Sumformula of the chemical C27H42C1N02H20
Use Pesticide; antiseptic; cationic Uetergent.
121 -54-0 Degradation point, °C
LC5O values to fishes
246
>10000 (MITI 1992) 156 (MITI 1992) 0.31 (MITI 1992)
98-10-2
Total degradation in water
Bioconcentration factor, fishes
Other information about bioaccuniulation
LC5O values 10 fishes, mg/I
Molecular weight
Log octanol/water coefficient, Iog Pow
Total degradation in water
158.17
-2.25 calculated Biodegradation:
87% by BOD period: 14d substance: 100 mg/I sludge: 30 mg/I (MIII 1992).
Confirmed to he biodegradable (Anon. 1987).
Biodegradation: decomposition by a soil microflora: 16 days (Verschueren 1983).
Environment Guide 71
Benzet
State and appearance Colourless, odourless piates, very biifer taste.
Odour Odourless.
Molecular weight 466.1
Melting point, °C 164—166
Other information about Biodegradation: at 18 mg/I no degradation after 28 days by nonadapted sewage
degradation (Verschueren 1983).
Health effects Man: highly toxic by ingestion; 1 gram may be fatal (Verschueren 1983).
Effects on microorganisms Bacteria: Staphylococcus aureus: at 20 mg/l bacteriolytic action after 1 hour;
bacteria isolated from Phone fFrance) water: at 20 mg/l no significant reduction of growth rate (Verschueren 1983).
LC5O values to crustaceans, 70 96hr, Penaeus californiensis (Hanks 1976) mg/I
LC5O values to fishes, mg/I 1.6 96hr, Pimephales promelas 1.4 96hr, Lepomis macrochirus (Surber & Pickering 1962)
53 96hr, Oncorhynchus kisutch (Verschueren 1983)
243
•Benzidine
92-87-5Synonyms p, p’-Bianiline
4,4’-Diaminobiphenyl Sumformula of the chemical Cl 2H1 2N2
Use Organic synthesis; manufacture of dyes.
State and appearance Grayish-yellow, white or reddish gray crystalline powder.
Molecular weight 184.23
Specific gravity (water=1) 1.25 at 20/4 °C Vapour density (air=1) 6.36
Density,kg/m3 1250 20°C
Water solubility,mgII 400 at 12 C 9400 atlOO°C
Melting point, °C 116—129
Boiling point, °C 402
Log octanol/water coefficient, 1.37 (Anon. 1989)
Iog Pow 1.81
Mobility Theoretical distribution:
>91% in water, the rest in sediment and soil (Nordic 1988).
Other reactions in Probable reactions in air: photo lysis and oxidation with ozone.
atmosphere Estimated half-life approximately 1 day (Radding et al. 1975).
Total degradation in soil 80% reduction aifer 4 weeks incubation in soil (Lu et al. 1977).
Degradation ways: methylation, acetylation in microbial degradation in soil (Lu et al. 1977).
Total degradation in water Degradation in soil-enzymes, photochemical, tree radicals.
Half-life in water: approximately 100 days (Radding 1975).
152 Environment Guide 71
Benzid
Other information about Possible biooxidation products scanned by GCIMS:
degradation N-hydroxybenzidine; 3-hydroxybenzidine;
4-amino-4’-nitrobiphenyl; N,N’-dihydroxybenzidine; 3,3’-dihydroxybenzidine;
4,4’-dinitrobjphenyl (Verschueren 1983).
Not easjly degradable (Rudoph & Boje 1988).
Benzidinedihydrochloride is more persistent than benzidine (Bowman et al.
1976).
Actrvated, aerated active sludge promotes degradation of benzid jne (Tabak &
Barth 1978).
85—93% reduction ot 20 mgIl benzjd jne after 6 hours at 20 C in biological aero bic wastewater treatment process (Baird et al. 1977).
flegradation products of special interest:
Acetyle derjvate ot benzjdine (microbial degradation, metabolites); colouring agents based on benzjdjne degrade to benzjdine; wjth chlorinatjon of benzidine in water forms degradation products ot chloroam jne type (IARC 1982, Lu et al.
1977, Jenkins & Bajrd 1975).
Other information about Fastly absorbed (USEPA 1 980d).
metabolism
3-hydroxybenzidine(80—90%),diacetylbenzidine (5—10%), monoacetylbenzidine (1—5%) and benzjdjne is detected in urine (IARC 1982).
Bioconcentration factor, 55 Gambusia (Lu et al. 1977) fishes
38—44 Lepomis, 42d (EG & Bjonomjcs 1975) Bioconcentration factor, 290 Daphnia (Lu et al. 1977)
crustaceans
Bioconcentration factor, algae 2620 Oedogonium (Lu et al. 1977) Bioconcentration factor, other 650 Physa (Lu et al. 1977) organisms
LD5O values to mammais in 1570 ori-rat (Marhold et al.1968) oral exposure,mglkg
Carctnogenicity Garcinogenicity: positive (McCann et al. 1975).
Colouring agents based on benzidjne induces cancer in rats and people, at the same tjme as benzjd jne is detected jn urine (IARC 1982).
Acetyle derivate ot benzjdine jnduces cancer in test animais and are mutagen jn Ames test wjth metabolic activation (IARC 1982).
Mutagenicity Mutagenicity iii the Salmonella test: positive;
1.4 revertant colonies/nmol
265 revertant colonjes at 0.050 mg/plate (McCann et al. 1975).
Mutagen in Ames test when metabolic actjvation js present (Fishbein 1984).
Mutagenic effects in Drosophila melanogaster (Fahmy & Fahmy 1977).
Chromosome changes in people exposed at work (Bassendowska-Karska 1980).
LC5O values to crustaceans, >20 96hr, Gammarus (USEPA 1 980d) mg/I
EC5D values to crustaceans, 1.1 24hr, Daphnia (Rudolph & Boje 1988) mg/I
LOEC values to crustaceans, 0.1 21d, Daphnia (Rudolph & Boje 1988) mg/I
NOEC values to crustaceans, 0.032 21d, Daphnia fRudolph & Boje 1988) mg/I
Environment Guide71 1 53
Benzid
LC5O values to fishes, mg/I 92 96hr, Leuciscus (Rudolph & Boje 1988)
>20 96hr, Pimephales (USEPA 1977) 7.4 96hr, Salmo gaidneri
4.35 SalveHnus namaycush 2.5 Notropis lutrensis 16.2 Jordanelia floridae
(USEPA 1980d)
Effects on the physiology of Ctenopharyngodon idella; Cyprinus carpio; Trnca tinca:
water organisms 10 mg/kg, 2 days; cytogenetic effect: changes in the RNA and DNA of the ceIl) (AI-Sabti 1986).
244
•Benzidine dihydrochloride
531-85-1 Other information about Impact on biodegradation: NH3 oxidation by Nitrosomonas sp.degradation at 100mgIl:84% inhibition at 50 mg/l: 56% inhibition at 10 mg!l: 12% inhibition (Hockenbury & Grady 1977).
245
•Benzo(a)fluorene
238-84-6Sumformula of the chemical C17H12
Molecular weight 21 6.28
Melting point, °C 187—1 89
Boiling point, °C 407
Cog octanolfwater coefficient, 5.4 (San gster 1989) Iog Pow
Other information about Lethal threshold concentration (L150):
water organisms Daphnia magna; 0.0048 mg/l, 0.96 days (Newsted & Giesy 1987).
246
•Benzo(a)pyrene
50-32-8Synonyms 3,4-Benzopyrene
B(a)P Benzfa)pyrene 1 ,2-Benzpyrene Benzo(def)chrysene 6,7-Benzopyrene Sumtormula of the chemical C20H1 2
Use Benzo(a)pyrene is found in coal tar, cigarette smoke, and in the atmosphere as a product ot incomplete combustion. It is found in the exhaust soot and tar from gasoline and diesel engines. It is also found in oil, water, and food. Used in can cer research.
State and appearance Pale yellow piates or Iong needies. Monoclinic or orthorhombic crystals. Practi cally insoluble.
Molecular weight 252.3
Vapour pressure, mmHg 0.0000000055, 25 °C
Water solubility, mg/I 0.005—0.010 in seawater at 22 °C
154 Envronment Guide 71
Benzo
Melting point, °C 179
Boiling point, °C 371 at 10 mm
Log octanol/water coefficient, 7.23 caicuiated (Anon. 1989)
Iog Pow 6.35 (Sangster 1989)
Volatilization Adsorption on and movement via the sediment is probably a more important transport process than volatilization.— The haif-iife for benzo(a)pyrene voiatil ization was 1500 hr, caiculated for a river 1 m deep, water velocity 0.5
mlsec
ond, and wind velocity lm/second (Sax 1986).
Adsorption/desorption Adsorption: in estuarine water; at 0.003 mg/I, 71% adsorbed on particles afier 3 hours (Lee 1977).
A one-compartm ent model that simulated river conditions, predicted that 83%
or the benzo(a)pyrene would be sorbed onto suspended solids. The same model predicted 71% sorption in eutrophic and oligotrophic lakes and 93% in eutrophic ponds. The half-Iife ot ali fate processes combined including dilution according to this model ranged from 0.48 hr in a stream to 7.4 hr in an eutrophic lake. The percentage ot sorbed B(a)P in various sur(ace waters and wastewaters was 24—
44% at 22 °C. The log of the mean partition coefficient between the suspended particulates and the water was 4.48 (Sax 7986).
Other bindings After 3 hours incubation in natural seawater, 75% of 0.002 mg/I were taken up by suspended aggregates ot dead phytoplankton cells and bacteria (Lee et al.
1978).
Other physicochemical lnsoluble.
properties
Photochemical degradation in The most common photooxidatf on product of PAHs in solution in an endo perox air ide. Dealkylation, ring cleavage, and other reactions ensue fouowing photoiysis
or pyrolysis ot these peroxides. Frequently, only quinones are isolable. Photo dimers may resuit in some cases. Adsorbed PAH5 are more reactive man in solu tion (Sax 1986).
Ozone and UV irradiation degraded more than haif of the pure benzo(a)pyrene present in a simuiated atmosphere after 0.50 hours. Kowever, photooxidation in the atmosphere is not as rapid as predicted from model laboratory studies.
Detectabie leveis ot PAHs are usually found in urban atmospheres.
—Benzo(a)pyrene in simuiated atmospheres containing 1 ppm nitrogen dioxide and approximately 70 ppb nitric acid formed nitro derivatives that were directiy mutagenic in the Ames test (Sax 1986).
Other reactions in Airborne particuiate PAKs can persist at relatively high concentrations in aero atmosphere sois transported for iong distances. The atmosperic persistence is longer than wouid be predicted from laboratory photo oxidation studies. On the other hand, The National Academy of Sciences (1972) proposed that the chemical hait-life ot PAH’s in the atmosphere may be iimited to hours or days. For example, the hait life for benzo(a)pyrene with ozone in the gas phase is 870 hours (Sax 1986).
Photochemical degradation in The haif-life for photo iysis calculated for surface waters in midsummer at 40° N water latitude is O.54hr. B(a)P photo oxidation in natural waters depends on water
depth and varies seasonally due to changes in solar radiation, temperature and dissolved oxygen. Because or the lack of solar radiation and oxygen, photo oxi dation in sediments is negligible (Sax 1986).
Hydrolysis in water PAHs do not contain groups amenable to hydrolysis (Sax 1986).
Envitonment Guiäe 71
______________________________________________
155
Benzo
Oxidation-reduction reactions Ozone and chiorinating agents oxidize potycyciic aromatic hydrocarbons to quinones, diacids, and nuciear and side-chain oxidation products. Chlorinating agents aiso produce chlorine-substituted derivatives.—Oxidation of any PAH by chiorine and ozone, when used for the disinfection of drinking water, forms quinones. The haif-iife forthereaction of chiorine with ali PAHs is iess than 0.5 hr (Sax 1986).
Oxidation by chromic acid or ozone gives benzo(a)pyrene-1 ,6-quinone and benzo(a)pyrene-3,6-quinone. Further oxidation gives benzanthrone dicarboxyiic anhydride (Sax 1986).
Oxidation of any PAH by chiorine and ozone, when used for the disinfection of drinking water, forms quinones.— Chiorinating agents wiii aiso produce chio rine-substituted PAHs as weii as oxidation products.— The hait-iife of benzo(a)pyrene in the presence of ozone is approximateiy 1 hour and in the presence ot 0.5 ppm chiorine, 10 min utes (Sax 1986).
Oxidation by R02 radicai is siow and not significant with a half-life of 96 hr. The dissoived portion may undergo rapid photoiysis with a haif-iife of 1—2 hours (Sax 1986).
Aerobic degradation in water Microbiai degradation to C02 in seawater at 12 °C in the dark after 48 hr incuba tion at 0.016 mgli: 0 jtg/i!day; aifer addition of water extract of fuei oii 2, after 24 hr incubation: 0.00001 mg/i/day—turnovertime: 1400 days (Verschueren 1983).
Biodegradation to C02 in estuarine water:
conc. incubation degradation
rate
turnovermg/l month time (hr) (mg/I/day) x 7000 time (days)
0.005 January 24 0
0.005 June 24 0
-0.005 May 96 0.002 3500
(Lee 1977).
Degradation in seawater by oii oxidizing microorganisms (in presence of 0.365 mg/i pyrene and 0.35 mg/i fiuorene at 10 °C): initiai conc.0.190mg/i; aifer 12 days: 0.090 mg/i: 53% decrease (McKenzie & Hughes 1976).
Total degradation in soil Soii systems provide better conditions for biodegradation than do aquatic sys tems. The rate and degree of degradation is greatest when the soii and its microbiai popuiation has been acciimated.— Mycobacterium rubrom and M. tia vum metaboiized approximateiy hait or the compound within 4 days.— Strains of bacteria from highiy contaminated soii couid metaboiize 75—86 % or the B(a)P within 5 days, Bacteria from iess contaminated soii metaboiized 48—59% within the same time period.—it has been ciaimed that soii microorganims decompose B(a)P when present at high concentrations (30 ppm), but that B(a)P is not readiiy degraded when concentrations are lower (Sax 1986).
Degradation is soii: 82% aifer 8 days (soil+adapted bacteria) (Lee &Takahashi 1977).
Total degradation in water Bioiogicai degradation in sea water (10 °C): 53% after 12 days fMcKenzie &
Hughes 1976).
Total degradation in sediment PAHs deposited in sediments are iess subjeot to photochemicai or bioiogicai oxi dation, especiaiiy it the sediment is anoxic. Sedimentary PAH is therefore quite persistent and may accumuiate to high concentrations fSax 1986).
156 Environment Gude71
Benzo
Other information about Average degradation by soi! bacteria aifer 8 days culture:
degradation
amount of extracted amount 0! B(A)P
B(a)P mg destroyed (%)
soil not inoculated with
bacteria (control) 0.191 0
soil+N 5 bacterial strain 0.090 53
sod+N 13 bacterial strain 0.061 66
soi!+N 13 bacterial strain* 0.033 82
*before the experiment this strain was cultured in a medium containing Bfa)P for 110 days fPoglazova et al. 1967).
Degradation ot benz(a)pyrene:
ENVIRONMENT CONC. REDOX- TEMR DEGRADATION REF
mg/I COND. %/day
sediment 1.25 aerobic 30 6.3/37 a
sediment 1.25 anaerob 30 0.09/37 a
sediment 7 aerobic - 0/1 b
sediment 17 aerobic 20 0.84/7 c
sand 7.6 aerobic 20 1.4/7 c
sand 9.5 aerobic 20 1.2/7 c
soil 1 aerobic - 13/25 d
soi! 5 aerobic - 6/25 d
soil 10 aerobic - 3/25 d
soil fadapted) 1 aerobic - 23/25 d
soil (adapted) 2.5 aerobic - 20/25 d
soil (adapted) 5 aerobic - 30/25 d
soil (adapted) 10 aerobic - 10/25 d
soil 9.5 aerobic - 33/90 e
soN 545 aerobic - 71/90 e
soi! (adapted) 28.5 aerobic - 52/90 e
soil 0.06 aerobic 28 66/8
soi! 0.09 aerobic 28 53/8
soi! (adapted) 0.09 aerobic 28 82/8 f
a) Delaune etal. 1981 b) Herbes 1981 c) Gardner et al. 1979 d) Löw 1983
e) Khesina et al. 1969 f) Poglazowa et al. 1967 (Anon. 1987b).
Above-ground parts of plants contain more B(a)P than underground parts. The concentration is directly proportional to exposure time during the growing sea son and surface area of the plant (Sax 1986).
Other information about Ihere are !arge differences among aquatic species in their ability to absotb and metabolism assimilate PAH from food. Polychaete worms have a vety Iimited ability; fish
show Iimited and variable absorption from the gut; and crustaceans readily assimilate PAH. Assimilated PAHs are metabolized and excreted rapidly. For bio magnification to occur, a substance must be relatively resistant to metaboUsm or exretion (Sax 1986).
Cauinectes sapidus, half-Iife<2 days (Lee 1976).
HaIf-Iife in Mytilus: 16 days (Knut2en & Skei 1988).
B(a)P is metabolized to approximately 20 primariiy and secundarily oxidized metabolites and many conjugates. Many metabolites induces mutagenicity, ceII a!terations and/or binds to cellular macromolecules fIARC 1984).
Bioconcentration tactor, 70.7 7 d, Salmo salar (Verschueren 1983) fishes
Environment Guide 71 157
Benzo
Bioconcentration factor, 190 2 days, Crassostrea virginica
mollusca 3000 8 days, Crassostrea virginica
(Lee et al. 1978) 861 Macoma inquinata, 7d 8.7 Rangia cuneata, 24hr
(Sax 1986)
Bioconcentration factor, 242 2d, Callinectes sapidus (Lee 1976) crustaceans
Bioconcentration factor, other 28200 aquatic organisms containing 7.6% iipids, estimated (Sax 1986) organisms
LD5O values to mammais in 50 scu-rat (Lewis & Sweet 1984) non-oral exposure, mglkg
LDL0 values to mammais in 500 ipr-mus (Sax 1986) non-oral exposure, mglkg
TDL0 values to mammais in 40 ori-rat, 14d preg, teratogenic oral exposure, mglkg 100 ori-mus, 7-16d preg, teratogenic
1600 orl-mus, 7-16d preg, teratogenic 160 ori-rat, 6D-C, tumorigenic 700 ori-mus, 75W-l, tumorigenic
(Sax1986)
TDL0 values to mammais in 60 ipr-rat, 16-18d preg, teratogenic non-oral exposure, mglkg 150 ipr-mus, 8d preg, teratogenic
10 ipr-ham, 5d male, teratogenic 160 scu-mus, tumorigenic 10 ivn-mus, tumorigenic 17 skn-rbt, 57W-I, tumorigenic
(Sax 1986)
TCLo values to mammais in 9.5 ihi-ham, 4hr, 96W-I, tumorigenic (Sax 1986) inhalation exposure, mglkg
Effects on the physiology of Besides producing malignant tumors in laboratory animais, benzo(a)pyrene mammais damages the lymphoid system, induces tracheobronchial epithelial proliferation
and ceil hyperpiasia without necrosis or infiammation, and suppresses the immune system. Dosed rodents show tissue destruction in the pancreas and liver, and abnormal sperm (Sax 1986).
Health effects PAH5 can presumably be absorbed from ingestion, inhalation and skin contact (Sax 1986).
Skin and eye irritation data: skn, mus, 0.014 mg, mild (Sax 1986).
Carcinogenicity Garcinogenicity: positive (Mccann et al. 1975).
Strongly carcinogenic. Bfa)P is a complete carcinogen, providing both initiating and promoting stimuli.—Benzo(a)pyrene produced tumours in ali of the animal species for which data were reported in 1973. Different administration included oral, skin, and intratracheal routes. ts carcinogenic effect is both Iocal and sys temic. it produced locai sarcomas in subhuman primates after repeated subcu taneous injections and Iung carconomas after intratracheal instillation. In addition, it initiated 5km carcinogenesis in mice and proved carcinogenic after singie doses and prenatal exposure.— B(a)P has aiso induced tumours in sali vary giands, pancreas, subcutaneous tissues, mammary grands, uterus, vagina, kidney, brain, and thymus (Sax 1986).
158 Environment Guide 71
Benzo
Mutagenicity Mutagenicity in the Salmonella test: positive;
121 revertant colonies/nmol
2398 revertant colonies at 0.005 mg/plate (McCann et al. 1975).
Mutagenicity: induced significant mutation to 8-azaguanine resistance in Sai-monella typhimurium at concentrations as low as 0.004 mM (Krishnan et al.
1979).
Mutagenic to mice and bacteria. Cell cultures of many species including man show inhibition ot DNA synthesis after treatment with B(a)R—Certain metabo lites ot B(a)P, especially the diol epoxides, are much more mutagenic in Salmo nella typhimurium 1A98 and chinese hamsterV79 ceiis than B(a)P itseit.— B(A)P was found to be positive in the sister chromatid exchange test, weakiy active in the chromosome aberration test, and negative in the micronucleus test (Sax 1986).
Mutagen data:
mmo, sat, 0.333 mg/plate;
mrc, esc, 0.070/weli;
dnr, ocs, 0.100 mi/piate;
dnd, omi, 11 ngli;
dnd, sai, tes, 0.005, 1 H-C;
msc, ofs, fbr, 5mgIl;
dnd, hmn, oth, 1500 nmoi/l;
dnd, hmn, ing, 0.001 mmoi/i (Sax 1986).
Effects on wastewater Polychiorinated PAHs are probably highiy toxic to aquatic organisms and persis treatment tent in the environment as are polychlorinated biphenyis and poiychiorinated
naphthalenes. Chiorination for puritication ot wastewaters or drinking waters containing high concentrations ot PAH5 may be inadvisabie. Activated siudge treatment is unable to oxidize PAHs within normal retention times. Since large PAHs are insoluble in water, either they do not support bacteriai growth or growth may be extremely siow. The probiem has been somewhat overcome by use of other carbon sources to stimulate (or induce) bacteria. Apparently, iong term exposure ot microbes is necessary before a bacteriai population is capabie of degrading PAHs (Sax 1986).
EC5O values to algae, mg/I >4 3d, grw, Anabaena fios-aquae
>4 3d, grw, Chiamydomonas reinhardtii
>4 3d, grw, Eugiena graciiis 0.005 3d, grw, Scenedesmus obliquus 0.015 3d, grw, Seienastrum capricornutum
>4 3d, grw, Poteriochromonas maihamensis (Schoeny et al. 1988)
LC5O values to crustaceans, 0.05 96 hr, Daphnia puiex (Govers et al. 1984) mg!I
Effects on the physiology of Ctenopharyngodon della; Cyprinus carpio; Tinca tinca:
water organisms 10mglkg,2 days, cytogenetic effect (changes in the RNA and DNA ot the ceil) (Al-Sabti 1986).
Lepomis macrochirus; 0.005 mg/g, 3 days, biochemicai effect (change in phys iochemicai process inciuding giycogen uptake, choiesterol leveis and lipid anat ysis) (Shugart et ai. 1987).
Saimo gairdneri; 0.63 mmol, 6 days, biochemical effect (change in physiochemi cai process inciuding giycogen uptake, choiesterol leveis and iipid anaiysis) (Miyauchi & Uematsu 1987).
lctaiurus nebulosus; 4 d, 0.005—0.025 mg/g, cytogenetic effect (Metcaite 1988).
Lepomis macrochirus, 10 d, 0.001—0.020 mg/g, enzyme effect (Jimenez & Burtis 1988).
Poeciiiopsis monacha, 1 d, 0.8—1.0 mg/l, enzyme effect;
Poeciiiopsis sp, 1 d, 3.75 mg/i, Iethai effect (Goddard et al. 1987).
Environment Guide 71 1 59
Benzo
Other information about Lethal threshold concentration (LT50):
water organisms Daphnia magna; 0.001 5 mg/I, 0.19 days (Newsted & Giesy 1987) Pimephales promelas; 0.0056 mg/I, 1.67 days (Oris et al. 1987).
Acute toxicity to fish:
High molecular PAH (B(a)P, chrysene) have generally Iow acute toxicity, probably due to their Iow solubility (Neff 1979).
Chronic toxicity:
Chronic toxicity (carcinogenicity, mutagenicity, teratogenicity) is a concequence of high activated, soluble metabolites ot B(a)P via covalent bindning to cellular macromoleculs (Heideiberger 1976).
The growth of algae is stimulized by low concentrations ot B(a)P (0.01—0.1 mg/l) (Graf & Nowak 1966, Boney & Corner 1962).
Other information Manufacturing source: coal tar processing; petroleum retining; shale refining;
coal and coke processing kerosene processing; heat and power generation sources.
Natural sources: quantities synthesized by various bacteria:
mg of B(a)P produced
per kg ofspecies dry bacterial biomass Mycobacterium smegmatis 0.060
Proteus vuigaris 0.056
Escherichia coli (strain 1) 0.050 Escherichia coli (strain 2) 0.046 Pseudomonas fluorescens 0.030
Serratia marcescens 0.020
Synthesized by algae Chlorella vuigaris.
Man caused sources (air and water): combustion of tobacco, combustion ot fuels; present in run off containing greases, oils, etc.; potential roadbed and asphalt leachate. (Verschueren 1983)
>10% otto atmosphere emitted B(a)P goes to water environment (Neff 1979).
Microbial degradation to 9-hydroxybenzofa)pyrene and acids (Gibson 1976b).
Degradation products with special interest:
benzo(a)pyrenequinones; 9,1 0-epoxy-7,8-dihydrozybenzo(a)pyrene;
B(a)P-dihydrodioles; B(a)P-diolepoxides; B(a)P-oxides (USEPA 1980).
247
•Benzo-a-pyrone
91-64-5Synonyms Coumarin
1 ,2-Benzopyrone o-Coumaric acid Iactone Coumarinic lactone Cumarin
Tonka bean camphor
State and appearance Colourless crystals, flakes or powder.
Odour GuaHty: vanilla
Hedonic tone: pleasant
Molecular weight 146.14
Specific gravity (water=1) 0.935 at 20/4 °C
Vapour pressure, mmHg 1 at 106 °C
40 at189°C
Water solubilily, mg/J 100 at 25 C
Melting point, °C 68 (MITI 1992)
160 Environment Guide 71
Benzo
Boihng point, °C 291 (MIII 1992)
Log octanol/water coetficient, 1.39 Iog Pow
Total degradation in water Biodegradation:
100% by BOD perod; 14d substance: 100 mg/I sludge: 30 mg/I (MIII 1992).
Ready biodegradability Confirmed to be biodegradable (Anon. 1987).
LD5O values to mammais in 235—290 orl-rat (Verschrueren 1983) oral exposure, mg/kg
248
•Benzofb)fluoranthene
205-99-2Synonyms 34-Benztluoranthene
B(b)F Sumformula of the chemical C2OH1 2
Molecular weight 252
Log octanol/water coefficient, 5.78 (Sangster 1989) Iog Pow
249
•Benzo(b)fluorene
30777-79-6Molecular weight 21 6.28
Melting point, C 209—210.5
Other information about Lethal threshold concentration (L150):
water organisms Daphnia magna: 0.0022 mgII, 0.93 Uays (Newsted & Giesy 1987).
250
•Benzo(e)pyrene
192-97-2Synonyms 1 ,2-Benzopyrene
B(e)P
Molecular weight 252
Water solubility, mgII 0.004 at 25 °C
Carcinogenicity Carcinogenicity: weakly carcinogenic (McCann et al. 1975).
Mutagenicity Mutagenicity in the Salmonella test: positive;
>60 revertant colonies/nmol
143 revertant colonies at 0.060 mg/plate (McCann et aI. 1975).
Other information about Lethal threshold concentration (LT5O):
water organisms Daphnia magna: 0.0007 mgII, 0.64 days (Newsted & Giesy 1987).
251
•Benzo(ghi)perylene
191-24-2Synonyms 1,1 2-Benzoperylene
B(ghi)P
Environmeni Gude 71
Benzo
Sumformula ot the chemical C22H1 2
Use Main constituent in the residues ftom coal hydrogenation.
State and appearance Large pale yeiiow-green piates.
Molecular weight 276.34
Vapour pressure, mmHg 0.0000000001 Water solubihty, mg/t 0.00026 at 25 °C
Melting point, °C 222
273
Log octanol/water coetficient, 7.23 (Sax 1986)
Iog Pow 6.51 (Sax 1986)
6.9 (Sangster 1989)
Volatilization Evaporation of iower-molecuiar-weight PAHs may be significant only in a clear, rapidly flowing shaliow stream (Sax 1986).
Adsorption/desorption Movement via sediment is an important transport process. An exchange equiiib rium exists in natural water systems between absorbed and soiubie PAHs.
Aithough the particuiate form is favoured, a significant fraction of the PAH wiii he dissolved except in systems that are vety heavHy contaminated by PAHs (Sax 1986).
Other physicochemical insoluble.
properties
Photochemical degradation in The most common photooxidation product of PAKs in solution in an endo perox air ide. Dealkylation, ring cieavage, and other reactions ensue foilowing photo lysis
or pyrolysis of these peroxides. Frequentiy, only quinones ate isolabie. Photo dimers may resuit in some cases. Adsorbed PAHs ate more reactive tilan fl solu tion (Sax 1986).
Photochemical degradation in Photo lysis in an aquatic environment may be an important fate process, espe water ciaiiy for the dissolved portion fSax 1986).
Hydrolysis in water Hydroiysis is not significant fSax 1986).
Oxidation-reduction reactions Ozone and chiorinating agents oxidize poiycyclic aromatic hydrocarbons to quinones, diacids, and nuclear and side-chain oxidation products. Chlorinating agents also produce chiorine-substituted detivatives.—Oxidation of any PAH by chiorine and ozone, when used for the disinfection ot dtinking water, forms quinones. The haif-life for the reaction of chiorine with ali PAHs is iess than 0.5
Oxidation-reduction reactions Ozone and chiorinating agents oxidize poiycyclic aromatic hydrocarbons to quinones, diacids, and nuclear and side-chain oxidation products. Chlorinating agents also produce chiorine-substituted detivatives.—Oxidation of any PAH by chiorine and ozone, when used for the disinfection ot dtinking water, forms quinones. The haif-life for the reaction of chiorine with ali PAHs is iess than 0.5