Hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) Biodegradation in Liquid and Solid-State Matrices by Phanerochaete chrysosporium

Extensive biodegradation of hexahydro-1,3,5 -trinitro-1,3,5 -triazine (RDX) by the white-rot fungus Phanerochaete chrysosporium in liquid and solid matrices was observed. Some degradation in liquid occurred under nonligninolytic conditions, but was approximately 10 times higher under ligninolytic conditions. Moreover, elimination was accounted for almost completely as carbon dioxide. No RDX metabolites were detected. The degradation rates in liquid appeared to be limited to RDX concentration in solution (approximately 80 mg/L), but degradation rates in soil were nonsaturable to 250 mg/kg. Manganese-dependent peroxidase (MnP) and cellobiose dehydrogenase (CDH) from P. chrysosporium, but not lignin peroxidase, were able to degrade RDX. MnP degradation of RDX required addition of manganese, but CDH degraded RDX anaerobically without addition of mediators. Attempts to improve biodegradation by supplementing cultures with micronutrients showed that addition of manganese and oxalate stimulated degradation rates in liquid, sawdust, and sand by the fungus, but not in loam soil. RDX degradation by P. chrysosporium in sawdust and sand was better than observed in liquid. However, degradation in solid matrices by the fungus only began after a lag period of 2 to 3 weeks, during which time extractable metabolites from wood were degraded.     

Biodegradation of hexahydro-1,3,5-trinitro-1,3,5-triazine by novel fungi isolated from unexploded ordnance contaminated marine sediment

Undersea deposition of unexploded ordnance (UXO) constitutes a potential source of contamination of marine environments by hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) and octahydro-1,3,5,7-tetranitro-1,3,5,7-tetrazocine (HMX). Using sediment from a coastal UXO field, Oahu Island, Hawaii, we isolated four novel aerobic RDX-degrading fungi HAW-OCF1, HAW-OCF2, HAW-OCF3 and HAW-OCF5, tentatively identified as members of Rhodotorula, Bullera, Acremonium and Penicillium, respectively. The four isolates mineralized 15–34% of RDX in 58 days as determined by liberated ¹⁴CO₂. Subsequently we selected Acremonium to determine biotransformation pathway(s) of RDX in more details. When RDX (100 μM) was incubated with resting cells of Acremonium we detected methylenedinitramine (MEDINA), N₂O and HCHO. Also we detected hexahydro-1-nitroso-3,5-dinitro-1,3,5-triazine (MNX) together with trace amounts of hexahydro-1,3-dinitroso-5-nitro-1,3,5-triazine (DNX) and hexahydro-1,3,5-trinitroso-1,3,5-triazine (TNX). Under the same conditions MNX produced N₂O and HCHO together with trace amounts of DNX and TNX, but we were unable to detect MEDINA. TNX did not degrade with Acremonium. These experimental findings suggested that RDX degraded via at least two major initial routes; one route involved direct ring cleavage to MEDINA and another involved reduction to MNX prior to ring cleavage. Nitrite was only detected in trace amounts suggesting that degradation via initial denitration did take place but not significantly. Aerobic incubation of Acremonium in sediment contaminated with RDX led to enhanced removal of the nitramine.     

Biodegradation of the Hexahydro-1,3,5-Trinitro-1,3,5-Triazine Ring Cleavage Product 4-Nitro-2,4-Diazabutanal by Phanerochaete chrysosporium

Initial denitration of hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) by Rhodococcus sp. strain DN22 produces CO₂ and the dead-end product 4-nitro-2,4-diazabutanal (NDAB), OHCNHCH₂NHNO₂, in high yield. Here we describe experiments to determine the biodegradability of NDAB in liquid culture and soils containing Phanerochaete chrysosporium. A soil sample taken from an ammunition plant contained RDX (342 μmol kg⁻¹), HMX (octahydro-1,3,5,7-tetranitro-1,3,5,7-tetrazocine; 3,057 μmol kg⁻¹), MNX (hexahydro-1-nitroso-3,5-dinitro-1,3,5-triazine; 155 μmol kg⁻¹), and traces of NDAB (3.8 μmol kg⁻¹). The detection of the last in real soil provided the first experimental evidence for the occurrence of natural attenuation that involved ring cleavage of RDX. When we incubated the soil with strain DN22, both RDX and MNX (but not HMX) degraded and produced NDAB (388 ± 22 μmol kg⁻¹) in 5 days. Subsequent incubation of the soil with the fungus led to the removal of NDAB, with the liberation of nitrous oxide (N₂O). In cultures with the fungus alone NDAB degraded to give a stoichiometric amount of N₂O. To determine C stoichiometry, we first generated [¹⁴C]NDAB in situ by incubating [¹⁴C]RDX with strain DN22, followed by incubation with the fungus. The production of ¹⁴CO₂ increased from 30 (DN22 only) to 76% (fungus). Experiments with pure enzymes revealed that manganese-dependent peroxidase rather than lignin peroxidase was responsible for NDAB degradation. The detection of NDAB in contaminated soil and its effective mineralization by the fungus P. chrysosporium may constitute the basis for the development of bioremediation technologies.     

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

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 (CO(2)) (72% of total C), and nitrous oxide (N2O) (60% of total N) through intermediary formation of methylenedinitramine (O(2)NNHCH(2)NHNO(2)). 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 micromol. h(-1). g [dry weight] of cells(-1)) similar to that of RDX (0.41 micromol. 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.     

Fungal interactions with the explosive RDX (hexahydro-1,3,5-trinitro-1,3,5-triazine)

The bacterially mediated, anaerobic biodegradation of the explosive RDX (hexahydro 1,3,5 trinitro-1,3,5-triazine) is well established. Reports of successful mineralization of RDX by white rot fungi, and the enhanced transformation of RDX in stirred as compared to static composts, led us to study the possible aerobic role of several filamentous fungi in RDX biodegradation.Cladosporium resinae, Cunninghamella echinulata varelegans, Cyathus pallidus andPhanerochaete chrysosporium were grown in the presence of 50 and 100 g ml^–1 of RDX on a vegetable juice agar. Little inhibition of radial growth was observed, while control cultures with TNT exhibited substantial inhibition. When 100 g ml^–1 of RDX was added to pre-grown mycelia in a nonlignolytic liquid medium, between 12 and 31% was lost after 3 days. In similar experiments using¹⁴C-RDX, most of the label remained in the organic fraction, and little or none was found in the aqueous fraction, the volatile fraction or incorporated into cell walls. Although disappearance of RDX was observed for all four species tested, there was no evidence of mineralization. Mixed cultures of microorganisms, including both bacteria and fungi, merit further study as agents for the decontamination of munitions-contaminated soils.     

Mineralization of the cyclic nitramine explosive hexahydro-1,3,5-trinitro-1,3,5-triazine by Gordonia and Williamsia spp

Hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) is a cyclic nitroamine explosive that is a major component in many military high-explosive formulations. In this study, two aerobic bacteria that are capable of using RDX as the sole source of carbon and nitrogen to support their growth were isolated from surface soil. These bacterial strains were identified by their fatty acid profiles and 16S ribosomal gene sequences as Williamsia sp. KTR4 and Gordonia sp. KTR9. The physiology of each strain was characterized with respect to the rates of RDX degradation and [U-14C]RDX mineralization when RDX was supplied as a sole carbon and nitrogen source in the presence and absence of competing carbon and nitrogen sources. Strains KTR4 and KTR9 degraded 180 microM RDX within 72 h when RDX served as the only added carbon and nitrogen source while growing to total protein concentrations of 18.6 and 16.5 microg/ml, respectively. Mineralization of [U-14C]RDX to 14CO2 was 30% by strain KTR4 and 27% by KTR9 when RDX was the only added source of carbon and nitrogen. The addition of (NH4)2SO4- greatly inhibited KTR9's degradation of RDX but had little effect on that of KTR4. These are the first two pure bacterial cultures isolated that are able to use RDX as a sole carbon and nitrogen source. These two genera possess different physiologies with respect to RDX mineralization, and each can serve as a useful microbiological model for the study of RDX biodegradation with regard to physiology, biochemistry, and genetics.     

Trace level detection of hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) by microimmunosensor.

Reported in this paper is the development and characterization of a highly sensitive microcapillary immunosensor for the detection of the explosive, hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX). The immunosensor exploits antibodies as recognition elements for target antigens, fluorescence dye conjugates for reporter molecules and fused silica microcapillaries for its high surface-to-volume ratio. Detection of RDX with the microcapillary immunosensor requires covalent immobilization of anti-RDX antibodies on the inner core of the microcapillaries via heterobifunctional cross-linker chemistry. Subsequent saturation of all antibody binding domains follows with a synthetically prepared fluorescent analog of RDX. Displacement immunoassays were performed with the microcapillary immunosensor with the injection of unlabeled RDX at concentration levels from 1 part-per-trillion (pptr) to 1000 part-per-billion (ppb). As unlabeled RDX reaches the binding domain of the antibody, fluorescent RDX analog is displaced from the antibody, flows downstream and is measured by a spectrofluorometer. Fluorescence measurements of the displaced fluorescent RDX analog were equated to a standard calibration curve to quantify sample concentration. Complete evaluation of the RDX microcapillary immunosensor for selectivity and sensitivity was performed based on the following criteria: variable flow rates, antibody cross-reactivity, reproducibility and cross-linker (carbon spacer) comparison. Results indicate the lowest detectable limit (LDL) for RDX is 10 pptr (ng/l) with a linear dynamic range from 0.1 to 1000 ppb (ug/l).     

Degradation of hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) by Stenotrophomonas maltophilia PB1.

A mixed microbial culture capable of metabolizing the explosive RDX (hexahydro-1,3,5-trinitro-1,3,5-triazine) was obtained from soil enrichments under aerobic and nitrogen-limiting conditions. A bacterium, Stenotrophomonas maltophilia PB1, isolated from the culture used RDX as a sole source of nitrogen for growth. Three moles of nitrogen was used per mole of RDX, yielding a metabolite identified by mass spectroscopy and 1H nuclear magnetic resonance analysis as methylene-N-(hydroxymethyl)-hydroxylamine-N'-(hydroxymethyl)nitroamin e. The bacterium also used s-triazine as a sole source of nitrogen but not the structurally similar compounds octahydro-1,3,5,7-tetranitro-1,3,5,7-tetrazocine, cyanuric acid, and melamine. An inducible RDX-degrading activity was present in crude cell extracts.     

固定化白腐真菌降解水溶液中2,4-二氯酚的研究

研究固定化黄孢原毛平革菌对水溶液中2,4-二氯酚（2,4-DCP）的降解效果,探讨固定化黄孢原毛平革菌处理水溶液中氯酚类污染物的可行性．结果表明,采用固定化方法处理的白腐真菌．其产酶稳定性及酶活均比游离态白腐真菌有显著提高．2,4-DCP降解效果受固定化孢子接种量、pH值、摇床转速、2,4-DCP的初始浓度和表面活性剂浓度的影响．当pH为4．5,摇床转速180r／min,培养基含有1％的Tween 80,2,4-DCP初始浓度为40mg／L时,加入10mL固定化白腐真菌孢子,2,4-DCP去除效果最好．     

Biodegradation of the nitramine explosives hexahydro-1,3,5-trinitro-1,3,5-triazine and octahydro-1,3,5,7-tetranitro-1,3,5,7-tetrazocine in cold marine sediment under anaerobic and oligotrophic conditions

The in situ degradation of the two nitramine explosives, hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) and octahydro-1,3,5,7-tetranitro-1,3,5,7-tetrazocine (HMX), was evaluated using a mixture of RDX and HMX, incubated anaerobically at 10 degrees C with marine sediment from a previous military dumping site of unexploded ordnance (UXO) in Halifax Harbor, Nova Scotia, Canada. The RDX concentration (14.7 mg.L-1) in the aqueous phase was reduced by half in 4 days, while reduction of HMX concentration (1.2 mg.L-1) by half required 50 days. Supplementation with the carbon sources glucose, acetate, or citrate did not affect the removal rate of RDX but improved removal of HMX. Optimal mineralization of RDX and HMX was obtained in the presence of glucose. Using universally labeled (UL)-[14C]RDX, we obtained a carbon mass balance distributed as follows: CO2, 48%-58%; water soluble products, 27%-31%; acetonitrile extractable products, 2.0%-3.4%; and products covalently bound to the sediments and biomass, 8.9% (in the presence of glucose). The disappearance of RDX was accompanied by the formation of the mononitroso derivative hexahydro-1-nitroso-3,5-dinitro-1,3,5-triazine (MNX) and formaldehyde (HCHO) that subsequently disappeared. In the case of HMX, mineralization reached only 13%-27% after 115 days of incubation in the presence or absence of the carbon sources. The disappearance of HMX was also accompanied by the formation of the mononitroso derivative. The total population of psychrotrophic anaerobes that grew at 10 degrees C was 2.6 x 10(3) colony-forming units.(g sediment dry mass)-1, and some psychrotrophic sediment isolates were capable of degrading RDX under conditions similar to those used for sediments. Based on the distribution of products, we suggest that the sediment microorganisms degrade RDX and HMX via an initial reduction to the corresponding mononitroso derivative, followed by denitration and ring cleavage.     

Biotransformation of hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) by a prospective consortium and its most effective isolate Serratia marcescens

The biotransformation of hexahydro-1,3,5-trinitro-1,3,5 triazine (RDX) has been observed in liquid culture by a consortium of bacteria found in horse manure. Five types of bacteria were found to predominate in the consortium and were isolated. The most effective of these isolates at transforming RDX was Serratia marcescens. The biotransformation of RDX by all of these bacteria was found to occur only in the anoxic stationary phase. The process of bacterial growth and RDX biotransformation was quantified for the purpose of developing a predictive type model. Cell growth was assumed to follow Monod kinetics. All of the aerobic and anoxic growth parameters were determined: mu(max), K(s), and Y(x/s). RDX was found to competitively inhibit cell growth in both atmospheres. Degradation of RDX by Serratia marcescens was found to proceed through the stepwise reduction of the three nitro groups to nitroso groups. Each of these reductions was found to be first order in both component and cell concentrations. The degradation rate constant for the first step in this reduction process by the consortium was 0.022 L/g cells . h compared to 0.033 L/g cells . h for the most efficient isolate. (c) 1997 John Wiley & Sons, Inc. Biotechnol Bioeng 53: 515-522, 1997.     

Biodegradation of Rose Bengal by Phanerochaete chrysosporium

Rose Bengal (tetrachloro-tetraiodo-fluorescein) was not able to limit the spreading growth of the ligninolytic fungus, Phanerochaete chrysosporium in the presence of Tween 80, and when added to the 5 d old liquid cultures of this organism it was almost completely degraded in 5 h. Thin layer chromatography analysis showed the formation of a single degradation product.     

A DFT study of adsorption and decomposition of hexahydro-1,3,5-trinitro-1,3,5-triazine on Mg(0001) surface

The adsorption and decomposition of hexogen (RDX) molecule on the Mg(0001) surface were investigated by the generalized gradient approximation (GGA) of density functional theory (DFT). The calculations employed a supercell (4?×?4?×?4) slab model and three-dimensional periodic boundary conditions. The strong attractive forces between RDX molecule and magnesium atoms induce the RDX’s N???O bond breaking. Subsequently, the dissociated oxygen atoms and radical fragment of RDX oxidize the Mg surface. The largest adsorption energy is ?2104.0 kJ mol^-1. We also investigated the decomposition mechanism of RDX molecule on the Mg(0001) surface. The activation energy for the dissociation step of configuration V4 is as small as 2.5 kJ mol^-1, while activation energies of other configurations are much larger, in the range of 964.9–1375.1 kJ mol^-1. Mg powder is more active than Al powder, and Mg powder performs better in increasing the combustion exothermicity of RDX as well.     

Biodegradation of polycyclic hydrocarbons by Phanerochaete chrysosporium

The ability of the white rot fungus Phanerochaete chrysosporium to degrade polycyclic aromatic hydrocarbons (PAHs) that are present in anthracene oil (a distillation product obtained from coal tar) was demonstrated. Analysis by capillary gas chromatography and high-performance liquid chromatography showed that at least 22 PAHs, including all of the most abundant PAH components present in anthracene oil, underwent 70 to 100% disappearance during 27 days of incubation with nutrient nitrogen-limited cultures of this fungus. Because phenanthrene is the most abundant PAH present in anthracene oil, this PAH was selected for further study. In experiments in which [14C]phenanthrene was incubated with cultures of P. chrysosporium containing anthracene oil for 27 days, it was shown that 7.7% of the recovered radiolabeled carbon originally present in [14C]phenanthrene was metabolized to 14CO2 and 25.2% was recovered from the aqueous fraction, while 56.1 and 11.0% were recovered from the methylene chloride and particulate fractions, respectively. High-performance liquid chromatography of the 14C-labeled material present in the methylene chloride fraction revealed that most (91.9%) of this material was composed of polar metabolites of [14C]phenanthrene. These results suggest that this microorganism may be useful for the decontamination of sites in the environment contaminated with PAHs.     

Prediction of growth and biotransformation rates of hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) in the presence of barium

The biotransformation of explosives has been investigated by many researchers. Bioremediation of soil and water contaminated with hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) is becoming the method of choice for clean-up of a variety of sites. In this study, we investigated biotransformation of RDX in the presence of barium. Ba is a metal commonly found in combination with RDX at sites requiring remediation. RDX was biotransformed by both a consortium of bacteria and an isolate from the consortium under anoxic conditions using a rich medium. However, Ba inhibited cell growth under both aerobic and anoxic conditions and slowed biotransformation rates by 40%. RDX and Ba inhibited growth of the isolate more than growth of the consortium. An additive inhibition model is proposed that accurately predicts the reduced growth rates observed.     

Determination of key metabolites during biodegradation of hexahydro-1,3,5-trinitro-1,3,5-triazine with Rhodococcus sp. strain DN22.

Rhodococcus sp. strain DN22 can convert hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) to nitrite, but information on degradation products or the fate of carbon is not known. The present study describes aerobic biodegradation of RDX (175 microM) when used as an N source for strain DN22. RDX was converted to nitrite (NO(2)(-)) (30%), nitrous oxide (N(2)O) (3.2%), ammonia (10%), and formaldehyde (HCHO) (27%), which later converted to carbon dioxide. In experiments with ring-labeled [(15)N]-RDX, gas chromatographic/mass spectrophotometric (GC/MS) analysis revealed N(2)O with two molecular mass ions: one at 44 Da, corresponding to (14)N(14)NO, and the second at 45 Da, corresponding to (15)N(14)NO. The nonlabeled N(2)O could be formed only from -NO(2), whereas the (15)N-labeled one was presumed to originate from a nitramine group ((15)N-(14)NO(2)) in RDX. Liquid chromatographic (LC)-MS electrospray analyses indicated the formation of a dead end product with a deprotonated molecular mass ion [M-H] at 118 Da. High-resolution MS indicated a molecular formula of C(2)H(5)N(3)O(3). When the experiment was repeated with ring-labeled [(15)N]-RDX, the [M-H] appeared at 120 Da, indicating that two of the three N atoms in the metabolite originated from the ring in RDX. When [U-(14)C]-RDX was used in the experiment, 64% of the original radioactivity in RDX incorporated into the metabolite with a molecular weight (MW) of 119 (high-pressure LC/radioactivity) and 30% in (14)CO(2) (mineralization) after 4 days of incubation, suggesting that one of the carbon atoms in RDX was converted to CO(2) and the other two were incorporated in the ring cleavage product with an MW of 119. Based on the above stoichiometry, we propose a degradation pathway for RDX based on initial denitration followed by ring cleavage to formaldehyde and the dead end product with an MW of 119.     

Biodegradation of polycyclic hydrocarbons by Phanerochaete chrysosporium.

The ability of the white rot fungus Phanerochaete chrysosporium to degrade polycyclic aromatic hydrocarbons (PAHs) that are present in anthracene oil (a distillation product obtained from coal tar) was demonstrated. Analysis by capillary gas chromatography and high-performance liquid chromatography showed that at least 22 PAHs, including all of the most abundant PAH components present in anthracene oil, underwent 70 to 100% disappearance during 27 days of incubation with nutrient nitrogen-limited cultures of this fungus. Because phenanthrene is the most abundant PAH present in anthracene oil, this PAH was selected for further study. In experiments in which [14C]phenanthrene was incubated with cultures of P. chrysosporium containing anthracene oil for 27 days, it was shown that 7.7% of the recovered radiolabeled carbon originally present in [14C]phenanthrene was metabolized to 14CO2 and 25.2% was recovered from the aqueous fraction, while 56.1 and 11.0% were recovered from the methylene chloride and particulate fractions, respectively. High-performance liquid chromatography of the 14C-labeled material present in the methylene chloride fraction revealed that most (91.9%) of this material was composed of polar metabolites of [14C]phenanthrene. These results suggest that this microorganism may be useful for the decontamination of sites in the environment contaminated with PAHs.     

Metabolism of hexahydro-1,3,5-trinitro-1,3,5-triazine through initial reduction to hexahydro-1-nitroso-3,5-dinitro-1,3,5-triazine followed by denitration in<Emphasis Type="Italic"> Clostridium bifermentans</Emphasis> HAW-1

A fast hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX)-degrading [28.1 mol h^–1 g (dry weight) cells^–1; biomass, 0.16 g (dry weight) cells^–1] and strictly anaerobic bacterial strain, HAW-1, was isolated and identified as Clostridium bifermentans using a 16S-rRNA-based method. Based on initial rates, strain HAW-1 transformed 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) with yields of 56, 7.3 and 0.2%, respectively. Complete removal of RDX and its nitroso metabolites produced (%, of total C or N) methanol (MeOH, 23%), formaldehyde (HCHO, 7.4%), carbon dioxide (CO₂, 3.0%) and nitrous oxide (N₂O, 29.5%) as end products. Under the same conditions, strain HAW-1 transformed MNX separately at a rate of 16.9 mol h^–1 g (dry weight) cells^–1 and produced DNX (25%) and TNX (0.4%) as transient products. Final MNX transformation products were (%, of total C or N) MeOH (21%), HCHO (2.9%), and N₂O (17%). Likewise strain HAW-1 degraded TNX at a rate of 7.5 mol h^–1 g (dry weight) cells^–1 to MeOH and HCHO. Furthermore, removal of both RDX and MNX produced nitrite (NO₂^–) as a transient product, but the nitrite release rate from MNX was quicker than from RDX. Thus, the predominant pathway for RDX degradation is based on initial reduction to MNX followed by denitration and decomposition. The continued sequential reduction to DNX and TNX is only a minor route.