DEHALOGENATION OF HALOGENATED ORGANIC COMPOUNDS

Abstract: A process for the degradation of a polyhalogenated organic compound comprises irradiating a polyhalogenated organic compound with ultra-violet light to produce a lesser halogenated organic compound and thereafter biologically degrading the lesser halogenated organic compound. The irradiation is performed such that the polyhalogenated organic compound is incompletely dehalogenated while the biological degradation is performed using an organism adapted to degrade the lesser halogenated compound produced by the irradiation of the polyhalogenated organic compound but not adapted to substantially effectively degrade the polyhalogenated compound.

Description: This invention relates to dehalogenation of halogenated organic compounds. This invention also relates to degradation of halogenated organic compounds. This invention also relates to disposal of halogenated organic compounds. Halogenated organic compounds are used for a variety of purposes including pesticides such as chlordane, DDT and Lindane, fumigants, solvents such as chlorobenzenes, and insulating fluids such as polychlorinated biphenyls (PCBs). These chemicals are often chemically stable and the substituent halogen atoms often cause them to be highly resistant to microbial degradation. Thus many of these chemicals are severe pollutants, lasting for decades in the environment and accumulating in the food chain with detrimental effects on animals and man. Much attention has been focused on the development of method for the safe disposal of such chemicals. Chemical methods such as incineration often have undesirable properties including generation of toxic byproducts causing further pollution, or inability to totally degrade the chemicals. Biological methods are often too slow or incomplete. For example, while PCB isomers with few chlorines are readily metabolized by certain bacteria, PCBs with many chlorines are digested slowly if at all. Much work is being done to improve microbial performance in this regard, but the development or isolation of bacteria capable of rapid destruction of all PCB isomers is considered some years off. Ultra-violet radiation has also been used with some success but is limited by the long treatment times that are necessary and the need to use dilute solutions of halogenated compounds. The present invention provides a process for degradation of a polyhalogenated organic compound comprising irradiating a polyhalogenated organic compound with ultra-­ violet light to produce a lesser halogenated organic compound and thereafter biologically degrading said lesser halogenated organic compound. Said irradiation is preferably performed so as not to completely dehalogenate said polyhalogenated organic compound. Preferably said polyhalogenated compound is in a liquid medium during said irradiation in an amount of at least 1,000ppm, more preferably at least 5,000ppm, still more preferably 1,000 to 100,000ppm, even more preferably 7,500 to 15,000ppm and most preferably about 10,000ppm. Preferably said polyhalogenated compound is subjected to from 1,000 to 20,000, more preferably 2,000 to 10,000 and most preferably 3,000 to 6,000 milliwatt hours of ultra-violet radiation per gm of polyhalogenated organic compound. Preferably said polyhalogenated compound in a liquid medium is subjected to from 50 to 1,000 more preferably 100 to 500 (1,500) most preferably 150 to 300 milliwatt hours of ultra-violet radiation per square centimeter of a surface of said medium while the depth of said medium and/or volume are such that the area irradiated is from 10 to 25 square cm per gm polyhalogenated compound dissolved therein. Said irradiation is increased or decreased for lesser or greater irradiated area and dependant on the proportion of said volume which is being effectively irradiated at any one time and said medium is circulated or made turbulent to improve average exposure per molecule. Preferably said medium is comprised of two substantially immiscible phases. One of said phases is preferably an aqueous phase and the other of said phases is preferably an organic solvent for the polyhalogenated organic compound. Said organic solvent may be a non-polar solvent but, since removal of chlorine is conveniently affected in part by salt formation, it is considered more convenient that said organic solvent be a polar solvent. Since polar solvents are commonly soluble in water such that said organic solvent and said aqueous phase might be miscible, it is particularly preferred that said aqueous phase be a solution such as to be substantially immiscible with the organic solvent. Thus, the aqueous phase may contain ingredients to effect the obtaining of two phases. In a preferred aspect said aqueous phase contains an alkali. Suitable alkalis include sodium hydroxide and potassium hydroxide. Of these sodium hydroxide is preferred by reason of cost. Preferably said aqueous phase contains at least 8%, more preferably at least 10% by weight of an alkali. Said aqueous phase may be saturated with alkali, and in practice this will amount to about 40% by weight. Preferably said aqueous phase comprises from 5% (10%) to 50% by weight of said medium with 15 to 30% being more preferred and about 25% being most preferred. As said organic solvent there may be used a non-polar solvent such as hexane but it is preferred to use an alcohol such as methanol, ethanol, butanol, propanol or isopropanol. Particularly preferred is to use isopropanol as said organic solvent. Solvents may be recycled if desired. Said irradiation is preferably conducted while passing hydrogen gas through said medium. Said irradiation is preferably performed over a period not in excess of 12 hours. The amount of hydrogen passed through said medium is preferably 50-60ml per minute of hydrogen gas (STPbase) or equivalent at other temperatures or pressures per 1,200 ml of said medium or 4 - 5ml per minute per gram or per ml of polyhalogenated organic compound. Unutilised hydrogen gas may be recycled. The biological degradation may involve the use of a wide variety of cells and amongst these we mention cells deposited by the inventors with ATCC and referenced. The above have also been deposited with ACMM (Australian Collection of Marine Micro-Organisms) as ACMM 600 to 604. NCIB 10643 ( Pseudomonas sp.) and NCIB 10504 ( Flavobacterium sp.) are also known biphenyl-utilizing strains. NCIB is the National Collection of Industrial Bacteria (U.K.). Other useful strains are the dichlorobenzoate-degrading strains Pseudomonas HCV(2,4) DCB (ATCC 31942) and Pseudomonas HCV(3,4) DCB (ATCC 31940) described in European Patent Application No. 85108991.4 (chlorobenzoic acids are common metabolites of chlorinated biphenyls). It should be noted that the particular micro-organism utilized in the biological degrdation is not of the essence of this invention and the above mentioned organisms are not the only ones which might be used. Fruitful sources of further micro-organisms would be by isolation from halogenated organic chemical contaminated soil. Genetically modified material might also be used. The biological degradation may be performed under aerobic or anaerobic conditions or a combination of both. A bromass may be suspended in a fixed film reactor or in a fluidized bed or a combination of both. Surplus biomugs may be used as a soil conditioner. Preferred apparatus for performing the present invention is show in the accompanying drawing in which:- Fig 1 is a schematic drawing of the apparatus. The apparatus comprises an input line 1 for PCB or other polyhalogenated organic chemical waste, a storage tank 2 for such waste, a line 3 between tank 2 and a reservoir 4, a storage tank 6 for solvent (usually isopropanol), a line 7 between tank 6 and the reservoir 4, a storage tank 8 for aqueous alkali and a line 9 between tank 8 and the reservoir 4. The apparatus further comprises a storage tank 21 for hydrogen gas, a line 22 between the reservoir 4 and UV treatment chambers 24 and fitted with a circulating pump 23, a line 26 connecting the tank 21 to the UV treatment chambers 24 and a line 27 connecting the outputs of the chambers 24 with the reservoir 4. In use the pump 23 will circulate fluid through the UV treatment chambers 24. The reservoir 4 is also connected to a condenser 28 via a line 29. A return line 31 for condensate is provided and a line 32 for recycling hydrogen to the tank 21 is provided. Connected to the line 22 is a line 38 for passing fluid treated to the desired extent in the UV treatment chambers 24 to a separation section. The line 38 is provided with a non-return valve 37. The separation section comprises a phase separator 41, a line 42 for returning aqueous alkali to the tank 8 via a one way valve 45, a transfer line 43 for passing the solvent, usually isopropanol, to an evaporator 44, a line 46 for passing vaporised solvent to a condenser 47 and a line 48 for recycling solvent to the tank 8. PCB material is transferred from the evaporator 44 via a line 51 fitted with a non-return valve 52 to a biological degradation section. The biological degradation section comprises a bioreactor 53 to which a culture medium is supplied from a tank 54 via line 56 and pump 57 and with return line 58. An air supply 59 and supply line 61 for the bioreactor 53 is also provided. Air from the bioreactor 53 is passed via line 62 to a scrubber 63 from where clean air may pass out as 64 and liquid material may be returned to the bioreactor via line 66. Waste sludge may pass from the bioreactor via line 67 via a one way valve 68 to a solvent extraction apparatus 69 and liquid from the bioreactor 53 can be passed to that solvent extraction apparatus 69 by a line 71 fitted with a one way valve 72. Remaining PCB waste extracted in the solvent extraction apparatus may be returned to the tank 2 via line 73 and non-­ toxic waste can exit at 74. The preferred form and manner of use of the above apparatus is given below by way of Example. EXAMPLE 1 The waste material to be destroyed is either fed directly into the bioreactor 53 (if already of sufficiently low percent halogenation) or dissolved in isopropanol from tank 2 to a level of 1%-10%w/v. Aqueous NaOH, 8% - 40%w/v, is added from tank 8 to form a two phase mixture. Typical ratios used for the treatment of polychlorinated biphenyls (PCB) would be, per litre, 10ml of PCB in 740ml of isopropanol, and 25g of NaOH in 250ml aqueous solution. On mixing and settling two clear phases are formed: a larger, less dense organic phase and a smaller, denser aqueous phase. This mixture is pumped through the UV treatment chambers 24 apparatus containing low-pressure mercury lamps with peak emission at 180 nm and/or 254 nm light along with a high flux of hydrogen gas (50-60ml/minute or 4-5 ml per minute per gram or per ml of PCB). The effluent gas is passed through the condensor 28 and trapped solvent and PCB is recycled. The hydrogen itself is also recycled (therefore pre-condensation of vapours may be omitted). When sufficient dehalogenation has been achieved (for example, when PCB has been converted into a mixture consisting almost entirely of biphenyl, monochlorobiphenyls and dichlorobiphenyls), the mixture is withdrawn and the aqueous phase removed in the phase separator 41. This may be re-used, or the alkali and any contaminating PCB extracted and recycled. The organic phase is then transferred to the evaporator 44 and the solvent evaporated off and recycled. The PCB may then be further extracted free of salts and alkali using partitioning between hexane and water, or used directly in the bioreactor 53. The bioreactor 53 may be of any suitable type, including free cells or immobilized cells in a stirred tank, column or fluidized bed. The preferred method is to use immobilized cells, serated in a tank or fluidized bed. The cells may be one or a mixture of several bacterial strains isolated from the environment by standard enrichment techniques, obtained from culture collections, and/or improved by standard genetic or recombinant DNA techniques. For PCB degradation, this strain or strains would be capable of degrading biphenyl and oligochlorinated biphenyls completely to carbon dioxide, water and chloride ions. Ability to degrade PCBs with several chlorines is advantageous for siding the destruction of residual PCBs, but is not necessary for the process. The immobilized cells are re-used until performance degrades. Effluent during treatment and discarded bioreactor material are treated by solvent extraction in the apparatus 69, to recover any unused PCBs or metabolites, which are then recycled. Waste biomass may be further used as a fermentation feedstock or source of fertilizer. EXAMPLE II Dechlorination of Aroclor 1260 by UV process Method: 790ml isopropanol, 12ml PCB, 400ml 20% (w/v) aqueous NaOH. Hydrogen flow rate 50ml/min. PCBs were analyzed using wide-bore capillary gas chromatography using both ECD (electron capture detector) and FID (flame ionization detector) detectors using standard techniques. The FID traces were used to calculate the percentages of each class of compound. BP=biphenyl, MCB=monochlorobiphenyl, DCB=dichlorobiphenyl, PCB=all compounds with longer retention time than DCB. The UV treatment chamber 24 used in this instance comprised an inner tube containing a UV lamp having an output at the tube exterior surface of 29, 000 microwatt/square cm. The tube had a diameter of 2.4cm, effective length of 25cm and effective surface area of 196 square cm and was surrounded by a stainless steel tube of 6cm diameter and length 25cm. The annulus between the two tubes had a volume of about 640ml. The volume of circulating solvent, PCB and aqueous alkal was about 1200 ml. The PCB was, as stated, about 12ml. From the above it can be calculated that the total output of the lamp was about 5, 684 milliwatt and over an 8 hour treatment time this is a total irradiation of 45,472 milliwatt hour. As 12ml of PCB was treated this is a rate of 3,789 milliwatt hour per ml of PCB. The UV absorbance of polyhalogenated organic chemicals is high. For example, we have measured the absorbance (254 nm, path length 1cm) of 10 ppm biphenyl in isopropanol at over 1; that is 90% of UV light of 254 nm is absorbed per cm even in very dilute solutions. At the concentrations used in this invention the radiation is absorbed close to the lamp. Thus the depth of the liquid (the distance between the lamp and the vessel walls) is not critical provided that most of the UV light is absorbed over that distance ensuring efficient use of the lamp.It is preferred that the liquid flow is turbulent to ensure good exposure per molecule. Microbial strains useful for degradation of treated PCB Microbial stains suitable for degrading chlorinated and non-­ chlorinated biphenyl can be isolated from soils contaminated by PCBs using standard enrichment techniques. Alternatively, previously isolated stains can be obtained from culture collections. The following strains have been isolated from contaminated soils by biphenyl enrichment and have been found to metabolize rapidly biphenyl and monochlorobiphenyl. These have been deposited at the ATCC. Our strain identification numbers and provisional identifications are shown below. NCIB 10643 (Pseudomonas sp.) and NCIB 10504 (Flavobacterium sp.) are also known biphenyl-utilizing strains, though we do not know whether they degrade chlorinated biphenyl, NCIB is the National Collection of Industrial Bacteria (U.K.) Other useful strains are the dichlorobenzoate-degrading strains Pseudomonas HCV(2,4) DCB (ATCC 31942) and Pseudomonas HCV(3,4) DCB (ATCC 31940) described in European Patent Application No. 85108991.4 (chlorobenzoic acids are common metabolites of chlorinated biphenyls). Examples of Microbial degradation of treated PCBs (1) A mixture of GCC 142, GCC 179, GCC 184 and GCC 190 were immobilized in 2% agar beads (average diameter <1 mm) and grown to saturation within the beads by incubation in rich medium (tryptone soya broth, Oxoid) with seration overnight. To a 50% slurry of washed beads in minimal salt medium containing 0.5% Twean 80 detergent was added treated, concentrated PCB to 0.1%. The treated PCB consisted of approximately 11% BP, 74% MCB and 15% DCB. After shaking at 30°C for 18 hr. the culture was acidified with 1% by volume of 70% percholric acid then extracted with ether and analyzed by GC. DCB was still present but all the BP and MCB had been destroyed. Control cultures grown under identical conditions but with killed bacteria showed only small losses of BP and MCB. Silylation of the ether phase by standard techniques revealed only minor amounts of chlorobenzoate, a metabolite of PCBs, indicating further metabolism was occurring. Similar results are found with free cells (ie, not immobilized) provided that the treated PCBs are first emulsified (for example, as a 5% emulsion in water before addition to the bacterial culture) by sonication or by an industrial emulsifier, to increase availability to the bacteria. The presence of detergent accelerates the rate of breakdown of the treated PCB but is not required. (2) GCC 128 was grown overnight in rich medium, washed and suspended at absorbance 3(815 nm) in minimal medium plus 0.5% Tween 80. A 3:1 mixture of treated PCB (MCB+BP) and untreated Aroclor 1242 as an internal standard was thoroughly emulsified and added to a concentration of 0.1%, and the culture was shaken at 30°C. After an induction period of about 2 hr during which little degradation occurred, total degradation of the treated PCB occurred in the next 2.5 hr, while no detectable degradation of more highly chlorinated species occurred. Subsequently added 0.1% of substrate was also completely degraded, with respect to BP and MCB, within 2-3 hr. Large amounts of chlorobenzoates were detected in the culture, however, indicating that simultaneous or subsequent treatment with other bacteria such as ATCC 31940 and ATCC 31942 would be desirable to completely degrade chlorinated species. The above process has the advantage that it combines the strengths, and compensates for the weaknesses, of each part. In the UV part, partial dehalogenation from many to few halogen substituents is more rapid than subsequent total dehalogenation; also, the final products may be undesirable. In contrast, while micro-organisms capable of rapidly degrading organics with a few halogen substituents may readily be isolated from the environment, ones capable of rapid and at least substantially complete degradation of highly halogenated compounds are not. The claims form part of the disclosure of this specification.

Claims: 1. A process for degradation of a polyhalogenated organic compound comprising irradiating a polyhalogenated organic compound with ultra-violet light to produce a lesser halogenated organic compound and thereafter biologically degrading said lesser halogenated organic compound. 2. A process for degradation of a polyhalogenated organic compound as claimed in claim 1, wherein said irradiation is performed to incompletely dehalogenate said polyhalo­ genated organic compound. 3. A process for degradation of a polyhalogenated organic compound as claimed in claim 1 or claim 2, wherein said polyhalogenated organic compound is in a liquid medium during said irradiation in an amount of at least 1,000 ppm. 4. A process for degradation of a polyhalogenated organic compound as claimed in any one of claims 1 to 3, wherein said polyhalogenated organic compound in a liquid medium is subjected to at least 1,000 milliwatt hours of ultra-­ violet radiation per gm of said polyhalogenated organic compound. 5. A process for degradation of a polyhalogenated organic compound as claimed in any one of claims 1 to 3, wherein said polyhalogenated organic compound in a liquid medium is subjected to 50 to 1,000 milliwatt hours of ultra-­ violet radiation per square cm of a surface of said medium while the depth and/or volume of said medium are such that the area irradiated is from 10 to 25 square cm per gm polyhalogenated compound. 6. A process for degradation of a polyhalogenated organic compound as claimed in any one of claims 3 to 5, wherein said liquid medium is comprised of two substantially immiscible phases. 7. A process for degradation of a polyhalogenated organic compound as claimed in claim 6, wherein one of said phases is an aqueous phase and the other of said phases is an organic solvent for said polyhalogenated organic compound. 8. A process for degradation of a polyhalogenated organic compound as claimed in claim 7, wherein said organic solvent is a polar solvent. 9. A process for degradation of a polyhalogenated organic compound as claimed in claim 8, wherein said aqueous phase is a solution such as to be substantially immiscible with the organic solvent. 10. A process for degradation of a polyhalogenated organic compound as claimed in claim 9, wherein said solution contains an alkali. 11. A process for degradation of a polyhalogenated organic compound as claimed in claim 10, wherein said alkali is present as at least 8% and preferably at least 10% by weight in said aqueous phase. 12. A process for degradation of polyhalogenated organic compound as claimed in claim 8, wherein said organic solvent is an alcohol. 13. A process as claimed in any preceding claim, wherein the biological degradation is performed using an organism adapted to degrade said lesser halogenated compound but not adapted to substantially effectively degrade said polyhalogenated compound.

Inventors: CRAIG, ROBIN, EVERS, DENNIS
Applicants: BIOTOX PTY. LIMITED
Application year: 1987
Main classification: A62D3
IPC codes: A62D3, A62D101, B01J19, C10G32