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EC number: 214-968-9 | CAS number: 1229-55-6
- 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 water and sediment: simulation tests
Administrative data
Link to relevant study record(s)
- Endpoint:
- biodegradation in water: sediment simulation testing
- Type of information:
- experimental study
- Adequacy of study:
- key study
- Reliability:
- 2 (reliable with restrictions)
- Rationale for reliability incl. deficiencies:
- other: Data is from peer reviewed journal
- Justification for type of information:
- Data is from peer reviewed journal
- Qualifier:
- according to guideline
- Guideline:
- other: as mentioned below
- Principles of method if other than guideline:
- Biodegradation in water and sediment study was carried out for determing the half-life of test chemical 1-[(2-methoxyphenyl)azo]-2-naphthol.
- GLP compliance:
- not specified
- Specific details on test material used for the study:
- - Name of test material: 1-[(2-methoxyphenyl)azo]-2-naphthol
- Common name: Solvent Red 1
- Molecular formula: C17H14N2O2
- Molecular weight: 278.31 g/mol
- Smiles notation: c12c(\N=N\c3c(cccc3)OC)c(ccc1cccc2)O
- InChl : 1S/C17H14N2O2/c1-21-16-9-5-4-8-14(16)18-19-17-13-7-3-2-6-12(13)10-11-15(17)20/h2-11,20H,1H3/b19-18+
- Substance type: Organic
- Physical state: solid - Radiolabelling:
- not specified
- Oxygen conditions:
- anaerobic
- Inoculum or test system:
- other: Lake water
- Details on source and properties of sediment:
- - Details on collection (e.g. location, sampling depth, contamination history, procedure): Sediments were obtained from 2 different lakes (i.e, Herrick and Kingfisher) near Athens, GA.
- Storage conditions: The sieved sediment (5-15 cm deep) was stored in the dark, under lake water, in sealed, 2-gal glass or plastic bottles until used.
- Storage length: The sieved sediment (5-15 cm deep) was stored until used.
- Organic carbon (%): Organic carbon content of sediments was determined at the University of Georgia Soil Testing Laboratory by the Walkley-Black method and by three other combustion methods, including that of Lee and Macalady. In general, the methods gave comparable results.
The percent organic carbon for each lake sediment was as follows: Beef Pond, 3.05 ± 14% (n =9); Herrick, 1.52 :l:
56% (n = 31); KingfIsher, 7.46:l: 45% (n = 10); Oglethorpe, 1.99 :l: 48% (n =7).
- Sediment samples sieved: Yes, sediments were scraped from the top few centimeters of the lake bottom at a water depth of less than about 50 cm and sieved, at the lake, through a 0.5 mm sieve. - Initial conc.:
- > 10 - < 98 other: mg/kg
- Based on:
- test mat.
- Initial conc.:
- > 10 - < 23 other: mg/kg
- Based on:
- test mat.
- Parameter followed for biodegradation estimation:
- other: HPLC and GC
- Key result
- Compartment:
- other: sediment
- DT50:
- 4 d
- Type:
- (pseudo-)first order (= half-life)
- Remarks on result:
- other: Sediment was obtained from Herrick lakes.
- Key result
- Compartment:
- other: sediment
- DT50:
- 2.2 d
- Type:
- (pseudo-)first order (= half-life)
- Remarks on result:
- other: Sediment was obtained from Kingfisher lakes.
- Other kinetic parameters:
- other: For all kinetic experiments, rate constants for dye loss, kL, was obtained as slope of a regression of logarithm dye concentration versus time.
- Transformation products:
- yes
- No.:
- #1
- No.:
- #2
- Details on transformation products:
- Products of the azo dye, SR 1, were expected to be o-anisidine and 1-amino-2-naphthol resulting from reductive cleavage of the azo bond. However, these compounds could not be identified by HPLC because they coeluted. After GPC cleanup, each product was detected by GC-MS with both spectra and retention times identical to those of purchased materials.
- Evaporation of parent compound:
- not specified
- Volatile metabolites:
- not specified
- Residues:
- not specified
- Validity criteria fulfilled:
- not specified
- Conclusions:
- The half-life value of test chemical 1-[(2-methoxyphenyl)azo]-2-naphthol in sediment obtained from 2 different lakes (i.e, Herrick and Kingfisher) was determined to be 4.0 and 2.2 days with an average first order rate constant of 7.2 × 10-3 and 1.3 × 10-2, respectively.
- Executive summary:
Biodegradation in water and sediment study was carried out for determining the half-life of test chemical 1-[(2-methoxyphenyl)azo]-2-naphthol (CAS no 1229 -55 -6) under anaerobic conditions. Sediments were obtained from 2 different lakes (i.e, Herrick and Kingfisher) near Athens, GA. The sieved sediment (5-15 cm deep) was stored in the dark, under lake water, in sealed, 2-gal glass or plastic bottles until used.Organic carbon content of sediments was determined at the University of Georgia Soil Testing Laboratory by the Walkley-Black method and by three other combustion methods, including that of Lee and Macalady.Ingeneral, the methods gave comparable results. The percent organic carbon for each lake sediment was as follows: Beef Pond, 3.05 ± 14%(n=9); Herrick, 1.52 :l:56% (n=31); KingfIsher, 7.46:l: 45%(n=10); Oglethorpe, 1.99 :l: 48%(n=7). Sediments were scraped from the top few centimeters of the lake bottom at a water depth of less than about 50 cm and sieved, at the lake, through a 0.5 mm sieve.The desired amount of sediment (based on wet weight and moisture content of filter cake) in lake water was sealed and allowed to remain quiescent for 2-4 days prior to dye addition. During dye addition (in ACN) and mixing, the sediment was maintained under N2 until placement in 20-mL scintillation vials. No attempt was made to measure redox potentials in the compacted sediment of either kinetic or product studies. However, under the study conditions, the reddish Georgia clay sediment quickly became the light gray color that is characteristic of reducing environments.Vials were sacrificed for analysis by shaking, sonicating, and filtering. To a portion of the filter cake was added a volume of ACN equal to twice the sediment moist weight. The vial was then shaken and sonicated and the slurry was filtered.Test chemical was identified by analytical methods such as HPLC and GC. For all kinetic experiments, rate constants for dye loss,kL,were obtained as the slope of a regression of the logarithm of dye concentration versus time.Products of the azo dye, SR 1, were expected to be o-anisidine and l-amino-2-naphthol resulting from reductive cleavage of the azo bond. However, these compounds could not be identified by HPLC because they coeluted. After GPC cleanup, each product was detected by GC-MS with both spectra and retention times identical to those of purchased materials.The half-life value of test chemical 1-[(2-methoxyphenyl)azo]-2-naphthol in sediment obtained from2 different lakes (i.e, Herrick and Kingfisher) was determined to be 4.0 and 2.2 days with an average first order rate constant of 7.2 × 10-3and 1.3 × 10-2, respectively. Based on this half-life value, it indicates that 1 -[(2 -methoxyphenyl)diazenyl]-2 -naphthol is not persistent in sediment.
Reference
Control studies showed recoveries· to be both high (>90%) and reproducible (±10%).
Table: Kinetic Data for chemicalin Sediment-Water Systems.
Dye |
sediment |
D0b(mg/kg) |
Di/D0e |
K (h-1)d |
ne |
T1/2 (days) |
SR1 |
H
K |
10-98
10-23 |
1.3
0.8 |
7.2 × 10-3[62] 1.3 × 10-2 [78] |
3
7 |
4.0
2.2 |
Where,
H = sediment from Herrick
K = sediment from Kingfisher
b = initial dye concentration or range
d = Average first order rate constant and coefficient of variation [ ].
e = No. of range constants
f = Half-life
Description of key information
Biodegradation in water and sediment study was carried out for determining the half-life of test chemical 1-[(2-methoxyphenyl)azo]-2-naphthol (CAS no 1229 -55 -6) under anaerobic conditions (George L. Baughman and Eric J. Weber, 1994). Sediments were obtained from 2 different lakes (i.e, Herrick and Kingfisher) near Athens, GA. The sieved sediment (5-15 cm deep) was stored in the dark, under lake water, in sealed, 2-gal glass or plastic bottles until used. Organic carbon content of sediments was determined at the University of Georgia Soil Testing Laboratory by the Walkley-Black method and by three other combustion methods, including that of Lee and Macalady.Ingeneral, the methods gave comparable results. The percent organic carbon for each lake sediment was as follows: Beef Pond, 3.05 ± 14%(n=9); Herrick, 1.52 :l:56% (n=31); KingfIsher, 7.46:l: 45%(n=10); Oglethorpe, 1.99 :l: 48%(n=7). Sediments were scraped from the top few centimeters of the lake bottom at a water depth of less than about 50 cm and sieved, at the lake, through a 0.5 mm sieve.The desired amount of sediment (based on wet weight and moisture content of filter cake) in lake water was sealed and allowed to remain quiescent for 2-4 days prior to dye addition. During dye addition (in ACN) and mixing, the sediment was maintained under N2 until placement in 20-mL scintillation vials. No attempt was made to measure redox potentials in the compacted sediment of either kinetic or product studies. However, under the study conditions, the reddish Georgia clay sediment quickly became the light gray color that is characteristic of reducing environments.Vials were sacrificed for analysis by shaking, sonicating, and filtering. To a portion of the filter cake was added a volume of ACN equal to twice the sediment moist weight. The vial was then shaken and sonicated and the slurry was filtered.Test chemical was identified by analytical methods such as HPLC and GC. For all kinetic experiments, rate constants for dye loss,kL,were obtained as the slope of a regression of the logarithm of dye concentration versus time.Products of the azo dye, SR 1, were expected to be o-anisidine and l-amino-2-naphthol resulting from reductive cleavage of the azo bond. However, these compounds could not be identified by HPLC because they coeluted. After GPC cleanup, each product was detected by GC-MS with both spectra and retention times identical to those of purchased materials.The half-life value of test chemical 1-[(2-methoxyphenyl)azo]-2-naphthol in sediment obtained from2 different lakes (i.e, Herrick and Kingfisher) was determined to be 4.0 and 2.2 days with an average first order rate constant of 7.2 × 10-3and 1.3 × 10-2, respectively. Based on this half-life value, it indicates that 1 -[(2 -methoxyphenyl)diazenyl]-2 -naphthol is not persistent in sediment.
Key value for chemical safety assessment
- Half-life in freshwater sediment:
- 4 d
Additional information
Biodegradation in water and sediment study was carried out for determining the half-life of test chemical 1-[(2-methoxyphenyl)azo]-2-naphthol (CAS no 1229 -55 -6) under anaerobic conditions (George L. Baughman and Eric J. Weber, 1994). Sediments were obtained from 2 different lakes (i.e, Herrick and Kingfisher) near Athens, GA. The sieved sediment (5-15 cm deep) was stored in the dark, under lake water, in sealed, 2-gal glass or plastic bottles until used.Organic carbon content of sediments was determined at the University of Georgia Soil Testing Laboratory by the Walkley-Black method and by three other combustion methods, including that of Lee and Macalady.Ingeneral, the methods gave comparable results. The percent organic carbon for each lake sediment was as follows: Beef Pond, 3.05 ± 14%(n=9); Herrick, 1.52 :l:56% (n=31); KingfIsher, 7.46:l: 45%(n=10); Oglethorpe, 1.99 :l: 48%(n=7). Sediments were scraped from the top few centimeters of the lake bottom at a water depth of less than about 50 cm and sieved, at the lake, through a 0.5 mm sieve.The desired amount of sediment (based on wet weight and moisture content of filter cake) in lake water was sealed and allowed to remain quiescent for 2-4 days prior to dye addition. During dye addition (in ACN) and mixing, the sediment was maintained under N2 until placement in 20-mL scintillation vials. No attempt was made to measure redox potentials in the compacted sediment of either kinetic or product studies. However, under the study conditions, the reddish Georgia clay sediment quickly became the light gray color that is characteristic of reducing environments.Vials were sacrificed for analysis by shaking, sonicating, and filtering. To a portion of the filter cake was added a volume of ACN equal to twice the sediment moist weight. The vial was then shaken and sonicated and the slurry was filtered.Test chemical was identified by analytical methods such as HPLC and GC. For all kinetic experiments, rate constants for dye loss,kL,were obtained as the slope of a regression of the logarithm of dye concentration versus time.Products of the azo dye, SR 1, were expected to be o-anisidine and l-amino-2-naphthol resulting from reductive cleavage of the azo bond. However, these compounds could not be identified by HPLC because they coeluted. After GPC cleanup, each product was detected by GC-MS with both spectra and retention times identical to those of purchased materials.The half-life value of test chemical 1-[(2-methoxyphenyl)azo]-2-naphthol in sediment obtained from2 different lakes (i.e, Herrick and Kingfisher) was determined to be 4.0 and 2.2 days with an average first order rate constant of 7.2 × 10-3and 1.3 × 10-2, respectively. Based on this half-life value, it indicates that 1 -[(2 -methoxyphenyl)diazenyl]-2 -naphthol is not persistent in sediment.
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