Generation of radicals in ferrous-persulfate system using KrCl excilamp Текст научной статьи по специальности «Химические науки»

УДК: 628.31

ГЕНЕРАЦИЯ РАДИКАЛОВ В ЖЕЛЕЗО-ПЕРСУЛЬФАТНОЙ СИСТЕМЕ С ИСПОЛЬЗОВАНИЕМ KRCL-ЭКСИЛАМПЫ

С.А. Попова, Г.Г. Матафонова, В.Б. Батоев

Светлана Александровна Попова, Галина Георгиевна Матафонова *, Валерий Бабудоржиевич Батоев Лаборатория инженерной экологии, Байкальский институт природопользования СО РАН, ул. Сахъяновой, 6, Улан-Удэ, Российская Федерация, 670047 E-mail: [email protected], [email protected] *, [email protected]

Изучена генерация сульфатного анион-радикала (SO4*-) и гидроксильногорадикала (•OH) в железо-персульфатной системе, активированной ультрафиолетовым (УФ) излучением KrCl-эксилампы (222 нм) (УФ/ПС/Fe2+). Для детекции радикалов и оценки уровней их воздействия проведены эксперименты по деструкции соединений-ловушек таргетныхрадикалов - терефталевой кислоты (ТФК) и п-хлорбензойной кислоты (п-ХБК). Деионизованная вода (ДВ), природная вода (ПВ) и очищенная хозяйственно-бытовая сточная вода (СВ), содержащие соединение-ловушку, последовательно обработаны прямым УФ облучением и в системах УФ/ПС и УФ/ПС^е2+. Показано, что для генерации радикалов в одной и той же водной матрице железо-персульфатная система является наиболее эффективной в ряду: > УФ/ПС > УФ. Сравнительный анализ различных водных матриц показал наиболее низкий уровень генерации радикалов в СВ. Поскольку ТФК и п-ХБК оказались малоподходящими соединениями для оценки вкладов SO4и •OH путем сравнения степени деструкции без и в присутствии метанола и трет-бутанола, гербицид атразин (АТЗ) взят как модельный органический поллютант, имеющий близкие константы скорости реакции с SO4и •OH. В результате экспериментов по деструкции АТЗ в присутствии спиртов установлен преобладающий вклад SO4при обработке ДВ (79%) и ПВ (60%) в системе УФ/ПС^е2+, тогда как в СВ вклад SO4и •OH был одинаков. При прямом УФ облучении (без персульфата и Fe2+) выявлена генерация •OH в СВ, что, возможно, обусловлено высокой фотореакционной активностью растворенного органического вещества (РОВ).

Ключевые слова: очистка воды, радикалы, KrCl -эксилампа, персульфат, фентоноподоб-ный процесс

GENERATION OF RADICALS IN FERROUS-PERSULFATE SYSTEM USING KRCL EXCILAMP

S.A. Popova, G.G. Matafonova, V.B. Batoev

Svetlana A. Popova, Galina G. Matafonova*, Valeriy B. Batoev

Laboratory of Engineering Ecology, Baikal Institute of Nature Management of SB of RAS, Sakhyanovoy st., 6, Ulan-Ude, 670047, Russia

E-mail: [email protected], [email protected] *, [email protected]

Generation of sulfate radical anion (SO4and hydroxyl radical (•OH) in the ferrous-per-sulfate system (UV/PS/Fe2+), activated with KrCl excilamp (222 nm) radiation, was studied. To detect radicals and evaluate levels of their action, degradation experiments were conducted using the probe compounds, which trap the target radicals - terephtalic acid (TPA) andp-chlorobenzoic acid (pCBA). Deionized water (DW), natural water (NW) and wastewater (WW), containing a probe compound, were sequentially treated by direct UV, UV/PS and UV/PS/Fe2+ systems. The ferrous-persulfate system was shown to be the most efficient in terms of radical generation within the same water matrix: UV/PS/Fe2+ > UV/PS > UV. Comparing different water matrices, the lowest radical generation was observed in WW. Since TPA and pCBA were unsuitable compounds to assess the contributions of SO4and •OH by comparison of degradation degree with and without methanol and tert-buthanol, herbicide atrazine (ATZ) was taken as a model organic pollutant with comparable reaction rate constants with SO4and •OH. Scavenging experiments with ATZ and alcohols

showed a major contribution of SO4during UV/PS/Fe2+ treatment of DW(79%) andNW(60%), whereas SO4and *OH contributed equally in WW. Direct UVirradiation (without persulfate and Fe2+) indicated the *OH production in WW, presumably, due to high photoreactivity of dissolved organic substance (DOM).

Key words: water treatment, radicals, KrCl excilamp, persulfate, photo-Fenton-like process

Для цитирования:

Попова С.А., Матафонова Г.Г., Батоев В.Б. Генерация радикалов в железо-персульфатной системе с использованием KrCl-эксилампы. Изв. вузов. Химия и хим. технология. 2019. Т. 62. Вып. 5. С. 118-123 For citation:

Popova S.A., Matafonova G.G., Batoev V.B. Generation of radicals in ferrous-persulfate system using KrCl excilamp. Izv. Vyssh. Uchebn. Zaved. Khim. Khim. Tekhnol. 2019. V. 62. N 5. P. 118-123

INTRODUCTION

Advanced oxidation processes (AOPs) are known to be effective for degrading bioresistant organic pollutants in water and wastewater via oxidative reactions with generated in situ reactive oxygen species (ROS). ROS can be produced upon irradiation with UV light in the presence of dissolved organic matter (DOM), oxidants (hydrogen peroxide, ozone, persulfate) or catalysts (TiO2, Fe2+/3+,°). In recent years, sulfate radical-based AOPs (SR-AOPs) are increas-

S2Ü82"

hv

■» 2SÜ4^

SÜ4^ + H2O ^ H+ + SO42- + •ОН

Fe2+ + S2Ü82" ^ Fe3+ + SÜ4^ + SÜ42-^ Fe3+ + SÜ42"

Fe + SÜ4^ SO42- + •ОН ^ SO4^ + ОН-

Fe3+ + S2Ü82- ^ Fe2+ + 2SÜ4^

ingly gaining attention as a promising strategy to remove organic pollutants from aqueous media and soil. The SR-AOPs utilize peroxysulfo-compounds as oxidants, primarily, peroxydisulfate (S2O82", PS) and per-oxymonosulfate (HSO5", PMS or Oxone), which produce sulfate anion radical (SO4O and hydroxyl radical (•OH) after activation with various methods, most commonly, with transition metal ions (Fe2+, Co2+) and UV radiation. Basically, the generation of radicals in such photo-Fenton-like systems is described via the following reactions [1]:

(1) (2)

(3)

(4)

(5)

(6)

k = 6.3107 M"1 s-1 k = 39-49 M-1 s-1 k = 3.0-108 M-1 s-1 k = 1.5 •Ю8 M-1 s-1

k = 22.5-33.5 M-1 s-1

The highly oxidizing SO4V which have a comparable redox potential (Eo = 2.5-3.1 V) with •OH (Eo = 1.8-2.7 V), has been considered as an alternative to •OH due to its lower pH sensitivity, longer half-time in water and higher oxidative selectivity towards many organic compounds [2]. Moreover, persulfates as salts are advantageous for environmental applications due to their solubility in water, lack of harmful byproducts, safe handling and relatively low cost.

Previous studies reported the generation of •OH and SO4^ in the oxidative systems such as PS(PMS)/transition metal [3] and UV/PS(PMS) using mercury lamps as UV sources [4-6]. However, the generation of •OH and SO4^ via photo-Fenton-like processes in real waters remains little investigated. Moreover, in view of the Minamata Convention on Mercury (adopted in 2013, Russian Federation signed in 2014), aimed at providing the gradual phase out of mercury use by 2020, mercury-free UV sources such as ex-cilamps [7] and light-emitting diodes [8] represent

good alternatives for replacement of traditional mercury lamps in AOPs applications.

The objective of this study was to detect and evaluate the radicals exposure in different types of aqueous matrices using the ferrous-persulfate system, activated with KrCl excilamp (222 nm) (UV/PS/Fe2+).

MATERIALS AND METHODS

Terephthalic acid (TPA, 98%, Aldrich), p-chlorobenzoic acid (pCBA, 99%, Acros), atrazine (99.1%, Sigma-Aldrich), iron (II) sulfate heptahydrate (Khimreaktivsnab, Russia), potassium persulfate (Vekton, Russia) were used as received. HPLC grade acetonitrile (ACN) was purchased from Cryochrom (Russia), methanol (MeOH), tert-buthanol (t-BuOH) and acetic acid from Khimreaktivsnab. Stock solutions of compounds were prepared in deionized water (DW, 18.2 mO cm) produced by a Simplicity®UV system from Millipore.

Natural water (NW) was collected from Selenga river (main tributary of Lake Baikal) and urban wastewater (WW) was obtained from the wastewater

treatment plant in Ulan-Ude (Russia). The samples were delivered and filtered on the same day (0.45 ^m RC, Vladisart, Russia) and stored at 4 °C. Dissolved organic carbon (DOC) level in NW and WW was 7.2 and 30.2 mg/L, respectively. Immediately prior to each treatment, water samples were diluted to a DOC value of 5 mg/L in order to elucidate the role of DOM. Water analyses were performed using the standard methods listed in the Environmental normative federal documents (Federal Center of Analysis and Assessment of Technogenic Exposure, Moscow, Russia). DOC was measured by TOC-L CSN (Shimadzu, Japan). Table 1 summarizes the general water quality data after dilution.

Notes: * except for pH nd - not detected

Примечания: * кроме рН, nd -не определялось

To detect and evaluate the radical exposure, scavenging experiments were conducted using probe compounds, which trap the target radicals with known second-order rate constants, £ros (Table 2). Briefly, radicals were detected indirectly via degradation of a probe compound.

Table 2.

Reaction rate constants between probe compounds and radicals (M-1 s-1) Таблица 2. Константы скорости реакции соедине-

A probe compound (20 ^M) was added to each water matrix (50 mL) and sequentially degraded in UV, UV/PS, UV/PS/Fe2+ and PS/Fe2+ (dark control) systems under magnetic stirring and irradiation in a

bench quasi-collimated beam reactor with a KrCl ex-cilamp (Institute for High Current Electronics SB RAS, Russia). The incident irradiance, determined by atrazine actinometry, was 0.08 mW/cm2. The molar ratio of Fe2+ and PS was 1:3.5 (M/M) and initial pH was 3.5. Samples were withdrawn at desired time intervals, filtered through PTFE filters (0.45 цт, Sartorius) to remove the precipitated iron after pH adjustment to 8.0, and analyzed by HPLC for residual concentrations. Probe compounds were determined using an Agilent 1260 Infinity HPLC system with UV detector equipped with a Zorbax SB-C18 column (4.6^150 mm). The el-uents MeOH and 1% CH3COOH (70:30 - pCBA, 30:70 - TPA), ACN and 75 mM CH3COOH (40:60) were used forpCBA (TPA) and ATZ analysis, respectively. The analytes were detected at 220 nm (ATZ), 230 nm (pCBA) and 240 nm (TPA) under flow rate of 0.8 mL/min (0.5 mL/min for ATZ). pH measurements were performed using a Metrohm 827 pH meter (Metrohm, Switzerland).

The reaction between probe compound and ROS is diffusion controlled with the expression of Eq. (7) [13]:

d[Probe compound] _ dt

= £ros [ROS] [Probe compound] (7) where £ros (M-1 s-1) is the reaction rate constant between ROS and a probe compound (Table 2). The pseudo-first-order rate constants (kobs, s-1) of degradation of probe compounds were obtained from experimental linear plots of Ln(C/C0) vs. treatment time through Eq. (8):

d [Probe compound] _ dt

= kobs [Probe compound] (8)

TPA and pCBA, widely used as probe compounds for OH in hydroxyl radical-based AOPs, also react with SO4^ (Table 2). Since the difference between kso4-- and ko№ values is not significant (one order of magnitude), it is difficult to distinguish between •OH and SO4^ just based on the degradation kinetics of pCBA and TPA. Therefore, herbicide atrazine (ATZ) was also taken as a reference compound for scavenging experiments in the presence of MeOH and г-BuOH, which quench •OH and SO4^ with different rate constants. These alcohols have been extensively used previously for •OH and SO4^ identification [4-6]. Specifically, MeOH readily react with both radicals, the reaction rate with •OH is approximately 88-fold higher than that with SO4V while i-BuOH mainly react with •OH, the reaction rate with •OH is approximately 103-fold higher than that with SO4^ (Table 2). If SO4^ is a predominant radical, the addition of i-BuOH would not affect a compound degradation as significantly as MeOH.

Table 1.

Hydro chemical characteristics of aqueous matrices for experiments

Таблица 1. Гидрохимические характеристики вод-

mg/L* Natural water Wastewater

рН 7.2 7.1

NH4+ nd 5.1

HCO3- 84.7 64.6

CO32- 6.3 6.0

NO3- nd 5.4

NO2- nd 2.3

SO42- 8.9 11.9

Cl" 1.3 36.6

PO43- nd 1.8

COD 7.6 4.0

ния-ловушки и радикалов (M-1 c-1)

Radical Probe compoUnd^^^^ •OH SO4^

^-chlorobenzoic acid 5.0 109 [9] 3.6108 [10]

Terephthalic acid 4.4109 [11] 1.7108 [10]

Methanol 9.7108 [10] 1.1107 [12]

/-buthanol 6.0108 [10] 4.0105 [12]

RESULTS AND DISCUSSION

At initial stage, pCBA and TPA were examined as radical probe compounds, based on the monitoring of their degradation. The pseudo-first-order rate constants of pCBA and TPA degradation by direct UV, UV/PS and UV/PS/Fe2+ treatment in DW, NW and WW are presented in Table 3. Dark experiments (PS/Fe2+) showed ~50% degradation of pCBA and TPA.

Table 3.

Pseudo-first-order rate constants of pCBA and TPA degradation in different water matrices. [pCBA]0 ([TPA]0) = 20 ^M, [Fe2+] : [PS] = 1:3.5 (М/М), pH0 = 3.5 Таблица 3. Константы скорости псевдо-первого порядка деградации п-ХБК и ТФК в различных водных матрицах. [п-ХБК]0 ([ТФК]0) = 20 мкМ, [Fe2+] :

According to pCBA and TPA degradation rates in the selected water matrices, the oxidative systems can be arranged in the following order: UV/PS/Fe2+ > UV/PS > UV. This indicates the highest •OH and SO4^ exposure in UV/PS/Fe2+ system in each type of water. However, comparing the k values for both probe compounds obtained by UV/PS/Fe2+ treatment of different water matrices, the lowest radical exposure in WW was observed: DW > NW > WW. It is due to •OH and SO4^ scavenging with common anions and DOM. It is known that NOM (DOM) scavenges ROS, including •OH and SO4V with kDoc, oh of 2.5104 L mg C-1 s-1 (on a carbon basis) [14] and kDoc, so4- = 6.6-103 L mg C-1 s-1 [15]. After dilution of NW and WW to 5 mg/L DOC and acidification, WW contained Cl- (1 mM) > SO42- (0.12 mM) > NO3- « NH+ >

NO2- > PO43-, whereas NW contained mainly SO42-

(0.09 mM) and Cl- (0.04 mM). SO42- anions do not react with SO4V but scavenge •OH. The SO4^-induced oxidation processes in UV/PS system were previously shown to be largely affected by chloride and bicarbonate [16]. Chlorides react fast with •OH and SO4^ yielding HOCl^ and Cl^ as primary products (9, 10) [17]:

Cl- + OH ^ HOCl^ k = 3.0-4.3109 M-1 s-1 (9) Cl- + SO4^- ^ Cl^ + SO42-k = 1.3-6.6108 M-1 s-1(10)

However, the conversion reactions of SO4^ into •OH are also probable in WW, increasing the relative contribution of •OH during UV/PS/Fe2+ treatment, which was further supported by scavenging experiments with t-BuOH and MeOH. In turn, the higher rate of •OH towards DOC (kDoc, oh > kDoc, SO4-) contributed to lower degradation rate, as compared to that in NW. The scavenging influence and involvement of HCO3YCO32- to the reactions with •OH and SO4^ at pH 3.5 can be ruled out.

On the contrary, direct UV irradiation showed the highest rate constants of compounds degradation in WW, indicating the ROS generation in this matrix. It is known that natural organic matter (NOM), a component of real waters, influences photolytic and photo-catalytic reactions. The absorption of light by the pho-toinductive constituents of NOM could generate singlet and triplet excited states of NOM, from which such ROS could be further generated such as •OH, 1O2 [18]. Therefore, alongside the inhibition, NOM is capable of promoting the indirect degradation of organic compounds, depending on the compound and the nature/origin and concentration of NOM. As DOC level in NW and WW was the same, the obtained result suggests a predominance of promoting effect of DOM (as samples were filtered) in WW upon direct irradiation with KrCl excilamp, presumably, due to its higher photochemical activity. Regarding UV/PS system, the degradation rates also decreased moving from DW to WW (Table 2). As TPA reacts with SO4^ approximately 1.5 times slower than pCBA, the lower degradation rates were observed.

Thus, pCBA and TPA present good trapping agents for total SO4^ and •OH and can be used as qualitative probe compounds in the persulfate systems. However, the steady-state concentrations of SO4^ and •OH cannot be calculated from Eq. (8) as a ratio kobs/kRos due to non-selectivity of these compounds towards SO4^ and •OH and reaction with rates of 108109 M-1 s-1 (Table 2). The contribution •OH and SO4^ to the compound degradation can be evaluated by comparing the difference between its degradation efficiency in the presence of MeOH and t-BuOH [6, 19]. To identify •OH and SO4^ in the ferrous-persulfate system, pCBA and TPA were tested by adding MeOH and t-BuOH. As expected, comparison of degradation kinetics showed similar degradation rates in the presence of both alcohols, indicating that pCBA and TPA are unsuitable to differentiate SO4^ and •OH. t-BuOH reacts 103 faster with •OH than with SO4V but both pCBA and TPA react with excess amount of SO4^ by

[Персульфат] = 1:3.5 (М/М), pHp = 3,5

System kpCBA • 10-2, s-1 R2 kTPA-10-2, s-1 R2

Deionized water

UV 0.4 0.99 0.1 0.99

UV/PS 10.1 0.99 7.7 1.00

UV/PS/Fe2+ 10.6 0.98 7.6 1.00

Natural water

UV 0.5 1.00 0.1 0.95

UV/PS 3.1 1.00 2.4 0.99

UV/PS/Fe2+ 4.3 1.00 5.0 0.99

Wastewater

UV 1.0 0.96 1.0 0.95

UV/PS 1.7 0.97 1.5 0.96

UV/PS/Fe2+ 3.3 0.96 2.5 0.99

one order of magnitude slower than with •OH (Table 2), making the difference between their degradation rates in the presence of MeOH or Z-BuOH be negligible (data not shown). Therefore, ATZ was further applied as a reference compound with similar rate constants of reaction with OH and SO4-- (W- = 1.4• 109 M-1 s-1, kOH- = 2.2-109 M-1 s-1 [20]).

C/C0 1

0,8 0,6 0,4 0,2 0

«

10 15

t, min

C/C

1

0,8 0,6 0,4 0,2 0

C/C0 1 0,8 0,6 0,4 0,2 0

10

15

t, min

Fig. Kinetic curves of atrazine degradation in the ferrous-persul-fate system without (1) and in the presence of t-buthanol (2) and methanol (3) in deionized (a), natural (b) and wastewater (c) Рис. Кинетические кривые деструкции атразина в железо -персульфатной системе без (1) и в присутствии t-бутанола (2) и метанола (3) в деионизованной (a), природной (b) и сточной воде (c)

ATZ was completely degraded in the absence of alcohols, whereas the degradation in the presence of ferrous-persulfate scavengers was remarkably inhibited, indicating the involvement of both and •OH in the oxidation (Figure). Assuming that ATZ was degraded by SO/- in the presence of t-BuOH (which faster scavenges •OH), the contribution of •OH can be obtained as the arithmetical difference between the degradation efficiency with /-BuOH and without both alcohols [6]. Accordingly, ATZ was 100% degraded after 15 min treatment of DW and NW in the absence of alcohols and SO4^ appears to be the primary radical formed: 79% SO4^ and 21% •OH in DW, 60% SO4-and 40% •OH in NW). However, in WW, SO4^ and •OH equally contributed to 87% ATZ degradation in 15 min. This observation was in agreement with previous studies [4-6], where SO4^ was found to be the primary radical during the persulfate oxidation of organic pollutants.

CONCLUSIONS

Sulfate radical anion and hydroxyl radical are most effectively generated in the ferrous-persulfate system. Though total •OH and SO4^ exposure in urban wastewater was lower than in natural water, DOM of wastewater demonstrated higher photoreactivity in terms of •OH production in UV system. The estimated contributions of •OH and SO4^ to the degradation of herbicide atrazine make the UV/PS/Fe2+ system with KrCl excilamp be promising for oxidation of biore-sistant organic pollutants in water and wastewater.

This study was supported by the State Project of BINM SB RAS (No. 0339-2018-0005).

REFERENCES ЛИТЕРАТУРА

1. Grcic I., Vujevic D., Koprivanac N. Modeling the mineralization and discoloration in colored systems by (US)Fe2+/H2O2/S2O82-processes: A proposed degradation pathway. Chem. Eng. J. 2010. V. 157. P. 35-44. DOI: 10.1016/j.cej.2009.10.042.

2. Oh W.-D., Dong Z., Lim T.-T. Generation of sulfate radical through heterogeneous catalysis for organic contaminants removal: Current development, challenges and prospects. Appl. Catal. B-Environ. 2016. V. 194. P. 169-201. DOI: 10.1016/j.apcatb.2016.04.003.

3. Anipsitakis G.P., Dionysiou D.D. Radical generation by the interaction of transition metals with common oxidants. Environ. Sci. Technol. 2004. V. 38. N 13. P. 3705-3712. DOI: 10.1021/es035121o.

4. Saien J., Osali M., Soleymani A.R. UV/persulfate and UV/hydrogen peroxide processes for the treatment of salicylic acid: effect of operating parameters, kinetic, and energy consumption. Desal. Water Treat. 2015. V. 56. N 11. P. 3087-3095. DOI: 10.1080/19443994.2014.963156.

0

5

a

b

1

0

5

c

5. Zhang Q., Chen J., Dai C., Zhang Y., Zhou X. Degradation of carbamazepine and toxicity evaluation using the UV/persulfate process in aqueous solution. J. Chem. Technol. Bio-technol. 2015. V. 90. P. 701-708. DOI: 10.1002/jctb.4360.

6. Michael-Kordatou I., Iacovou M., Frontistis Z., Hapeshi E., Dionysiou D.D., Fatta-Kassinos D. Erythromycin oxidation and ERY-resistant Escherichia coli inactivation in urban wastewater by sulfate radical-based oxidation process under UV-C irradiation. Water Res. 2015. V. 85. P. 346-358. DOI: 10.1016/j.watres.2015.08.050.

7. Lomaev M.I., Sosnin E.A. Excilamps and their applications. Chem. Eng. Technol. 2016. V. 39. N 1. P. 39-50. DOI: 10.1002/ceat.201500229.

8. Matafonova G., Batoev V.B. Recent advances in application of UV light-emitting diodes for degrading organic pollutants in water through advanced oxidation processes: A review. Water Res. 2018. V. 132. P. 177-189. DOI: 10.1016/j.wa-tres.2017.12.079.

9. Buxton G.V., Greenstock C.L., Helman W.P., Ross A.B. Critical review of rate constants for reactions of hydrated electrones, hydrogen atoms and hydroxyl radicals (•OHAO-) in aqueous solution. J. Phys. Chem. Ref. Data. 1988. V. 17. P. 513-886. DOI: 10.1063/1.555805.

10. Neta P., Madhavan V., Zemel H., Fessenden R.W. Rate constants and mechanism of reaction of sulfate radical anion with aromatic compounds. J. Am. Chem. Soc. 1977. V. 99. P. 163-164. DOI: 10.1021/ja00443a030.

11. Page S.E., Arnold W.A., McNeill K. Terephthalate as a probe for photochemically generated hydroxyl radical. J. Environ. Monit. 2010. V. 12. P. 1658-1665. DOI: 10.1039/c0em00160k.

12. Neta P., Huie R.E., Ross A.B. Rate constants for reactions of inorganic radicals in aqueous solution. J. Phys. Chem. Ref. Data. 1988. V. 17. P. 1027-1284. DOI: 10.1063/1.555808.

13. Rosario-Ortiz F.L., Canónica S. Probe compounds to assess the photochemical activity of dissolved organic matter. Environ. Sci. Technol. 2016. V. 50. N 23. P. 12532-12547. DOI: 10.1021/acs.est.6b02776.

14. Larson R.A., Zepp R.G. Reactivity of the carbonate radical with aniline derivatives. Environ. Toxicol. Chem. 1988. V. 7. P. 265-274. DOI: 10.1002/etc.5620070403.

15. Lutze H.V., Bircher S., Rapp I., Kerlin N., Bakkour R., Geisler M., von Sonntag C., Schmidt T.C. Degradation of chlorotriazine pesticides by sulfate radicals and the influence of organic matter. Environ. Sci. Technol. 2015. V. 49. P. 1673-1680. DOI: 10.1021/es503496u.

16. Lutze H.V., Kerlin N., Schmidt T.C. Sulfate radical-based water treatment in presence of chloride: formation of chlorate, inter-conversion of sulfate radicals into hydroxyl radicals and influence of bicarbonate. Water Res. 2015. V. 72. P. 349-360. DOI: 10.1016/j.watres.2014.10.006.

17. Waclawek S., Lutze H.V., Grübel K., Padil V.V.T., Cerník M., Dionysiou D.D. Chemistry of persulfates in water and wastewater treatment: A review. Chem. Eng. J. 2017. V. 330. P. 44-62. DOI: 10.1016/j.cej.2017.07.132.

18. Li S., Hu J. Transformation products formation of ciprofloxacin in UVA/LED and UVA/LED/TiO2 systems: Impact of natural organic matter. Water Res. 2018. V. 132. P. 320-330. DOI: 10.1016/j.watres.2017.12.065.

19. Bu L., Shi Z., Zhou S. Modeling of Fe(II)-activated persulfate oxidation using atrazine as a target contaminant. Sep. Pu-rif. Technol. 2016. V. 169. P. 59-65. DOI: 10.1016/j.sep-pur.2016.05.037.

20. Azenha M.E.D.G., Burrows H.D., Canle L.M., Coimbra R., Fernández M.I., García M.V., Rodrigues A.E., Santa-balla J.A., Steenken S. On the kinetics and energetics of one-electron oxidation of 1,3,5-triazines. Chem. Commun. 2003. V. 9. P. 112-113. DOI: 10.1039/b210119j.

Поступила в редакцию 19.07.2018 Принята к опубликованию 10.01.2019

Received 19.07.2018 Accepted 10.01.2019