- Open Access
Kinetic and mechanistic study of sulfadimidine photodegradation under simulated sunlight irradiation
Environmental Sciences Europe volume 31, Article number: 40 (2019)
The extensive uses of sulfadimidine (SDMD) resulted in its presence in water bodies, and subsequent posed risks to eco-environment and human health. In this study, photodegradation of SDMD in water was studied under UV–Visible irradiation. The intermediates, degradation pathways of SDMD photodegradation and ecological risk of SDMD were investigated as well.
SDMD was rapidly degraded under alkaline conditions. Nitrate ion enhanced SDMD degradation under UV–Vis irradiation, while dissolved organic matter and Fe(III) inhibited its decay, and bicarbonate ion did not exert any effect. The reactive species involved in the SDMD photodegradation was singlet oxygen. Four major transformation products were identified by high-performance liquid chromatography–mass spectrometry (HPLC–MS), and the photolytic pathway was also proposed. Photoinduced hydrolysis, desulfonation and photooxidation were the major photodegradation mechanisms for SDMD. Toxicity analysis with Vibrio fischeri showed an obvious decrease in toxicity of the reaction solution, from the initial inhibition rate of 38.5% to 0% after 150-min irradiation.
Initial pH and common water constituents influence the photo-degradation of SDMD under UV–Vis irradiation. Photodegradation of SDMD could reduce its ecological risk in the aqueous solution.
The ubiquitous occurrence of pharmaceuticals and personal care products (PPCPs) in the environment has now been recognized as a new environmental problem and has aroused increasing concern on their fate and risks [1,2,3,4,5]. In the aquatic ecosystem, the majority of PPCPs tends to absorb light due to their structural characteristics containing functional groups like aromatic rings and heteroatoms, making them prone to undergo photolysis under UV–Vis irradiation [6,7,8]. Pharmaceuticals may be directly photodegraded, which are converted into excited states and subject to chemical transformation as a result of photo-absorption . Indirect photolysis is also an important photodegradation pattern for PPCPs, which happens because of the energy transference or reactions with transient reactive species in natural water arising from irradiation, including reactive oxygen species (ROS, for instance, ·OH and 1O2) and triplet excited states of natural organic matter (3NOM*) [8, 9].
In the aqueous environment, the water constituents (such as nitrate, bicarbonate, dissolved organic matter (DOM) and Fe(III)) are of great importance to the photochemical behavior of pollutants [10,11,12]. Nitrate can generate ·OH under light irradiation which is photoactive to the organic contaminants [10, 13,14,15]. Bicarbonate is documented to yield CO −·3 through reacting with ·OH, and it could also prohibit the photo-transformation of organic contaminants because of the ·OH scavenging [14,15,16]. DOM, as the major form of organic carbon existing in surface water, has dual effects on the photodegradation of organic compounds. It can accelerate the photooxidation by generating oxidants such as HOO/O2−, ·OH, 1O2 and triplet excited-state DOM, and also can scavenge ROS or compete light absorption [11, 17, 18]. The photodegradation of organic compounds is accelerated by Fe(III) complexes by internal charge transfer to generate Fe(II) and hydroxyl radical, which could enhance the photodegradation and serve as the catalytic oxidant [10, 17, 19].
Sulfonamides belong to antibiotics which contain aromatic rings in their structure, with potential to absorb light and undergo photochemical degradation under irradiation [8, 20]. Many researchers have reported the photodegradation of sulfonamides, including sulfamethoxazole, sulfamethazine, and sulfadimethoxine in aqueous environment [16, 18, 21,22,23,24]. Albeit with similar structures, these antibiotics undertake different photodegradation behaviors [8, 21]. Sulfadimidine (SDMD) is a sulfonamide antibiotic which has long been used for prophylactic or therapeutic purposes in animal production . Due to its high water solubility and mobility, SDMD has been widely detected in various environmental matrices, with concentrations up to 323 ng/L in water [25,26,27], up to 20 mg/kg in animal manure [26, 28] and 15 μg/kg in agriculture soils [26, 27]. The runoff concentration from manured plots could reach 680 μg/L with 1-day contact time [26, 28]. Generally, sorption and photodegradation processes governed sulfamethazine fate in freshwater–sediment microcosms , and the SDMD photodegradation have been studied in several studies [7, 30,31,32]. However, few studies have been solely conducted to investigate its photodegradation behaviors, and its photodegradaion products and mechanisms remained unclear. In this study, we investigated the photochemical degradation of SDMD in aqueous solution under UV–Vis irradiation. The experiments were conducted under different conditions including different pH values and different levels of water constituents. The degradation intermediates/products were identified by high-performance liquid chromatography–mass spectrometry (HPLC–MS), and tentative degradation pathways were proposed. Bioassay with Vibrio fischeri bacteria was carried out to test the acute toxicity variation of SDMD during its photodegradation process.
Materials and methods
Chemicals and materials
Sulfadimidine (purity > 99%) and humic acid sodium salt (HA) were purchased from Sigma Aldrich (St. Louis, MO, USA). Methanol and isopropanol (HPLC grade) were obtained from Tedia Company, Inc. All other analytical-grade chemicals were used without further purification.
A Hg lamp (300 W) and a xenon lamp (800 W, Institute of Electric Light Source, Beijing) placed in the cold trap were employed to simulate UV–Vis and sunlight irradiation. The photodegradation experiment was performed in the photochemical reactor system (XPA-7, Nanjing Xujiang Machinery Factory, Nanjing, China) with the main apparatus containing cylindrical quartz well for the UV irradiation (λ > 200 nm) and Pyrex well for the sunlight irradiation (λ > 290 nm). The light source irradiance spectra (Fig. 1) were measured by a fiber-optic spectrometer (Ocean Optics, USB2000-FLG), and the light intensities were measured with a full spectrum bright light power meter (CEL-NP2000, Beijing Zhongjiaojinyuan Technology Limited company) in the center of the solutions with 3.85 mW/cm2 and 4 mW/cm2 for the mercury and xenon lamp, respectively. The relatively stable photon flux (< 5%) confirmed the stable irradiance during the photodegradation experiment . The SDMD absorption spectra (Additional file 1: Figure S1) under different pH condition were determined by UV–Vis spectrophotometer (Varian Cary 100).
The pH value of the solution was adjusted with HCl or NaOH.
Quartz tubes (60 mL) containing 50 mL of reaction solution ([SDMD]0 = 10 mg/L) were placed in the photochemical reactor system and magnetically stirred. Two milliliters of reaction solution were sampled at specific time intervals. To explore the effects of pH and water compositions [nitrate, bicarbonate, humic acid (HA) and Fe(III)] on SDMD photodegradation, the reagents with serial and concentration gradient at specific pH were added to the reaction solutions. To examine the reactive species involved in SDMD photodegradation, scavenging experiments were performed using isopropanol as the quencher of ·OH  and sodium azide (NaN3) as the quencher of 1O2 and ·OH [34, 35]. Dark control experiments were performed in the same procedures with quartz tubes wrapped with aluminum foils. Triplicate experiments were conducted for all conditions.
An Agilent 1200 HPLC equipped with a diode array detector was employed to analyze SDMD concentrations, with the absorbance wavelength at 261 nm. Compounds were separated by an Agilent Zorbax Eclipse XDB-C18 column (100 mm × 2.1 mm, 3.5 μm). 30% methanol and 70% water with 0.1% formic acid were used as the mobile phases. The flow speed was maintained at 1.0 mL/min.
The photodegradation products were identified by LC–MS (Quest LCQ Duo, US) equipped with an electrospray ionization (ESI) source and operated in the positive ion mode (ESI+) with the mass ranging from 50–500 m/z. The LC separation was performed using an eclipse XDB-C18 column (150 mm × 2.1 mm, 5 μm) with a mobile phase of acetonitrile (A) and water (B) (with 0.1% formic acid) at a flow of 0.3 mL/min. The column temperature was kept at 40 °C, and the gradient was as follows: 0–5 min: 90% B; 5–7 min: 85% B; 7–11 min: 60% B; 11–15 min: 10% B; 15–25 min: 90% B. The capillary voltage and cone voltage were 3.5 kV and 25 V, respectively. The desolvation temperature was 350 °C and source temperature was 120 °C. The flow of sheath gas was 7 L/min.
The toxicity of SDMD solution during photodegradation was evaluated with the bioluminescence inhibition test using Vibrio fischeri. The test was conducted with Microtox Toxicity Analyzer (Model 500), with the initial SDMD concentration at 10 mg/L. The luminescence was determined after incubation at 15 °C for 15 min. The inhibition of luminescence compared to a toxic-free control gives the percentage of inhibition, and was calculated following the established protocol using the Microtox calculation program [36, 37]. Briefly, the decrease in bacterial luminescence (Γ, %) due to the addition of toxic chemicals can be determined with the equation [36, 37]:
where IC0 and IT0 are the luminescence of control and test sample at t = 0. ICT and ITT are luminescence values for control and test samples measured after T minutes of exposure.
Results and discussion
The comparative experiment showed that no observable loss of SDMD was found in dark control, indicating that the SDMD degradation other than photolysis was negligible. Results also showed that under simulated sunlight irradiation (λ > 290 nm), SDMD did not photodegrade due to the weak absorption of light at λ > 290 nm (Fig. 1), which was consistent with previous observation . In contrast, SDMD could be quickly photodegraded under UV–Vis (λ > 200 nm) irradiation. In this study, 300-W high-pressure mercury lamp was used to explore the SDMD photodegradation in aqueous solution.
SDMD photodegradation at varying pH
Figure 2 illustrated the photodegradation of SDMD in solution at different pH values. It showed that within 150-min UV–Vis irradiation, SDMD was almost completely eliminated under alkaline conditions. Linear regression between ln(Ct/C0) and time (t) indicated that photochemical reaction followed the pseudo-first-order kinetics (R2 > 0.98). The degradation rate constant k, half-live (t1/2) and R2 are summarized in Additional file 1: Table S1. Results indicated that SDMD in the alkaline solution was photolyzed more quickly than in acidic environment. The highest k value was 0.0363 min−1 at pH 9, which was much greater than the maximum degradation rate of 0.0179 min−1 in acidic solution at pH 2. This is likely due to the speciation of SDMD under different pH values influencing the absorption of light wavelength (Additional file 1: Figure S1). The pKa1 and pKa2 values of SDMD were 1.95 and 7.45, respectively ; thus, substrate anions with high electron density surrounding the ring structure under alkaline condition were much more reactive for photochemical reaction than their neutral or protonated species [40, 41].
Influence of different constituents
The effect of NO3− on the SDMD photodegradation is illustrated in Fig. 3a. In natural water bodies, the level of nitrate ion generally ranges from 10−5 to 10−3 mol/L . In this study, the addition of NO3− slightly accelerated the SDMD removal rate. The first-order rate constant k increased from 0.032 min−1 (without NO3−) to 0.037 min−1 (10 mmol/L NO3−). It has been reported that the ubiquitous nitrate ion in natural water is the main source for ·OH under irradiation, which will further induce the photodegradation of organic compounds [13, 42]. The results suggested that ·OH could result in SDMD photodegradation. Since SDMD was mainly degraded through direct photolysis, indirect photolysis induced by ·OH only played a minor role in SDMD removal. In view of the nonselectivity of ·OH to react with organic pollutants and high reactivity to sulfonamides , ·OH formed in natural sunlit waters might play important roles in the photodegradation of SDMD and other sulfonamides.
The effect of bicarbonate on SDMD photodegradation is shown in Fig. 3b, which suggested that the addition of bicarbonate did not exert any effect. Bicarbonate is also a ubiquitous ion in natural water, and its presence is of great importance to the photochemical reaction of organic compounds. Bicarbonate can cause approximately 10% of ·OH quenching as a radical scavenger , and it could also lead to the generation of carbonate radical (·CO3−). Compared with ·OH, ·CO3− is less reactive, and is conducive to the removal of easily oxidized substances in nature water [44, 45]. Due to the lower reactivity, ·CO3− in natural water was more steady than ·OH , and its effect on SDMD photodegradation was negligible.
Dissolved organic matter (DOM)
Figure 3c showed that SDMD photodegradation followed the pseudo-first-order kinetics in the presence of humic acid (HA), and HA had an inhibition impact on SDMD photolysis. As shown in Additional file 1: Figure S2, HA has a wide light absorption range of 200–700 nm. HA could compete with SDMD to absorb short-wavelength UV light in the solution, resulting in the inhibition of SDMD photodegradation. Its scavenging ability toward ·OH might be another reason for the inhibition effect. As a photosensitizer, HA may be conducive to photodegradation [46,47,48], while this result showed the minor role of photosensitization played in SDMD photodegradation.
Iron is the abundant element in natural water environment . In this study, three concentrations of FeCl3 (10 μmol/L, 20 μmol/L and 40 μmol/L) representing environmental levels were added into the reaction solution to evaluate its effect on SDMD photodegradation. As shown in Fig. 3d, the degradation of SDMD under UV–Vis irradiation was obviously decreased in the presence of Fe(III).
As reported that Fe(III) could enhance the sulfadimethoxine photodegradation , in this experiment a reversed trend was observed for SDMD. This was mainly related to the iron speciation. Under acidic condition, Fe3+, FeOH2+, and FeSO4+ were the main dissolved forms of Fe(III), which were photoactive for the removal of organic chemicals by the photo-generated ·OH . Under neutral or alkaline conditions, dimeric and oligomeric Fe(III) compounds and Fe(III) colloids were the dominant forms. Fe(III) colloids like ferric oxyhydroxides tend to prevail over other iron species at pH 8 , which would absorb or scatter light, and finally lead to less light received by SDMD in aqueous solution.
Mechanisms of SDMD photodegradation
To determine which reactive oxygen species was involved in the SDMD photolysis, NaN3, isopropanol and N2 were individually added and introduced into the reaction system. It has been reported that NaN3 quenches 1O2 and isopropanol quenches ·OH or O2·−, while purging N2 into the system can eliminate dissolved oxygen (DO) which is documented to quench the molecules from excited triplet state to unexcited state . Results in Fig. 4 showed that the addition of NaN3 inhibited SDMD degradation, suggesting that 1O2 formed during photoreaction played an important role in SDMD photodegradation. Other ROS such as ·OH or O2·− may be not the key radicals involved in the photolysis process.
Due to the high sensitivity, selectivity and efficiency, LC–MS has been widely used as a powerful tool in identifying and charactering drug metabolites . Herein, the intermediates/products of SDMD photodegradation were identified with the retention time and LC/MS–ESI+ spectra. A total of eleven intermediates/products were identified, with detailed information in Additional file 1: Figures S3 and S4. To avoid unreliable analysis, these intermediates were compared to previous studies [8, 51]. Usually, the direct photodegradation products of sulfonamides arise from similar cleavage as shown in Additional file 1: Scheme S1, and cleavage at these positions are mainly involved in photohydrolysis and desulfonation processes [11, 20, 51,52,53]. As shown in Additional file 1: Figures S3 and S4, the direct photolysis of SDMD generated several photoproducts which were also observed by others [18, 51,52,53]. The direct cleavage processes generated products I, II, III, V and VIII, which have been reported in literatures [8, 51]. Desulfonylation is the other important direct pathway induced by excitation of SDMD to its triplet state to produce SO2 extrusion product IV, which has been identified by previous studies [20, 21]. In addition, photooxidation was involved in SDMD photodegradation. Oxidation products where the m/z increased by 16 were identified to N-oxides (VI and X), and by 32 were identified to product VI. O-addition to the phenyl ring or addition to both rings, or the hydroxyl addition through reaction with HO· may result in the oxidation products . The photoproducts may further undergo the desulfonylation process to produce SO2 extrusion products VII and X. The SDMD photolysis pathways are proposed in Fig. 5.
As V. fischeri luminescent bacteria can demonstrate a great potential in ecotoxicological evaluation in comparison to other bioassays, it has been widely used for assessing the toxic effect in aquatic ecosystem [36, 37]. Figure 6 illustrated the toxicity evolvement of the photodegradation reaction solution under UV–Vis irradiation. Results showed that the initial inhibition percentage of SDMD (0 h of irradiation) to V. fischeri was 38.5%. With the reaction continued, the degradation intermediates showed decreased toxicity to V. fischeri. The inhibition disappeared after 90-min experiment. It should be noted that the inhibition percentage firstly decreased to 22.2% (10 min), then increased to 29.5% (40%) and finally decreased to 21.5% (60 min) and 0 (≥ 90 min). This trend indicated the complex photodegradation pathways of SDMD, with some toxic intermediates produced and further transformed to more toxic compounds. Overall, the whole toxicity was eliminated after long-time photodegradation, and the risk of SDMD in natural environments was reduced when exposed to light irradiation. When utilizing UV light to remove SDMD and other antibiotics, the toxicity variation should be monitored, so that the optimum treatment time with low toxicological risk to ecology and human health could be determined.
The present work explored the photo-degradation of SDMD in aqueous solution. The SDMD photo-degradation under UV–Vis irradiation was pH dependent, with higher removal efficiencies under alkaline condition than acidic and neutral conditions. The common water constituents exerted different influence on the SDMD photolysis, depending on different reactive oxygen species involved. Results showed that 1O2 was an important radical generated during the photolysis process. A total of eleven reaction intermediates/products were identified, which were less toxic toward V. fischeri, indicating that photodegradation played a positive role in diminishing the ecotoxicological risk of SDMD in natural water.
Availability of data and materials
The datasets used and analyzed during the current study are available from the corresponding author on reasonable request.
high-performance liquid chromatography–mass spectrometry
pharmaceuticals and personal care products
reactive oxygen species
dissolved organic matter
triplet excited states of natural organic matter
Stamm C, Alder AC, Fenner K, Hollender J, Krauss M, McArdell CS, Ort C, Schneider MK (2008) Spatial and temporal patterns of pharmaceuticals in the aquatic environment: a review. Geography Compass 2:920–955
Mompelat S, Le Bot B, Thomas O (2009) Occurrence and fate of pharmaceutical products and by-products, from resource to drinking water. Environ Int 35:803–814
Homem V, Santos L (2011) Degradation and removal methods of antibiotics from aqueous matrices—a review. J Environ Manage 92:2304–2347
García-Galán MJ, Díaz-Cruz MS, Barceló D (2012) Kinetic studies and characterization of photolytic products of sulfamethazine, sulfapyridine and their acetylated metabolites in water under simulated solar irradiation. Water Res 46:711–722
Jia A, Wan Y, Xiao Y, Hu J (2012) Occurrence and fate of quinolone and fluoroquinolone antibiotics in a municipal sewage treatment plant. Water Res 46:387–394
Boreen AL, Arnold WA, McNeill K (2003) Photodegradation of pharmaceuticals in the aquatic environment: a review. Aquat Sci 65:320–341
Kim I, Yamashita N, Tanaka H (2009) Photodegradation of pharmaceuticals and personal care products during UV and UV/H2O2 treatments. Chemosphere 77:518–525
Boreen AL, Arnold WA, McNeill K (2004) Photochemical fate of sulfa drugs in the aquatic environment: sulfa drugs containing five-membered heterocyclic groups. Environ Sci Technol 38:3933–3940
Prados-Joya G, Sánchez-Polo M, Rivera-Utrilla J, Ferro-garcía M (2011) Photodegradation of the antibiotics nitroimidazoles in aqueous solution by ultraviolet radiation. Water Res 45:393–403
Tercero Espinoza LA, Neamţu M, Frimmel FH (2007) The effect of nitrate, Fe(III) and bicarbonate on the degradation of bisphenol A by simulated solar UV-irradiation. Water Res 41:4479–4487
Ge L, Chen J, Qiao X, Lin J, Cai X (2009) Light-source-dependent effects of main water constituents on photodegradation of phenicol antibiotics: mechanism and kinetics. Environ Sci Technol 43:3101–3107
Mao L, Meng C, Zeng C, Ji Y, Yang X, Gao S (2011) The effect of nitrate, bicarbonate and natural organic matter on the degradation of sunscreen agent p-aminobenzoic acid by simulated solar irradiation. Sci Total Environ 409:5376–5381
Brezonik PL, Fulkerson-Brekken J (1998) Nitrate-induced photolysis in natural waters: controls on concentrations of hydroxyl radical photo-intermediates by natural scavenging agents. Environ Sci Technol 32:3004–3010
Vione D, Khanra S, Man SC, Maddigapu PR, Das R, Arsene C, Olariu RI, Maurino V, Minero C (2009) Inhibition vs. enhancement of the nitrate-induced phototransformation of organic substrates by the ·OH scavengers bicarbonate and carbonate. Water Res 43:4718–4728
Ji Y, Zeng C, Ferronato C, Chovelon JM, Yang X (2012) Nitrate-induced photodegradation of atenolol in aqueous solution: kinetics, toxicity and degradation pathways. Chemosphere 88:644–649
Lam MW, Mabury SA (2005) Photodegradation of the pharmaceuticals atorvastatin, carbamazepine, levofloxacin, and sulfamethoxazole in natural waters. Aquat Sci 67:177–188
Fisher JM, Reese JG, Pellechia PJ, Moeller PL, Ferry JL (2006) Role of Fe(III), phosphate, dissolved organic matter, and nitrate during the photodegradation of domoic acid in the marine environment. Environ Sci Technol 40:2200–2205
Guerard JJ, Chin YP, Mash H, Hadad CM (2009) Photochemical fate of sulfadimethoxine in aquaculture waters. Environ Sci Technol 43:8587–8592
Feng W, Nansheng D (2000) Photochemistry of hydrolytic iron (III) species and photoinduced degradation of organic compounds. A minireview. Chemosphere 41:1137–1147
Trovó AG, Nogueira RFP, Agüera A, Sirtori C, Fernández-Alba AR (2009) Photodegradation of sulfamethoxazole in various aqueous media: persistence, toxicity and photoproducts assessment. Chemosphere 77:1292–1298
Boreen AL, Arnold WA, McNeill K (2005) Triplet-sensitized photodegradation of sulfa drugs containing six-membered heterocyclic groups: identification of an SO2 extrusion photoproduct. Environ Sci Technol 39:3630–3638
Accinelli C, Hashim M, Epifani R, Schneider RJ, Vicari A (2006) Effects of the antimicrobial agent sulfamethazine on metolachlor persistence and sorption in soil. Chemosphere 63:1539–1545
Baran W, Sochacka J, Wardas W (2006) Toxicity and biodegradability of sulfonamides and products of their photocatalytic degradation in aqueous solutions. Chemosphere 65:1295–1299
Nasuhoglu D, Yargeau V, Berk D (2011) Photo-removal of sulfamethoxazole (SMX) by photolytic and photocatalytic processes in a batch reactor under UV-C radiation (lambdamax = 254 nm). J Hazard Mater 186:67–75
Xu WH, Zhang G, Zou SC, Li XD, Liu YC (2007) Determination of selected antibiotics in the Victoria Harbour and the Pearl River, South China using high-performance liquid chromatography–electrospray ionization tandem mass spectrometry. Environ Pollut 145:672–679
Kaczala FE, Blum S (2016) The occurrence of veterinary pharmaceuticals in the environment: a review. Curr Anal Chem 12:169–182
Gaw S, Thomas Kevin V, Hutchinson Thomas H (2014) Sources, impacts and trends of pharmaceuticals in the marine and coastal environment. Philosoph Transac R Soc B 369:20130572
Larsbo M, Fenner K, Stoob K, Burkhardt M, Abbaspour K, Stamm C (2008) Simulating sulfadimidine transport in surface runoff and soil at the microplot and field scale. J Environ Q 37:788–797
Carstens KL, Gross AD, Moorman TB, Coats JR (2013) Sorption and photodegradation processes govern distribution and fate of sulfamethazine in freshwater-sediment microcosms. Environ Sci Technol 47:10877–10883
Chen N, Huang Y, Hou X, Ai Z, Zhang L (2017) Photochemistry of hydrochar: reactive oxygen species generation and sulfadimidine degradation. Environ Sci Technol 51:11278–11287
Yang B, Mao X, Pi L, Wu Y, Ding H, Zhang W (2017) Effect of pH on the adsorption and photocatalytic degradation of sulfadimidine in Vis/g-C3N4 progress. Environ Sci Pollut Res 24:8658–8670
Sören T-B, Peters D (2007) Photodegradation of pharmaceutical antibiotics on slurry and soil surfaces. Landbauforschung Volkenrode. 57:13
Miller PL, Chin YP (2002) Photoinduced degradation of carbaryl in a wetland surface water. J Agric Food Chem 50:6758–6765
Buxton GV, Greenstock CL, Helman WP, Ross AB (1988) Critical review of rate constants for reactions of hydrated electrons, hydrogen atoms and hydroxyl radicals. J Phys Chem Ref Data 17:513–886
Miolo G, Viola G, Vedaldi D, Dall’Acqua F, Fravolini A, Tabarrini O, Cecchetti V (2002) In vitro phototoxic properties of new 6-desfluoro and 6-fluoro-8-methylquinolones. Toxicol In Vitro 16:683–693
Calza P, Marchisio S, Medana C, Baiocchi C (2010) Fate of antibacterial spiramycin in river waters. Anal Bioanal Chem 396:1539–1550
Parvez S, Venkataraman C, Mukherji S (2006) A review on advantages of implementing luminescence inhibition test (Vibrio fischeri) for acute toxicity prediction of chemicals. Environ Int 32:265–268
Pouliquen H, Delépée R, Larhantec-Verdier M, Morvan ML, Le Bris H (2007) Comparative hydrolysis and photolysis of four antibacterial agents (oxytetracycline oxolinic acid, flumequine and florfenicol) in deionised water, freshwater and seawater under abiotic conditions. Aquaculture 262:23–28
Burkhardt M, Stamm C (2007) Depth distribution of sulfonamide antibiotics in pore water of an undisturbed loamy grassland soil. J Environ Qual 36:588–596
Latch DE, Packer JL, Stender BL, VanOverbeke J, Arnold WA, McNeill K (2005) Aqueous photochemistry of triclosan: formation of 2,4-dichlorophenol, 2,8-dichlorodibenzo-p-dioxin, and oligomerization products. Environ Toxicol Chem 24:517–525
Chen Z, Cao G, Song Q (2010) Photo-polymerization of triclosan in aqueous solution induced by ultraviolet radiation. Environ Chem Lett 8:33–37
Zhou X, Mopper K (1990) Determination of photochemically produced hydroxyl radicals in seawater and freshwater. Mar Chem 30:71–88
Sági G, Csay T, Szabó L, Pátzay G, Csonka E, Takács E, Wojnárovits L (2015) Analytical approaches to the OH radical induced degradation of sulfonamide antibiotics in dilute aqueous solutions. J Pharm Biomed Anal 106:52–60
Huang J, Mabury SA (2000) Steady-state concentrations of carbonate radicals in field waters. Environ Toxicol Chem 19:2181–2218
Mazellier P, Busset C, Delmont A, De Laat J (2007) A comparison of fenuron degradation by hydroxyl and carbonate radicals in aqueous solution. Water Res 41:4585–4594
Hassett JP (2006) Dissolved natural organic matter as a microreactor. Science 311:1723–1724
Vione D, Falletti G, Maurino V, Minero C, Pelizzetti E, Malandrino M, Ajassa R, Olariu RI, Arsene C (2006) Sources and sinks of hydroxyl radicals upon irradiation of natural water samples. Environ Sci Technol 40:3775–3781
Zhan M, Yang X, Xian Q, Kong L (2006) Photosensitized degradation of bisphenol A involving reactive oxygen species in the presence of humic substances. Chemosphere 63:378–386
Chiron S, Minero C, Vione D (2006) Photodegradation processes of the antiepileptic drug carbamazepine, relevant to estuarine waters. Environ Sci Technol 40:5977–5983
Shirayama H, Tohezo Y, Taguchi S (2001) Photodegradation of chlorinated hydrocarbons in the presence and absence of dissolved oxygen in water. Water Res 35:1941–1950
García-Galán MJ, Silvia Díaz-Cruz M, Barceló D (2008) Identification and determination of metabolites and degradation products of sulfonamide antibiotics. Trends Anal Chem 27:1008–1022
Dodd MC, Huang C-H (2004) Transformation of the antibacterial agent sulfamethoxazole in reactions with chlorine: kinetics, mechanisms, and pathways. Environ Sci Technol 38:5607–5615
Motten AG, Chignell CF (1983) Spectroscopic studies of cutaneous photosensitizing agents–III. Spin trapping of photolysis products from sulfanilamide analogs. Photochem Photobiol 37:17–26
This work was supported by the National Natural Science Foundation of China (Nos. 41673120 and 51208482).
Ethics approval and consent to participate
Consent for publication
The authors declare that they have no competing interests.
Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
The absorption spectra of SDMD at different pH. Figure S2. UV–Vis spectrum of the HA. Figure S3. The total ion chromatogram for UV–Vis photodegradation of SDMD. Figure S4. MS spectra of the intermediates detected in the SDMD photodegradation solutions under the simulated light irradiation. Scheme S1. Potential direct photolysis cleavage sites . Table S1. Rate constants (k), half-lives (t1/2) and correlation coefficients (r2) for the photodegradation of the SDMD under irradiation of UV–Vis at different pH.
About this article
Cite this article
Hao, Z., Guo, C., Lv, J. et al. Kinetic and mechanistic study of sulfadimidine photodegradation under simulated sunlight irradiation. Environ Sci Eur 31, 40 (2019). https://doi.org/10.1186/s12302-019-0223-z