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Munitions Constituents – Photolysis

Munitions compounds (MCs), including 2,4,6-trinitrotoluene (TNT), hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX), 2,4-dinitroanisole (DNAN), 3-nitro-1,2,4-triazol-5-one (NTO), and nitroguanidine (NQ), absorb light in the UV range and are therefore susceptible to photolysis on soil surfaces and in surface water. Photochemical reactions are important to consider when assessing the environmental impact of MCs since they can yield products that differ from their parent compounds in both toxicity and transport behavior. Quantum yield calculations can aid in predicting the photolysis rates and half-lives of MCs. The photolysis of MCs may be enhanced or inhibited in the presence of compounds that are also excited by UV irradiation.

Related Article(s):

• Munitions Constituents

Contributor(s): Dr. Warren Kadoya

Key Resource(s):

• Environmental Organic Chemistry, Chapter 15: Direct Photolysis
• Photochemical Degradation of Composition B and Its Components
• Verification of RDX Photolysis Mechanism
• Photochemical transformation of the insensitive munitions compound 2,4-dinitroanisole
• Photo-transformation of aqueous nitroguanidine and 3-nitro-1,2,4-triazol-5-one: Emerging munitions compounds

Introduction

Insensitive munitions, including IMX-101 and IMX-104, are replacing traditional explosives because they are less prone to accidental detonation and therefore safer for military personnel to handle. IMX-101, composed of 2,4-dinitroanisole (DNAN), 3-nitro-1,2,4-triazol-5-one (NTO), and nitroguanidine (NQ), will replace 2,4,6-trinitrotoluene (TNT) in artillery; IMX-104, composed of DNAN, NTO, and hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX), will replace Composition B (Comp B) in mortars. As both traditional munitions compounds and these insensitive munitions compounds (collectively referred to as MCs) may be deposited onto firing ranges via incomplete detonation, understanding their environmental fate is of concern. Phototransformation due to sunlight exposure is an important fate-controlling parameter for MCs and can occur on the surfaces of solid explosive particles, as shown in Figure 1, as well as in the aqueous phase following MC dissolution by rainwater. Furthermore, MC photolysis can be affected by the presence of natural organic matter and other compounds that are excited by sunlight.

Figure 1. Color change over time as particles of IMX-101 and IMX-104 were exposed to sunlight and rainfall, suggesting phototransformation. Image courtesy of the U.S. Army Engineer Research and Development Center.

Direct photolysis

Compounds that absorb ultraviolet (UV, 100-400 nm) and/or visible (Vis, 400-800 nm) light can undergo direct photolysis from sunlight. Light is absorbed in discrete units, or photons, and the energy of these photons is indirectly proportional to the wavelength of the light. When a chemical molecule absorbs a photon, its ground state electrons may become excited. As the excited electrons return to the ground state, they may undergo a chemical reaction that results in transformation. Figure 2 shows that the UV range is further divided into UV-A (315-400 nm), UV-B (280-315 nm), and UV-C (100-280 nm). Because most of UV-C is filtered out by the Earth’s atmosphere, direct photolysis of compounds at the surface primarily involves UV-A and UV-B.

Figure 2. The ultraviolet and visible spectrum of sunlight measured at noon in midsummer in Cleveland, Ohio in June 1986. Reproduced with permission from Q-Lab Corporation.

The MCs TNT, RDX, DNAN, NTO, and NQ may undergo direct photolysis since they all absorb light in the UV-Vis range (Figure 3). These graphs convey the probability that the compounds will absorb light at a given wavelength. The absorption maxima correspond to one or more electrons transitioning to an excited state.

Figure 3. UV-Vis absorbance spectra for munitions compounds. Spectra over the wavelength range of 200-800 nm were obtained using a Jasco V-630 UV-Vis Spectrophotometer and quartz cuvettes, UV transparent to 200 nm (YeHui Instruments). Adapted from Taylor et al. (2017).

For a chemical bond to break via direct photolysis, a molecule must absorb a photon with higher energy than the energy of the bond. The energy of photons in the UV-Vis range is similar to the bond energies of several single covalent bonds found in organic molecules. Therefore, many of the bonds in TNT, DNAN, NTO, and NQ are susceptible to photolysis from sunlight exposure (Figure 4).

Figure 4. Calculated bond energies (black) and corresponding photon wavelengths (blue, determined from Planck’s equation) required to break the bonds in TNT, DNAN, NTO, and NQ (calculations by Dr. Diego Troya). Energies for bonds in the aromatic and heterocyclic rings are not shown because they exceed the maximum energy of the photons in sunlight reaching the Earth’s surface (500 kJ/mol or 239 nm).

Photolysis products and pathways

The products of the direct photolysis of MCs have been studied in depth, both in photoreactors using UV bulbs emitting light at a given wavelength (Figure 5) or wavelength ranges (including simulated sunlight) and outdoors in natural sunlight. The photolysis of MCs can form mineral products as well as transformation products that may be more toxic than the original compounds.

Figure 5. Example of a UV photoreactor (A) with slots for UV bulbs (B) and a rotating carousel to hold samples (C). Reproduced with permission from The Southern New England Ultraviolet Company.

TNT

The formation of pink and red wastewater released by some ammunition plants led to investigations into the photolysis products of TNT starting in the 1970s. Laboratory experiments observed rapid phototransformation from sunlight in natural waters, some with half-lives less than an hour. Numerous photolysis products of TNT have been reported and include, but are not limited to, 2-amino-4,6-dinitrobenzoic acid, 2,4,6-trinitrobenzaldehyde, 4,6-dinitroanthranil, 2,4,6-trinitrobenzonitrile, 2,4,6-trinitrobenzoic acid, 1,3,5-trinitrobenzene (TNB), 2,4,6-trinitrobenzyl alcohol, and an array of azo and azoxy compounds.

The mechanism of TNT photolysis is not completely understood as numerous products are formed, many of which are not readily synthesized or purchased. However, evidence suggests that TNT is initially excited to a triplet state by UV light. Figure 6 shows a proposed environmental reaction pathway for TNT that combines photo- and biological reactions based on studies in waste disposal lagoons.

Figure 6. Proposed environmental transformation pathway for TNT, including phototransformation and biotransformation reactions. Image courtesy of the U.S. Army Engineer Research and Development Center.

The aquatic toxicity of phototransformed TNT solutions and ammunition wastewaters was not found to be significantly different from that of untransformed TNT. Although TNT phototransformation products tend to be more toxic than TNT, the relatively low product formation coupled with the disappearance of TNT may explain these results.

RDX

RDX photolysis products detected in aqueous systems include nitrite, nitrate, ammonia, formaldehyde, formic acid, formamide, nitrous oxide, and 4-nitro-2,4-diazabutanal. Stable phototransformation products also detected include nitroso compounds MNX (hexahydro-1-nitroso-3,5-dinitro-1,3,5-triazine), DNX (hexahydro-1,3-dinitroso-5-nitro-1,3,5-triazine), and TNX (hexahydro-1,3,5-trinitroso-1,3,5-triazine), which contain one, two, and three nitroso groups each, respectively, in place of the nitro groups. The formation of unsaturated MUX (1,3-dinitro-1,2,3,4-tetrahydro-1,3,5-triazine) was also reported (Figure 7).

Figure 7. Proposed phototransformation mechanism for RDX. Image courtesy of the U.S. Army Engineer Research and Development Center.

Peyton et al. (1999) compiled experimental results for RDX photolysis in a proposed reaction mechanism (Figure 7). The most common first step is the breaking of an N-N bond between a nitro group and a nitrogen atom in the heterocyclic ring, resulting in two radical species (structure (R) in the center and an NO₂ radical). They hypothesize that the NO₂ radical can become an NO radical that may then recombine with structure (R), giving nitroso product MNX. This process can be repeated to form products DNX and TNX (i.e., via cleavage of the other N-N bonds, as shown in the formation of structure [R₂]). The formation of MUX, containing an unsaturation (C=N double bond in the ring) was likely due to the loss of HNO₂ from RDX. Other products could include a combination of nitroso groups and unsaturations. The unsaturated compounds, including MUX, are expected to undergo hydrolysis, forming many smaller products (e.g., nitrite and formaldehyde). One of the major products of RDX photolysis is nitrate, a common groundwater pollutant of concern, despite being much less toxic than RDX. The risk posed by the other toxic products should be evaluated, though they are formed in smaller quantities.

DNAN

The products formed from DNAN photolysis include nitrate, nitrite, 2,4-dinitrophenol (DNP), 2-methoxy-5-nitrophenol, 4-methoxy-3-nitrophenol, [[1]], formaldehyde, and formic acid.Rao et al. (2013) proposed a pathway for DNAN photolysis with photooxidation as the primary mechanism (Figure 8). According to the computational modeling of DNAN bond energies, the C-N bonds and the C-O bond of the methoxy group are most susceptible to photolysis (Figure 4). This is in agreement with the transformation products formed. Once DNAN is excited to a photo-activated triplet state, OH^- in solution can displace either of its nitro groups via an S_N2 reaction to form a methoxynitrophenol. This releases nitrite, which can then form nitrate through further photooxidation. DNP could form via O-demethylation of DNAN, which could occur by hydroxylation of the methyl group and the release of formaldehyde. Formaldehyde or formic acid may react with NH₂ groups in methoxynitroanilines or aminonitrophenols to produce formamide derivatives.

Figure 8. Proposed phototransformation pathways for DNAN. Redrawn from Rao et al. (2013).

Ecotoxicity estimates predict that DNAN phototransformation products are less toxic than DNAN, except for DNP, which is more toxic and known to uncouple oxidative phosphorylation. However, upon further photolysis, DNP was shown to degrade into nitrocatechol and nitrite.

NTO

Aqueous NTO formed ammonium, nitrate, nitrite, and a urazole intermediate when irradiated with UV light. A significant amount of the original NTO mass was not recovered. This may be due, in part, to the volatilization of gaseous species since bubbles formed in the irradiated solutions. A proposed pathway for NTO photolysis is shown in Figure 9. The first step is the breaking of the C-NO₂ bond, which has the lowest bond energy (Figure 4). This forms a nitro radical and a triazolone radical. The nitro radical can then form nitrite and nitrate, and the triazolone radical can form urazole upon reaction with water. Urazole and/or NTO may undergo hydrolysis that breaks open the heterocyclic ring and ultimately forms degradation products such as ammonium and carbon dioxide gas. In aquatic toxicity studies, UV-irradiated NTO was found to be up to 100 times more toxic than non-irradiated NTO. The specific photolysis products responsible for this increase in toxicity are still being investigated.

Figure 9. Proposed phototransformation pathways for NTO. Redrawn from Becher et al. (2019).

NQ

The major products formed from NQ photolysis are nitrate, nitrite, guanidine, and urea. Minor products include cyanamide, cyanoguanidine, ammonium, melamine, ammeline, and cyanide. Nitrosoguanidine and hydroxyguanidine were identified as intermediates that were further phototransformed^30,31. A proposed pathway for NQ photolysis is shown in Figure 10. The weakest bond is the N-NO₂ bond (Figure 4), and when it is cleaved, it forms nitro and guanidine radicals. The nitro radical can form nitrite and nitrate. The guanidine radical, upon reaction with a hydrogen ion or a water molecule, can form guanidine or hydroxyguanidine, respectively. Ammonia and cyanamide can also form from the breakdown of the guanidine radical. Cyanamide can then undergo either dimerization to form cyanoguanidine or hydrolysis to form urea. Melamine is a trimer of cyanamide and ammeline is a hydrolysis product of melamine. Cyanide may be formed from cyanoguanidine under acidic conditions.

Figure 10. Proposed phototransformation pathways for NQ. Redrawn from Becher et al. (2019).

UV-irradiated NQ was found to be orders of magnitude more toxic to aquatic organisms than NQ that was not irradiated. Furthermore, it was responsible for most of the toxicity of irradiated IMX-101. Moores et al. (2020) found that guanidine, nitrite, ammonia, nitrosoguanidine, and cyanide produced from NQ photolysis were each more toxic to Daphnia pulex than NQ, with nitrite and cyanide contributing the most to the toxicity. When adding up the individual toxicities caused by these photolysis products, only 25% of the overall toxicity caused by exposure to irradiated NQ was accounted for. This implied that additional, unidentified products with greater toxicity to D. pulex formed and/or that exposure to all the products at once created a synergistic toxic effect.

Photolysis kinetics

In dilute solutions, the direct photolysis of a compound may be described as a pseudo first-order process, in which the log of the compound concentration decreases linearly with time. In contrast, when the compound concentration is high enough that it absorbs most of the incident light, the photolysis rate no longer depends on the compound concentration, and the process may be described as zero order. First-order kinetics were reported in studies irradiating MCs at 1 mg L^-1, whereas zero-order kinetics were reported for MCs irradiated at higher initial concentrations. The phase of an MC can impact its photolysis rate, as aqueous RDX was found to transform significantly faster than solid RDX. In addition, the half-lives of UV-irradiated compounds are highly dependent on sunlight exposure and intensity, which vary with time (of day and year) and location (latitude and altitude). Therefore, it is more useful to describe photolysis in terms of quantum yields rather than reaction rates or half-lives, since they account for differences in experimental setup and irradiance and are more readily comparable.

Quantum yields The proportion of photons absorbed by a given compound that results in its transformation (i.e., via chemical reaction) is known as the reaction’s quantum yield. These are usually determined experimentally. Schwarzenbach et al. (2003)¹ define quantum yield as:

In systems involving organic pollutants in natural waters, quantum yields are generally between 0 and 1, since chain reactions resulting in higher quantum yields are rare. Furthermore, quantum yields are not expected to vary significantly with the wavelength of light absorbed, at least over a given absorption band, and can be used to approximate the overall transformation rates of compounds¹.

Where quantum yield can be assumed to be independent of wavelength, it can be expressed as the ratio of the photolysis reaction rate (k_p) to the rate of light absorption (k_a):

Thus, if there is an experimentally derived quantum yield available, and if the light absorption rate of a given system can be measured or approximated (e.g., by a spreadsheet or computer program), the direct photolysis rate can be calculated by the above equation. Reported quantum yields for solutions in distilled water are included in the table below.