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Applied and Environmental Microbiology, November 2002, p. 5336-5341, Vol. 68, No. 11
0099-2240/02/$04.00+0     DOI: 10.1128/AEM.68.11.5336-5341.2002
Copyright © 2002, American Society for Microbiology. All Rights Reserved.

Biodegradation of Hexahydro-1,3,5-Trinitro-1,3,5-Triazine and Its Mononitroso Derivative Hexahydro-1-Nitroso-3,5-Dinitro-1,3,5-Triazine by Klebsiella pneumoniae Strain SCZ-1 Isolated from an Anaerobic Sludge

Jian-Shen Zhao, Annamaria Halasz, Louise Paquet, Chantale Beaulieu, and Jalal Hawari^*

Biotechnology Research Institute, National Research Council of Canada, Montreal, Quebec H4P 2R2, Canada

Received 15 May 2002/ Accepted 9 August 2002

Top Abstract Introduction Materials and Methods Results and Discussion References

 
In previous work, we found that an anaerobic sludge efficiently degraded hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX), but the role of isolates in the degradation process was unknown. Recently, we isolated a facultatively anaerobic bacterium, identified as Klebsiella pneumoniae strain SCZ-1, using MIDI and the 16S rRNA method from this sludge and employed it to degrade RDX. Strain SCZ-1 degraded RDX to formaldehyde (HCHO), methanol (CH₃OH) (12% of total C), carbon dioxide (CO₂) (72% of total C), and nitrous oxide (N₂O) (60% of total N) through intermediary formation of methylenedinitramine (O₂NNHCH₂NHNO₂). Likewise, hexahydro-1-nitroso-3,5-dinitro-1,3,5-triazine (MNX) was degraded to HCHO, CH₃OH, and N₂O (16.5%) with a removal rate (0.39 µmol · h^-1 · g [dry weight] of cells^-1) similar to that of RDX (0.41 µmol · h^-1 · g [dry weight] of cells^-1) (biomass, 0.91 g [dry weight] of cells · liter^-1). These findings suggested the possible involvement of a common initial reaction, possibly denitration, followed by ring cleavage and decomposition in water. The trace amounts of MNX detected during RDX degradation and the trace amounts of hexahydro-1,3-dinitroso-5-nitro-1,3,5-triazine detected during MNX degradation suggested that another minor degradation pathway was also present that reduced NO₂ groups to the corresponding NO groups.

Top Abstract Introduction Materials and Methods Results and Discussion References

 
Hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) is a widely used explosive that severely contaminates soil and groundwater (13, 22). RDX has been found to be toxic in various terrestrial and aquatic environments (26, 29). The toxicity of cyclic nitramines means that contaminated soil and groundwater must be remediated, preferably by bioremediation. Biodegradation of RDX with anaerobic sludge was extensively studied by McCormick et al. (21) and Kaplan (19), who proposed a pathway based on the sequential reduction of RDX to hexahydro-1-nitroso-3,5-dinitro-1,3,5-triazine (MNX), hexahydro-1,3-dinitroso-5-nitro-1,3,5-triazine (DNX), and hexahydro-1,3,5-trinitroso-1,3,5-triazine (TNX). It was proposed that the nitroso compounds undergo further transformation to hydroxylamino derivatives (HOHN-RDX), which are subsequently cleaved to produce formaldehyde (HCHO), methanol (CH₃OH), hydrazine (NH₂NH₂), and dimethyl hydrazine [(H₃C)₂NNH₂].

Other research groups have employed mixed anaerobic microbial cultures that have included methanogens (1, 2), acetogens (4), nitrate reducers (12), and individual isolates such as isolates of Desulfovibrio sp. (5), Clostridium bifermentans (25) Providencia rettgeri (20), Citrobacter freundii (20), Morganella morganii (20), and Serratia marcescens (31) to biotransform RDX, but in most cases no clear details concerning ring cleavage products or mineralization were provided in the descriptions. Subsequent work in our laboratory (14, 15, 16) showed that RDX could be degraded in anaerobic sludge via intermediary formation of methylenedinitramine (O₂NNHCH₂NHNO₂), which decomposes in water to nitrous oxide (N₂O) and HCHO. Recently, Oh et al. (23) confirmed the formation of O₂NNHCH₂NHNO₂ during RDX degradation with anaerobic sludge. Despite these previous efforts, there is still insufficient information regarding the roles of individual anaerobic isolates and their products during RDX degradation. Without these details, particularly details concerning specific initial enzymatic reactions and their products, it will be difficult to understand degradation pathways and to optimize degradation towards mineralization.

The objective of the present study was to investigate degradation of RDX by an RDX-mineralizing strain, Klebsiella pneumoniae strain SCZ-1, which was isolated from the anaerobic sludge that was successfully used previously to degrade this energetic chemical (14, 16). We also used this strain to degrade MNX, an RDX degradation metabolite, under the same conditions that were used for the RDX degradation in an attempt to provide new insight into the anaerobic degradation pathway of cyclic nitramine explosives.

Top Abstract Introduction Materials and Methods Results and Discussion References

 
Chemicals.
RDX (99% pure) and L-[U-¹⁴C]RDX (chemical purity, >98%; radiochemical purity, 96%; specific radioactivity, 28.7 µCi · mmol^-1) were provided by Defense Research and Development Canada, Quebec, Canada (3). TNX (99% pure) was synthesized by the method described by Brockman et al. (7). H¹⁴CHO (specific activity, 53 mCi · mmol^-1) was obtained from Aldrich, Oakville, Ontario, Canada. MNX (98% pure) was provided by R. J. Spanggord of SRI International (Menlo Park, Calif.). Methylenedinitramine was purchased from the rare chemical department of Aldrich. All other chemicals used were reagent grade.

Media.
The medium used for isolation of anaerobic bacteria was 5.8% Difco anaerobic agar (Becton Dickinson, Sparks, Md.). The YPG medium (pH 7.3) used for fermentative bacterial growth and RDX degradation contained (per liter of basic salts medium) 3.0 g of yeast extract, 0.6 g of Bacto Peptone (Difco), and 1.0 g of glucose. The basic salts medium was prepared as described previously (30), except that no (NH₄)₂SO₄ was added and (NH₄)₆Mo₇O₂₄ · 4H₂O was replaced with NaMoO₄ · 2H₂O. YPS agar was prepared as described by Zhao et al. (32). Liquid media were sterilized either by autoclaving at 120°C for 20 min or by filtration with sterile filters (pore size, 0.22 µm; Millex GP; Millipore, Bedford, Mass.) for trace metals and the glucose stock solution. The dry serum bottles used were sterilized by autoclaving them at 120°C for 60 min.

Bacterial isolation and characterization.
A methanogenic industrial sludge was obtained from Sensient Flavor Canada (Cornwall, Ontario, Canada) and was incubated on Difco anaerobic agar plates at 37°C under an atmosphere containing a mixture of H₂ and CO₂ (GasPak Plus; BBL, Sparks, Md.). Anaerobic conditions were monitored with a BBL indicator (VWR Canlab, Mississauga, Ontario, Canada). One strain, SCZ-1, was selected for subsequent characterization due to its high growth rate under both aerobic and anaerobic conditions and its capacity to mineralize RDX anaerobically. As determined by the Sherlock microbial identification system (MIDI, Newark, Del.), strain SCZ-1 was closely related to Klebsiella pneumoniae, with a similarity index of 0.9. As determined by the 16S rRNA identification method (18), the gene sequence of a 0.7-kb fragment (representing one-half of the total length of the gene) of the 16S rRNA gene from the isolate was 99% similar to the K. pneumoniae sequence.

Bacterial growth and biodegradation tests.
By using a procedure described previously (16), serum bottles (60 ml), each containing 18.5 ml of YPG medium and 106 µM RDX, were made anaerobic by repeated degassing under a vacuum and charging with filter-sterilized oxygen-free nitrogen or argon. The sealed bottles were then inoculated with 1.5 ml of an aerobic liquid culture (initial optical density at 600 nm [OD₆₀₀], 0.15) of strain SCZ-1 and incubated in a rotatory shaker (200 rpm) at 37°C. After 3 h of anaerobic incubation, the bacterial growth reached a maximum OD₆₀₀ of 0.7 (0.91 g [dry weight] of cells per liter). We measured the redox potential (E_h) with a Pt/Ag/AgCl electrode (Fisher Scientific, Montreal, Canada) and found that it decreased from 200 to -300 mV during this incubation period (meanwhile the pH decreased from 7.3 to 6.3). MNX (100 µM) and TNX (100 µM) biodegradation tests were conducted under the same conditions that were used for the RDX degradation tests. Separate bottles were used for monitoring production of either aqueous metabolites or N₂O. For sampling, sterile syringes and needles washed with reduced buffer were used. Some microcosms were spiked with L-[U-¹⁴C]RDX (0.038 µCi) to measure mineralization (liberated ¹⁴CO₂) with a Tri-Carb 4530 liquid scintillation counter (model 2100 TR; Packard Instrument Company, Meriden, Conn.) (16). When ¹⁴CO₂ ceased to form in a microcosm, the microcosm was sacrificed to measure the remaining radioactivity in the culture supernatant and in the biomass. A similar procedure was used to mineralize HCHO (166 µM) supplemented with H¹⁴CHO (0.030 µCi).

RDX and metabolite analyses.
The concentrations of RDX and its nitroso products MNX, DNX, and TNX (in the aqueous phase obtained by centrifugation at 9,000 x g for 3 min) were analyzed at 230 nm by a high-performance liquid chromatography-UV method as described previously (16). The methods used for analyses of methylenedinitramine, (methyl)hydrazines, N₂O (14, 16), and HCHO (11, 28) have also been described previously. CH₃OH was measured by gas chromatography with a flame ionization detector (HP 6890) by using a Hayesep Q micropacked column (2 m by 0.03 mm; Supelco, Bellefonte, Pa.) (detection limit, 0.25 ppm). Nitrite was analyzed by U.S. Environmental Protection Agency method 345.1 (10), which has a detection limit of 10 ppb. Ammonia was analyzed by an enzymatic assay in which L-glutamate dehydrogenase and NADPH (Sigma, St. Louis, Mo.) were used. All tests were performed in triplicate.

Top Abstract Introduction Materials and Methods Results and Discussion References

 
Isolation of strain SCZ-1.
An anaerobic RDX-mineralizing bacterium, strain SCZ-1, was isolated from the anaerobic sludge that was previously used to degrade RDX (14, 16). Strain SCZ-1 is a nonmotile, non-spore-forming, gram-negative, rod-shaped, facultatively anaerobic bacterium. Under aerobic and anaerobic conditions, strain SCZ-1 grew on glucose and peptone, but it did not grow when RDX was used as a sole source of carbon or nitrogen. On the basis of MIDI and 16S rRNA data, we identified strain SCZ-1 as K. pneumoniae.

RDX degradation with strain SCZ-1.
We found that strain SCZ-1 grew better aerobically but degraded RDX only under anaerobic conditions in the presence of glucose and peptone. K. pneumoniae strain SCZ-1 degraded RDX at a rate of 0.41 µmol · h^-1 · g (dry weight) of cells^-1, which was lower than the rate observed with the mixed anaerobic culture (10 µmol · h^-1 · g [dry weight] of cells^-1) (16). On the other hand, the rate of removal of RDX with strain SCZ-1 (9.0 µM · day^-1) (biomass OD₆₀₀, 0.7) is comparable to removal rates previously reported for other facultatively anaerobic organisms, such as M. morganii (12.1 µM · day^-1), P. rettgeri (12.1 µM · day^-1), C. freundii (7.3 µM · day^-1; biomass OD₅₈₀, 1.6 to 1.8) (20), and S. marcescens (20.4 µM · day^-1; biomass unknown) (31). The previously described pure anaerobic cultures exhibited only low RDX mineralization activity (Table 1). In contrast, strain SCZ-1 could mineralize 72% of RDX (Fig. 1A).

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TABLE 1. Comparison of RDX mineralization values and maximal nitroso metabolite yields obtained with pure anaerobic bacterial isolates

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FIG. 1. Anaerobic degradation of 106 µM RDX with K. pneumoniae strain SCZ-1. (A) Live cells (initial biomass, 0.15 OD600 unit; maximal growth, 0.7 OD600 unit or 0.9 g [dry weight] of cells · liter-1). (B) Killed cells (initial biomass, 0.15 OD600 unit).

Removal of RDX by strain SCZ-1 was accompanied by formation of several products, including N₂O (60%), HCHO, CO₂ (72%), and CH₃OH (12%) (Fig. 1A). In controls containing RDX and killed cells, approximately 10% of the RDX was degraded (hydrolyzed) and nitrite accumulated (Fig. 1B). Nitrite was not seen in RDX degradation experiments when live strain SCZ-1 was used, and this was attributed to the bacterial conversion of nitrite to ammonia. For instance, when we incubated a standard solution of sodium nitrite (130 µM) with strain SCZ-1, the anion disappeared at a rate of 128 µmol · h^-1 · g (dry weight) of cells^-1, which was more than 300 times higher than the rate of RDX removal (0.41 µmol · h^-1 · g [dry weight] of cells^-1). Unfortunately, we were unable to quantify ammonia because relatively large amounts of it were released from YPG medium. Strain SCZ-1 did not degrade RDX in basic salts medium with RDX added as a carbon or nitrogen source; thus, we were unable to quantify ammonia production from RDX degradation. Other potential N-containing products, such as hydrazine and dimethyl hydrazines, which were reported by McCormick et al. (21), were not detected in the present study.

HCHO did not accumulate and was mineralized. For instance, when we incubated a reference standard of HCHO spiked with H¹⁴CHO with strain SCZ-1, we observed more than 85% mineralization (¹⁴CO₂) in less than 20 h (Fig. 2). Figure 2 clearly shows that long after the removal of the aldehyde CO₂ continued to form slowly.

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FIG. 2. Anaerobic mineralization of 169 µM HCHO with K. pneumoniae strain SCZ-1 culture supplemented with 0.03 µCi of H14CHO. The biomass was the same as that described in the legend to Fig. 1.

Using liquid chromatography-mass spectrometry with negative electron spray ionization, we were able to identify methylenedinitramine as a key ring cleavage intermediate, and spontaneous decomposition of this compound gave N₂O and HCHO, as reported previously (14). Furthermore, we detected trace amounts of MNX, but we were unable to detect DNX or TNX. The product distribution described above is strikingly similar to that obtained during RDX incubation with the anaerobic sludge, indicating that there are similarities between the degradation pathways in the two cases (see below).

Stoichiometry of RDX degradation.
Conversion of 2.1 µmol of RDX (106 µM) produced 3.8 µmol of N₂O, representing 60% of the total N content of RDX (4 N atoms) (Fig. 1A). Methylenedinitramine (O₂NNHCH₂NHNO₂), a key intermediate during degradation of RDX by strain SCZ-1, is the main source of N₂O. It has been demonstrated previously that 1 mol of O₂NNHCH₂NHNO₂ decomposes quantitatively in water at pH 7 and 30°C to produce 2 mol of N₂O and 1 mol of HCHO (14). The stoichiometry of N₂O formation supported our belief that methylenedinitramine, which has two NH-NO₂ groups, was responsible for the quantitative formation of N₂O from RDX in strain SCZ-1 (14).

Conversion of 106 µM RDX also produced 39 µM CH₃OH, representing 12% of the total carbon in transformed RDX (Fig. 1A). Using L-[U-¹⁴C]RDX as the substrate, we found that strain SCZ-1 mineralized 72% of the total carbon in RDX (liberated ¹⁴CO₂) over 36 days (Fig. 1A). Most of the remaining radioactivity (27%) was in the aqueous phase of the culture medium, and less than 0.5% of the RDX carbon was in biomass, which left roughly 15% of the carbon content of RDX unaccounted for. However, slow release of CO₂ was still occurring long after the complete disappearance of RDX (Fig. 1A).

MNX and TNX degradation.
When we incubated MNX (100 µM) with live cells of strain SCZ-1, the compound was degraded at an initial rate of 0.39 µmol · h^-1 · g (dry weight) of cells^-1 (Fig. 3A), which was close to the rate of RDX degradation under the same conditions (0.41 µmol · h^-1 · g [dry weight] of cells^-1). The MNX transformation products were N₂O, CH₃OH, and HCHO (Fig. 3A) and thus were similar to those of RDX. However, removal of 2 µmol of MNX produced only 1.0 µmol of N₂O (17% of the total N content of MNX) (Fig. 3A), compared to production of 3.8 µmol of N₂O (60% of the total N content of RDX) from 2.1 µmol of RDX (Fig. 1A). Another notable observation is the detection of a small amount of DNX after MNX degradation; however, no TNX was detected. During MNX degradation we did not observe formation of O₂NHNCH₂NHNO₂, the key intermediate during RDX degradation by strain SCZ-1.

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FIG. 3. Anaerobic degradation of MNX (2.0 µmol in 20 ml) with K. pneumoniae strain SCZ-1. (A) Live cells. (B) Killed cells. The biomass was the same as that described in the legend to Fig. 1.

In controls containing killed cells (Fig. 3B), MNX decomposed at a rate of 0.16 µmol · h^-1 · g (dry weight) of cells^-1, which was almost one-half its rate of removal in the presence of live cells (0.39 µmol · h^-1 · g [dry weight] of cells^-1), indicating that MNX was not a stable compound and underwent hydrolysis in water (Fig. 3B). Abiotic degradation of each 1 mol of MNX released approximately 1 mol of nitrite.

When we incubated the trinitroso derivative TNX (100 µM) under the same conditions, we found that the compound was converted much more slowly than either RDX or MNX. The rate of removal of TNX (0.07 µmol · h^-1 · g [dry weight] of cells^-1) was six times lower than that of MNX (0.39 µmol · h^-1 · g [dry weight] of cells^-1) or that of RDX (0.41 µmol · h^-1 · g [dry weight] of cells^-1). In controls with killed cells, TNX was not degraded. It has been reported frequently that TNX tends to accumulate during RDX biodegradation (20, 21, 23, 27, 31).

Pathway(s) of RDX degradation: initial denitration versus nitroso formation.
Based on the product distribution described above, we propose an RDX degradation pathway in K. pneumoniae strain SCZ-1 (Fig. 4). The RDX degradation pathway in this isolate is similar to the pathway(s) described previously for anaerobic sludge in that both involve methylenedinitramine as a ring cleavage intermediate (14, 16). Here we suggest that there is an important initial denitration step during RDX degradation that leads to ring cleavage and decomposition (Fig. 4, path a). The fact that oxygen completely quenched RDX removal by strain SCZ-1 supports the belief that an O₂-sensitive reaction involving transfer of one electron to an NO₂ group in RDX might initiate degradation. Such a process would produce an unstable radical anion, RDX^·- (compound I), whose denitration could produce the unstable radical RDX (compound II). Subsequent reaction of compound II via abstraction would give the amine (compound III), or subsequent reaction of compound II via elimination of an H atom would give the monounsaturated intermediate (compound IV) (6, 17, 24). Methylenedinitramine is one of the expected products of decomposition of compound III or IV. The N denitration mechanism suggested in the present RDX study is similar to the mechanism reported previously for N denitration of nitramines by dihydronicotinamide (8). In the latter case, cleavage of an N-NO₂ bond proceeds via a one-electron transfer process (8). Also, N denitration of RDX to compound IV has frequently been reported during alkaline hydrolysis (9, 17), in which the latter compound is found to decompose with a rate constant (k) that is 10⁵ times larger than that of RDX (17).

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FIG. 4. Postulated routes for anaerobic degradation of RDX and MNX by K. pneumoniae strain SCZ-1. Compounds in brackets were not detected in this study. MeOH, methanol.

Sequential reduction of the nitro group(s) (NO₂) in RDX to the corresponding nitroso (NO) derivative(s) did not seem to be a major degradation route for strain SCZ-1. If the sequential reduction of NO₂ to NO is an important degradation pathway for RDX, then one might expect the accumulation of TNX (Fig. 4, path a), which we did not observe in the present study. As discussed above, TNX was degraded at a rate much lower than the rates of degradation of MNX and RDX with strain SCZ-1. In addition, we observed only traces of MNX during RDX degradation and traces of DNX during MNX degradation. Likewise, we suggest that MNX was also degraded mainly by initial denitration prior to ring cleavage (Fig. 4, path b). The absence of methylenedinitramine during MNX degradation supports the hypothesis that one of the two nitro functional groups (NO₂) in MNX might be removed prior to ring cleavage, leaving the compound unable to act as a precursor to methylenedinitramine.

In conclusion, we found that a facultatively anaerobic bacterium isolated from an anaerobic sludge mineralized RDX predominantly via initial denitration, whereas reduction of the nitro group of RDX to the corresponding nitroso products was a minor secondary reaction. Although the isolated strain improved our understanding of the pathways involved in the degradation of cyclic nitramines, use of this organism in remedial applications might not be practical because of a low rate of degradation. However, the high level of mineralization observed during RDX degradation should encourage us to optimize various physiological parameters to enhance the rate of degradation of RDX.

 
We thank Kevin Orouke of Sensient Flavor Canada for providing the anaerobic sludge. We are grateful to Sonia Thiboutot and Guy Ampleman of the Defense Research Establishment Valcartier, Quebec, Canada, for providing the energetic chemicals. We thank Jim Spain for valuable discussions, and we thank Carl Groom, Alain Corriveau, Stéphane Deschamps, and Philomena D'Cruz for technical assistance.

We thank the Natural Sciences and Engineering Research Council (NSERC) and the National Research Council (NRC) of Canada for granting a visiting fellowship to J.-S. Zhao. Funding was provided by the U.S. DoD/DoE/EPA Strategic Environmental Research and Development Program (grant SERDP CU1213).

 
* Corresponding author. Mailing address: Biotechnology Research Institute, National Research Council of Canada, 6100 Royalmount Ave., Montreal, Quebec H4P 2R2, Canada. Phone: (514) 496-6267. Fax: (514) 496-6265. E-mail: jalal.hawari{at}nrc.ca.

Top Abstract Introduction Materials and Methods Results and Discussion References

 

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Applied and Environmental Microbiology, November 2002, p. 5336-5341, Vol. 68, No. 11
0099-2240/02/$04.00+0     DOI: 10.1128/AEM.68.11.5336-5341.2002
Copyright © 2002, American Society for Microbiology. All Rights Reserved.

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