53-70-3

Hazards Identification

Pictogram(s):

Signal:

Danger

GHS Hazard Statements:

H350: May cause cancer [Danger Carcinogenicity]
H400: Very toxic to aquatic life [Warning Hazardous to the aquatic environment, acute hazard]
H410: Very toxic to aquatic life with long lasting effects [Warning Hazardous to the aquatic environment, long-term hazard]

Precautionary Statement Codes:

P203, P273, P280, P318, P391, P405, and P501

Hazard Classes and Categories:

Carc. 1B
Aquatic Acute 1
Aquatic Chronic 1
Carc. 1B (100%)
Aquatic Acute 1 (100%)
Aquatic Chronic 1 (98.31%)
Carcinogenicity - category 1B
Hazardous to the aquatic environment (acute) - category 1
Hazardous to the aquatic environment (chronic) - category 1
Germ cell mutagenicity - Category 2
Carcinogenicity - Category 1B
Hazardous to the aquatic environment (Long-term) - Category 4
Carcinogens, Mutagens

Hazards Summary:

May cause skin photosensitization; A probable human carcinogen; Can be absorbed through skin; [ICSC] Evidence of carcinogenicity, mutagenicity, developmental toxicity, and immunosuppression in experimental animals; Emergency treatment: Polynuclear aromatic hydrocarbons; Acute toxicity of PAHs is low; May cause photosensitivity; May cause cancer after chronic exposure; [HSDB] Causes decreased humoral immune response and changes in hepatic microsomal mixed oxidase in oral toxic-dose studies of mice; [RTECS] May cause skin and eye irritation; [Cerilliant MSDS] See POLYCYCLIC AROMATIC HYDROCARBONS.

Usage

Uses

Used in Research Applications:
Dibenz[a,h]anthracene is used as a mutagen in biological research for inducing tumorigenesis. It has produced positive results in bacterial DNA damage and mutagenicity assays, as well as in mammalian cell DNA damage, mutagenicity, and cell transformation assays.
Used in Environmental and Industrial Applications:
Dibenz[a,h]anthracene is found in coal tars, shale oils, and soots, and has been detected in gasoline engine exhaust, coke oven emissions, cigarette smoke, charcoal broiled meats, vegetation near heavily traveled roads, and surface water and soils near hazardous waste sites. It is used for studying the effects of environmental pollutants and carcinogens on human health and the environment.
There is no report on the common use of dibenz[a,h]anthracene and its commercial production, indicating that its primary application is limited to research purposes.

Production Methods

There is no commercial production or known use of this compound. It has been isolated from the coal tar pitch and is found in coke over effluents. It has been detected in urban atmospheres and occurs in tobacco smoke. Dibenz [a,h]anthracene is present as a minor component of the total PAH content in the environment. Human exposure occurs through smoking, inhaling of polluted air, and by ingesting food and water containing combustion products.

Air & Water Reactions

Insoluble in water.

Reactivity Profile

1,2:5,6-DIBENZANTHRACENE is incompatible with strong oxidizing agents. Is oxidized by chromic acid and by osmium tetraoxide .

Health Hazard

The toxicity of dibenz[a,h]anthracene is onthe same order as that of benz[a]anthracene.A lethal dose in mice by intravenous routeis 10 mg/kg. There is no report on its oraltoxicity. It is a mutagen. Its carcinogenicityin animals is well established, causing cancersin the lungs, liver, kidney, and skin.

Fire Hazard

Flash point data for 1,2:5,6-DIBENZANTHRACENE are not available; however, 1,2:5,6-DIBENZANTHRACENE is probably combustible.

Safety Profile

Confirmed carcinogen with experimental carcinogenic, tumorigenic, and neoplastigenic data. Poison by intravenous route. Human mutation data reported. When heated to decomposition it emits acrid smoke and irritating fumes.

Potential Exposure

Dibenz(a,h)anthracene is a chemical substance formed during the incomplete burning of fossil fuel, garbage, or any organic matter and is found in smoke in general; it condenses on dust particles and is distributed into water and soil and on crops. DB(a,h)A is a PAH and is also a component of coal tar pitch, which is used in industry as a binder for electrodes, and creosote is used to preserve wood. PAHs are also found in limited amounts in bituminous materials and asphalt used in industry and for paving.

Carcinogenicity

Based on no human data and sufficient data from animal assays, IRIS classifies dibenz [a,h]anthracene as a B2 carcinogen, a probable human carcinogen, and the IARC classifies dibenz[a,h]anthracene as a 2A carcinogen. Dibenz[a,h]anthracene produced carcinomas in mice following oral or dermal administration and injection site tumors in several species following s.c. or i.m. injection. It is also a tumor initiator.

Source

Constituent in coal tar, cigarette smoke (4 μg/1,000 cigarettes), and exhaust condensate of gasoline engine (96 μg/g) (quoted, Verschueren, 1983). Also detected in asphalt fumes at an average concentration of 12.25 ng/m3 (Wang et al., 2001). Based on laboratory analysis of 7 coal tar samples, dibenz[a,h]anthracene was not detected (EPRI, 1990). Lehmann et al. (1984) reported dibenz[a,h]anthracene concentrations of 0.03 mg/g and 1,300 mg/kg in a commercial anthracene oil and high-temperature coal tar, respectively. Identified in a high-temperature coal tar pitch used in roofing operations at concentrations ranging from 317 TO 1,680 mg/kg (Malaiyandi et al., 1982). Nine commercially available creosote samples contained dibenz[a,h]anthracene at concentrations ranging from 1 to 16 mg/kg (Kohler et al., 2000). Under atmospheric conditions, a low rank coal (0.5–1 mm particle size) from Spain was burned in a fluidized bed reactor at seven different temperatures (50 °C increments) beginning at 650 °C. The combustion experiment was also conducted at different amounts of excess oxygen (5 to 40%) and different flow rates (700 to 1,100 L/h). At 20% excess oxygen and a flow rate of 860 L/h, the amount of dibenz[a,h]anthracene emitted ranged from 32.0 ng/kg at 900 °C to 260.9 ng/kg at 750 °C. The greatest amount of PAHs emitted were observed at 750 °C (Mastral et al., 1999).

Environmental fate

Biological. In activated sludge, <0.1% of the applied dibenz[a,h]anthracene mineralized to carbon dioxide after 5 d (Freitag et al., 1985). Based on aerobic soil die away test data, the estimated half-lives ranged from 361 to 940 d (Coover and Sims, 1987). Ye et al. (1996) investigated the ability of Sphingomonas paucimobilis strain U.S. EPA 505 (a soil bacterium capable of using fluoranthene as a sole source of carbon and energy) to degrade 4, 5, and 6-ringed aromatic hydrocarbons (10 ppm). After 16 h of incubation using a resting cell suspension, only 7.8% of dibenz[a,h]anthracene had degraded. It was suggested that degradation occurred via ring cleavage resulting in the formation of polar metabolites and carbon dioxide. Soil. The reported half-lives for dibenz[a,h]anthracene in a Kidman sandy loam and McLaurin sandy loam are 361 and 420 d, respectively (Park et al., 1990). Photolytic. A carbon dioxide yield of 45.3% was achieved when dibenz[a,h]anthracene adsorbed on silica gel was irradiated with light (λ >290 nm) for 17 h (Freitag et al., 1985). The photooxidation half-life in the atmosphere was estimated to range from 0.428 to 4.28 h (Atkinson, 1987). Chemical/Physical. Dibenz[a,h]anthracene will not hydrolyze because it does not contain a hydrolyzable functional group (Kollig, 1993). At influent concentrations of 1.0, 0.1, 0.01, and 0.001 mg/L, the GAC adsorption capacities were 69, 12, 2.1, and 0.39 mg/g, respectively (Dobbs and Cohen, 1980).

Shipping

UN2811 Toxic solids, organic, n.o.s., Hazard Class: 6.1; Labels: 6.1-Poisonous materials, Technical Name Required. UN3077 Environmentally hazardous substances, solid, n.o.s., Hazard class: 9; Labels: 9-Miscellaneous hazardous material, Technical Name Required.

Purification Methods

The yellow-green colour (due to other pentacyclic impurities) is removed from it by crystallising from *benzene or by selective oxidation with lead tetraacetate in acetic acid [Moriconi et al. J Am Chem Soc 82 3441 1960]. [Beilstein 5 IV 2722.]

Toxicity evaluation

Dibenz[a,h]anthracene is largely associated with particulate matters, soils, and sediments. Its presence in places distant from primary sources indicates that it is reasonably stable in the atmosphere and capable of long-distance transport.Dibenz[a,h]anthracene can be adsorbed very strongly if released to the soil. However, no leaching to the groundwater or hydrolization or evaporation from soils surface is expected.With half-lives of 18 and 21 days, it is generally subjected to biodegradation in soil systems. Volatilization of dibenz[a,h] anthracene from wet soil surfaces is not expected to be an important fate process based on an estimated Henry’s Law constant of 7.3×10-8 atm-m3 mol-1. A biodegradation halflife of 750 days at 20°C after incubation with unacclimated soil microcosms indicates that biodegradation is not an important environmental fate process in soil. Dibenz[a,h]anthracene released to the atmosphere will likely be associated with particulate matter and may be subjected to moderately long-range transport, depending mainly on the particle size distribution and climatic conditions, which will determine the rates of wet and dry deposition. The estimated vapor pressure of 9.5×1010 mm Hg at 25°C of dibenz[a,h] anthracene indicates that Dibenz[a,h]anthracene will exist solely in the particulate phase in the ambient atmosphere if released into air. Its presence in areas remote from primary sources demonstrates the potential for this long-range transport as well as dibenz[a,h]anthracene’s considerable stability in the air. Dibenz[a,h]anthracene absorbs solar radiation strongly, suggesting that it may be susceptible to direct photolysis in the environment. The estimated vapor phase half-life in the atmosphere is 1 day as a result of reaction with photochemically produced hydroxyl radicals.

Waste Disposal

See the entry on Coal Tar Pitch Volatiles. Consult with environmental regulatory agencies for guidance on acceptable disposal practices. Generators of waste containing this contaminant (≥100 kg/ mo) must conform with EPA regulations governing storage, transportation, treatment, and waste disposal.

References

https://pubchem.ncbi.nlm.nih.gov/compound/Dibenz_a_h_anthracene#section=Top Heidelberger, Charles, and H. B. Jones. "The Distribution of Radioactivity in the Mouse Following Administration of Dibenzanthracene Labeled in the 9 and 10 Positions with Carbon Fourteen." Cancer1.2(2010):252. https://rais.ornl.gov/tox/profiles/dibenz_a_h_anthracene_c_V1.html

InChI:InChI=1/C22H14/c1-3-7-19-15(5-1)9-11-17-14-22-18(13-21(17)19)12-10-16-6-2-4-8-20(16)22/h1-14H

Upstream product

• 41774-28-1 (2-methylnaphthalen-1-yl)(naphthalen-1-yl)methanone 
• 110876-52-3 (2-methyl-[1]naphthyl)-[2]naphthyl ketone 
• 90-12-0 1-Methylnaphthalene 
• 86-52-2 1-Chloromethylnaphthalene 
• 91-57-6 2-Methylnaphthalene 
• 63077-06-5 dibenzanthracen-7-ol acetate 
• 3719-43-5 dibenzo[a,h]anthracene-7,14-dione 
• 73540-67-7 3-[1]naphthyl-3H-naphtho[1,2-c]furan-1-one 
• 66-77-3 1-naphthaldehyde 
• 81194-74-3 lithium salt of N,N-diethyl-1-naphthtamide 
• 75-15-0 carbon disulfide 
• 7446-70-0 aluminium trichloride 
• 2506-41-4 1-chloromethylnaphthalene 
• 57816-08-7 7,14-dihydrodibenz[a,h]anthracene 

Downstream Products

• 3719-43-5 dibenzo[a,h]anthracene-7,14-dione 
• 63348-49-2 7-Fluor-dibenzanthracen 
• 192-47-2 1.2,4.5,8.9-tribenzopyrene 
• 14474-66-9 5,12-Diphenyl-dibenzanthracen 
• 1421-85-8 dibenzanthracene 5,6-oxide 
• 153-34-4 5,6-dihydrodibenzanthracene 
• 153-31-1 5,6,12,13-tetrahydrodibenzanthracene 
• 63041-91-8 7-nitrodibenzanthracene 
• 3732-92-1 dibenz[a,h]anthracene-5,6-dione 
• 79970-90-4 C₃₆H₂₅BrO₄ 
• 66267-18-3 trans-1,2-dihydroxy-1,2-dihydrodibenzanthracene 
• 66302-72-5 trans-1,2-bis(benzoyloxy)-1,2-dihydrodibenzanthracene 
• 66267-13-8 trans-1,2-bis(benzoyloxy)-1,2,3,4-tetrahydrodibenzanthracene 
• 63019-72-7 5-Methoxydibenzanthracen 

Relevant academic research and scientific papers

(1)H NMR PATTERNS OF ANTIAROMATIC SYSTEMS: PARATROPIC DISPLACEMENT DEPENDENCE UPON LUMO-HOMO ENERGY GAP

(1)H NMR chemical shifts of antiaromatic species reveal an enhanced paratropic displacement.The high-field shifts exhibited by doubly charged benzenoid polycycles were shown to be strongly related to the LUMO-HOMO energy gap in these antiaromatic systems.As the gap decreases, a larger paratropic shift was observed.

Br?nsted Acid-Catalyzed Carbonyl-Olefin Metathesis: Synthesis of Phenanthrenes via Phosphomolybdic Acid as a Catalyst

Compared with the impressive achievements of catalytic carbonyl-olefin metathesis (CCOM) mediated by Lewis acid catalysts, exploration of the CCOM through Br?nsted acid-catalyzed approaches remains quite challenging. Herein, we disclose a synthetic protocol for the construction of a valuable polycycle scaffold through the CCOM with the inexpensive, nontoxic phosphomolybdic acid as a catalyst. The current annulations could realize carbonyl-olefin, carbonyl-alcohol, and acetal-alcohol in situ CCOM reactions and feature mild reaction conditions, simple manipulation, and scalability, making this strategy a promising alternative to the Lewis acid-catalyzed COM reaction.

Dibenzoanthradiquinone Building Blocks for the Synthesis of Nitrogenated Polycyclic Aromatic Hydrocarbons

A straightforward method for the synthesis of two dibenzo[a,h]anthracene-5,6,12,13-diquinone building blocks is reported. To showcase their usefulness, a series of dibenzo[a,h]anthracene nitrogenated derivatives have been synthesized that show different optoelectronic, redox, and charge transport properties, illustrating their potential as organic semiconductors.

Oxidative, Iodoarene-Catalyzed Intramolecular Alkene Arylation for the Synthesis of Polycyclic Aromatic Hydrocarbons

A catalytic, metal-free and chemoselective oxidative intramolecular coupling of arene and alkene C?H bonds is reported. The active hypervalent iodine (HVI) reagent, generated catalytically in situ from iodotoluene and meta-chloroperoxybenzoic acid (m-CPBA), reacts with o-vinylbiphenyls to generate polyaromatic hydrocarbons in up to 95 % yield. Experimental evidence suggests the reactions proceed though vinyliodonium and, possibly, vinylenephenonium intermediates.

Synthesis of phenanthrenes by cationic chromium(III) porphyrin-catalyzed dehydration cycloaromatization

Readily available biphenyl derivatives with ortho oxirane moiety react in the presence of cationic chromiun(III) porphyrin catalyst to afford phenanthrenes. The reaction is considered to be triggered by activation of the oxirane moiety through coordination to the Lewis acidic cationic chromium to give aldehyde via 1,2-hydride shift, which reacts with arene through intramolecular electrophilic aromatic substitution and subsequent dehydration. The reaction allows constructing a variety of polycyclic aromatic and heteroaromatic compounds.

Synthesis of dibenz[a,h]anthracenes by Pd-catalyzed intramolecular double-cyclization of (Z,Z)-p-styrylstilbenes

Dibenz[a,h]anthracene (1a) and its dimethoxy derivatives 1b and 1c were synthesized by the Pd-catalyzed intramolecular double-cyclization of the corresponding (Z,Z)-p-styrylstilbene derivatives 25, which were readily prepared by the Wittig reaction. The optical properties of the dibenz[a,h]anthracenes 1a1c are also presented.

Controlling the regioselectivity of the di-p-methane rearrangements of 1,2-naphtho-annelated barrelene derivatives-Solution versus solid-state photochemistry

The synthesis of 1,2-naphtho-annelated barrelene derivatives, namely dimethyl-7,12-dihydro-7,12-ethenobenzo[a]anthracene-13,14-dicarboxylate (4a) and dimethyl-7,14-dihydro-7,14-ethenodibenzo[a,j]-anthracene-15,16-dicarboxylate (4b), and the investigation

Role of temperature and hydrochloric acid on the formation of chlorinated hydrocarbons and polycyclic aromatic hydrocarbons during combustion of paraffin powder, polymers, and newspaper

Formation of chlorinated hydrocarbons and polycyclic aromatic hydrocarbons (PAHs) were determined using a laboratory-scale incinerator when combusting materials at different temperatures, different concentrations of hydrochloric acid (HCl), and when combusting various types of polymers/newspaper. Polychlorobenzenes (PCBz), polychlorophenols (PCPhs), polychlorinated dibenzo-p-dioxins/furans (PCDD/Fs) and their toxic equivalency (TEQ) and PAHs were highlighted and reported. Our results imply maximum formation of chlorinated hydrocarbons at 400°C in the following order; PCBz≥PCPhs?PCDFs>PCDDs>TEQ on a parts-per-billion level. Similarly, a maximum concentration of chlorinated hydrocarbons was noticed with an HCl concentration at 1000 ppm with the presence of paraffin powder in the following order; PAHs>PCBz≥PCPhs?PCDFs>PCDDs>TEQ an a parts-per-billion level. PAHs were not measured at different temperatures. Elevated PAHs were noticed with different HCl concentrations and paraffin powder combustion (range: 27-32 μg/g). While, different polymers and newspaper combusted, nylon and acrylonitrile butadiene styrene (ABS) produced the maximum hydrogen cyanide (HCN) concentration, concentrations of PCDD/FS, dioxin-like polychlorinated biphenyls (DL-PCBs), and TEQ were in a decreasing order: polyvinylchloride (PVC)newspaperpolyethyleneterephthalate (PET) polyethylene (PE) polypropylene (PP) ABS = blank. Precursors of PCBs were in a decreasing order: PPnylonPEnewspaperABSPVCblankPET. Precursors of PCDD/Fs were in a decreasing order: newspaper PP= nylonPEABSPVC= blankPET. BTX formation was in a decreasing order; PEnylonnewspaperABSPP. PAHs formation were elevated with parts-per-million levels in the decreasing order of PPnylonPE newspaperblankABS PETPVC.

Emission factors for carbonaceous particles and polycyclic aromatic hydrocarbons from residential coal combustion in China

Emission factors of carbonaceous particles, including black carbon (BC) and organic carbon (OC), and polycyclic aromatic hydrocarbons (PAHs) were determined for five coals, which ranged in maturity from sub-bituminous to anthracite. They were burned in the form of honeycomb briquettes in a residential coalstove, one of the most common fuel/stove combinations in China. Smoke samples were taken through dilution sampling equipment, with a high volume sampler that could simultaneously collect emissions in both particulate and gaseous phases, and a cascade impactor that could segregate particles into six fractions. Particulate BC and OC were analyzed by a thermal-optical method, and PAHs in emissions of both phases were analyzed by GC-MS. Burning of bituminous coals produced the highest emission factors of particulate matter (12.91 g/kg), BC (0.28 g/kg), OC (7.82 g/kg), and 20 PAHs (210.6 mg/kg) on the basis of burned dry ash-free (daf) coal, while the anthracite honeycomb-briquette was the cleanest household coal fuel. The size-segregated results show that more than 94% of the particles were submicron, and calculated mass median aerodynamic diameters (MMAD) of all particles were under 0.3 μm. Based on the coal consumption in the residential sector of China, 290.24 Gg (gigagrams) of particulate matter, 5.36 Gg of BC, 170.33 Gg of OC, and 4.72 Gg of 20 PAHs mass were emitted annually from household honeycomb-briquette burning during 2000. Anthracite coal should be selected preferentially and more advanced burning conditions should be applied in domestic combustion, from the viewpoint of both climate change and adverse health effects.

Experimental study on the removal of PAHs using in-duct activated carbon injection

This paper presents the incineration tests of municipal solid waste (MSW) in a fluidized bed and the adsorption of activated carbon (AC) on polycyclic aromatic hydrocarbons (PAHs). An extraction and high performance liquid chromatography (HPLC) technique was used to analyze the concentrations of the 16 US EPA specified PAHs contained in raw MSW, flue gas, fly ash, and bottom ash. The aim of this work was to decide the influence of AC on the distribution of PAHs during the incineration of MSW. Experimental researches show that there were a few PAHs in MSW and bottom ash. With the increase of AC feeding rate, the concentrations of three- to six-ring PAHs in fly ash increased, and the concentration of two-ring PAH decreased. The total-PAHs in flue gas were dominated by three-, and four-ring PAHs, but a few two-, five-ring PAHs and no six-ring PAHs were found. PAHs could be removed effectively from flue gas by using in-duct AC injection and the removal efficiencies of PAHs were about 76-91%. In addition, the total toxic equivalent (TEQ) concentrations of PAH in raw MSW, bottom ash, fly ash, and flue gas were 1.24 mg TEQ kg-1, 0.25 mg TEQ kg-1, 6.89-9.67 mg TEQ kg-1, and 0.36-1.50 μg TEQ N m-3, respectively.