3.8, 8, 17 and 34 mg/L. The resultant EC10value, based on frond number, was 0.21 mg/L. The EC50value, also based on frond number, was 2.30 mg/L C11.8 LABS Na. Normalizing the EC10of 0.21 mg/L to C11.6 LABS Na results in a final value of 0.30 mg/L.
Toxicity to microorganisms
No data on the target substance is available for the endpoint toxicity to micro-organisms because testing was technically not feasible. As the substance is expected to be highly insoluble in water, toxicity is considered unlikely and therefore the toxicity to micro-organisms study does not need to be conducted. The target substances are used as an additive in formulated lubricant oils. Strict risk management measures are in place to ensure that the substance or product is not released to the environment, including no discharge to STP.
Additional information
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