Electrochemical, Photochemical, and Photoelectrochemical Treatment of Sodium p-Cumenesulfonate

The degradation of sodium p-cumenesulfonate (SCS) by electrochemical, photochemical, and photoelectrochemical methods in aqueous solution of NaClO4, NaCl, and NaClO has been studied. It was found that as a result of NaClO4 electroreduction and photodecomposition, the ions Cl− and ClO3 − are formed. These ions undergo transformations into radicals, mainly Cl•, Cl2 •−, ClO•−, ClO2 •−, and ClO3 •−, due to electrochemical and photochemical reactions. It was shown that the interpretation of results of the studies over mineralization processes carried out in the presence of ClO4 − cannot be adequate without taking into consideration the reduction of ClO4 − to Cl− and ClO3 −. Therefore, previous works presented in the literature should be rediscussed on the basis of the new data. Photoelectrochemical mineralization of substrate in NaCl solution at the concentration of 16 mmol L−1 is comparable with the efficiency of the reaction in NaClO4 solution containing more than 8 mmol L−1 of NaClO. Total SCS mineralization was obtained in the photoelectrochemical reactor with a UV immersion lamp with a power 15 W in the period of 135 min and current intensity of 350 mA. In such conditions, the power consumption was about 1.2 kWh per g of TOC removed.


Introduction
Hydrotropes are mild surface active amphiphilic organic salts with hydrophobic part comparatively smaller than in the case of conventional surfactant. Hydrotropes exhibit a higher and often more selective ability to solubilization of organic compounds in water. The self-aggregation of the hydrotropes has been considered to be a pre-requisite for a number of applications in various fields such as drugs solubilization (Yalkowsky 1981), chemical reactions (Khadilkar et al. 1995), and separa-cleaners. The use of hydrotropes in household laundry and cleaning products raises no safety concerns for the consumers. They are also used as corrosion inhibitors, components of electroplating baths, and as a support for an extraction process (Stanton et al. 2010). The studies carried out on individual hydrotropes or surfactant-hydrotrope mixtures support the fact that hydrotropes are able to form self-aggregates in aqueous solutions known as minimum hydrotrope concentration (MHC), analogous to critical micelle concentration (CMC) for surfactants (Bhat and Gaikar 1999;Bhat and Gaikar 2000).
The photoelectrochemical process is an efficient method of degradation of organic pollutants in water (Osiewała et al. 2012;Socha et al. 2005). The effectiveness of this process depends on the composition of supporting electrolyte and electrode properties. There are numerous semiconductors which can be used as photocatalysts: TiO, WO 3 , SnO 2 , ZnO, and CdS. As generally observed, TiO 2 is an efficient photocatalyst with high quantum yields. Photocatalysis by TiO 2 (Eg=3.2 eV) involves, under UV light excitation, the generation of electron (e − ) in the conduction band and a hole (h + ) in the valence band. These species undergo charge transfer reactions across the interface with oxygen, water, or organic pollutants adsorbed on TiO 2 surface. The reaction of h + with OH − or H 2 O leads to the generation of reactive • OH radicals, which are powerful oxidants attacking the recalcitrant organic compounds (Noorjahan et al. 2003); the reaction pathway is illustrated by Eqs. (1)-(6): Hole pathway : OH − þ TiO 2 h þ ð Þ→TiO 2 þ • OH ð2Þ Electron pathway : • OH þ M→degradation products The electrocatalytic activity of RuO 2 coupled with oxygen evolution is very favorable for the photochemical process of pollutants degradation, because the oxygen superoxide anion radicals (O 2 •− ) formed during the photochemical process can produce additional amounts of hydroxyl radicals (Pelegrini et al. 1999).
The dissolved oxygen molecule absorbs the quantum of UV light forming activated oxygen radicals. Subsequently, the oxygen radical reacts with hydrogen ions to produce water. At the same time, activated oxygen radicals can also be destroyed by single radical termination as a result of collision with inert water (Harano and Shmit 1968), Eqs. (7)-(9): It has been known that degradation of organic pollutants by UV light radiation is more effective in the presence of some oxidants such as sodium hypochlorite and sodium persulfate (Hepel and Luo 2001;Catanho et al. 2006). One of the most often used hydrotrope is sodium p-cumenesulfonate (SCS). The structure of this compound is presented in Fig. 1.
So far, the literature data concerning the degradations of SCS are not numerous. Kimura and Ogata (1983) studied the decomposition of SCS by the photochemical oxidation (UV light λ>290 nm) in alkaline aqueous solution with an addition of sodium hypochlorite (NaClO). The SCS mineralization was about 38 % after 45 min reaction at room temperature and the following products were detected: cumene, 2-isopropylphenol, 4isopropylphenol, and 2-phenyl-2-propanol.
SCS very often coexists in wastewater with chloride ions, for example in zinc electroplating baths (Kozłowski et al. 1990). In many studies, the effect of chloride ions on the photoelectrochemical degradation of pollutants was investigated. Xiao et al. (2009) found that the presence of chlorides accelerates degradation of organic compounds in wastewater.
This work presents the results of sodium pcumenesulfonate degradation in the solutions of NaClO 4 , NaCl, and the mixtures of NaClO 4 and NaClO or NaCl using electrochemical, photochemical, and photoelectrochemical methods.

Analytical Methods
In order to assess the mechanism of electrochemical oxidation and reduction of SCS, the cyclic (CV) and differential pulse (DPV) voltammetry measurements were carried out using an Autolab Potentiostat PGstat30 (EcoChemie, Holland). A three-electrode cell was applied in all experiments; platinum and titanium covered with TiO 2 (70 %) and RuO 2 (30 %) electrodes were used as a working electrodes for the oxidation process. The mercury electrode was used as a working electrode for the reduction process. The potential of the working electrode was measured vs. the saturated calomel electrode (SCE), whose standard potential is defined as 0.244 V vs. the standard hydrogen electrode (SHE). Before the measurements, solutions were purged with argon in order to remove dissolved oxygen. During measurements, an argon blanket was kept over solutions. Differential capacity was measured using the method of electrochemical impedance spectroscopy (module FRA in Autolab, PGstat30). Electrode potential was changed every 10 mV in the applied potential range. Each measurement was taken on a new drop.
Electrochemical degradation was carried out in an electrochemical cell (reactor volume of 80 mL) using electrodes; titanium covered by TiO 2 (70 %) and RuO 2 (30 %) as an anode (50 mm×20 mm) and platinum as a cathode (50 mm×20 mm). Photoelectrochemical reactions were carried out using the same cell as used in electrochemical reactions insert into two different reactors: first one the reactor RPR 200 (Southern New England Ultraviolet Co.) which was equipped with 16 lamps emitting radiation at the wavelength of 254 nm (volume 80 mL) and second one Labor-UV-Reactor system with volume of 160 mL (Heraeus Noblelight) equipped with a UV lamp emitting wavelength of 254 nm and power 15 W (Fig. 2). The latter reactor was also used in photochemical reactions.
In order to assess the degradation of SCS, the following analytical methods were performed: Total organic carbon (TOC) was analyzed using TOC 5050A Shimadzu Total Organic Carbon Analyzer, SCS mineralization calculated by Eq. (10): Where αTOC is TOC conversion (%), C 0 is organic carbon content in initial solution (mg L −1 ), and C is organic carbon content in solution after reaction (mg L −1 ).
The total organic carbon (TOC), UV/Vis spectra, and sulfate ion concentration in the solutions were recorded before and after the process.

Electrooxidation and Electroreduction
The electrooxidation and electroreduction reactions of SCS at the platinum and mercury electrode were studied by cyclic and differential pulse voltammetry in NaClO 4 solution. Differential pulse voltammetry is the method with higher resolution, which enables better separation of peaks characterizing subsequent steps of the electrode reaction. Half-wave potential (E 1/2 ) corresponds to the potential of the peak occurring in a differential pulse curve and is characteristic for each of the subsequent steps of the investigated electrode reaction. Basic information about the course of electrochemical reaction is provided by the dependence of the current on the potential. Figure 3a shows the reduction of SCS on the mercury electrode. The process starts at a potential of about −0.8 V and three peaks are observed during polarization with scan rate 100 mV s −1 in the negative direction at potentials of −1.19 (week), −1.35, and −1.45 V. An increase in the scan rate leads to an increase in the peak's maximum current in all cases. Peaks I and III are irreversible, whereas peak II is quasi-reversible and corresponds to the adsorptiondesorption process. A shift of peak I towards the more positive potential and the shift of peak III towards more negative potential are observed. For the last peak, the dependence of current vs. root of scan rate (v 1/2 ) was determined (insert, Fig. 3a), it is linear and crosses the origin of coordinates. This indicates that the last process (peak III) is characterized by diffusion process. In order to confirm the above results, the changes of double layer capacity for SCS and electrolyte, as well as differential pulse voltammograms, were recorded (Fig. 3b). In the potential range from −0.2 to −1.39 V, the double layer capacity is lower in the solution containing SCS and electrolyte compared to the solution without substrate. Lower capacity corresponds to the adsorption of substrate and reaction products on the electrode's surface. A sharp desorption-adsorption peak in cyclic voltammogram (Fig. 3a), the differential pulse voltammogram, and the increase in capacity (Fig. 3b) indicate that substrate and reaction products undergo desorption from the electrode surface (at the potential of −1.35 V), and therefore, the diffusion peak (III) may arise.
The substrate was also oxidized at platinum and titanium covered by TiO 2 (70 %) and RuO 2 (30 %) electrodes, but peaks were not observed at cyclic and differential pulse voltammograms in the potential range lower than the potential at which oxygen evolution started. Therefore, solution (100 mmol L −1 ), insert; dependence of peak III current (i p ) on the square root of the potential scan rate (v 1/2 ). b Differential pulse voltamogram of ( ) SCS (40 mmol L −1 ) in NaClO 4 solution (100 mmol L −1 ), capacity vs. the potential of SCS (40 mmol L −1 ) in NaClO 4 solution(100 mmol L −1 ), and NaClO 4 solution (100 mmol L −1 ), recorded at mercury electrode, pH=7 the dependence of current on the potential on platinum electrode in the saturated solution of SCS in acetonitryle in the presence of sodium tetrabuthylammonium perchlorate as a basic electrolyte was observed. The potential was measured versus the ferrocene and saturated calomel electrodes. The dependence presented in Fig. 4 proves that oxidation of the substrate begins with the potential of 1.7 V, and two stages of oxidation characterized by poorly shaped peaks were observed on the curves.
The curves of capacity vs. potential were obtained for both electrodes (Fig. 5a, b). In both cases in the potential range from 0.2 to 1.2 V, the double layer capacity is lower in the solution containing SCS and electrolyte than in the solution without substrate; this indicates that SCS was adsorbed on the electrode surface in the investigated potential range.
The above results indicate that the reduction of SCS starts at the potential of −0.8 V vs. SCE and an oxidation at the potential of 1.7 V; however, the oxidation potential of SCS is higher than the potential of oxygen evolution. The current density used in the electrochemical treatment was tenfold higher than it followed from the cyclic voltammograms (from 5×10 −3 A cm −2 to 1.5×10 −2 A cm −2 ). The electrochemical process in water can generate hydroxyl radicals ( • OH). The direct evidence for • OH formation was obtained by the electron spin resonance method (YanQing et al. 2007). The powerful • OH generated electrochemically could effectively degrade organic pollutants, but during the electrochemical degradation of SCS only slight change of αTOC about 5 % was observed. It may be caused by the strong adsorption of substrate on the electrode surface, which is associated with the generation of hydroxyl radicals.

Photochemical Mineralization
Photochemical degradation of SCS (2 mmol L −1 ) was carried out in three aqueous solutions: NaClO 4 , NaClO 4 +NaClO and NaCl. In all cases, after a 120min reaction, SCS was degraded, about 40 % sulfate groups was disconnected from the aromatic ring, and αTOC was in the range from 7 % to 10 %. Exemplary results of photochemical SCS degradation in NaClO 4 solution are presented in Fig. 6. In order to improve the degradation of SCS, electrochemical and photochemical methods were combined.

Photoelectrochemical Mineralization
UV light and chlorination are two of the most common disinfection methods of water and wastewater. Hypochlorite acid can form hydroxyl and hypochlorite radicals by irradiation with UV light in the range from 200 to 400 nm (Xiao et al. 2009).
During the electrolysis of the solutions containing chloride ions the following reactions may occur Eqs. (11)-(16): Anode: Cathode: Bulk of the solution 3 Some researchers have reported that hypochlorous acid can dissociate to hydroxyl radical ( • OH) and chloride radical (Cl • ) upon adsorption of UV photon in the region 200-400 nm (Guo 1993;Mollna et al. 1980). During radiation the solution at the wavelength of 254 nm, the following reactions may occur, Eqs. (17)-(19): The reaction of • OH with Cl − in the acidic solution leads to a rapid formation of Cl 2 •− and can be formulated as follows, Eqs. (20)- (21): The radicals • OH, Cl • , and Cl 2 •− are a reactive species which may oxidize many organic compounds. (Hasegawa and Neta 1978;Feng et al. 2007).
Electrochemical and photoelectrochemical studies of oxidation and reduction of organic compounds are often performed in NaClO 4 aqueous solution as a basic electrolyte. Kim and Anderson (1994)  performed. The studies were carried out in an electrolyzer placed in the photoreactor containing 16 lamps emitting radiation at the wavelength of 254 nm, the solution volume was 80 mL and current intensity of 0.3 A. Figure 7 shows the dependence of changes of SCS and SO 4 −2 concentrations as well as αTOC during the photoelectrochemical reaction in NaClO 4 (100 mmol L −1 ) solution. This dependence proves that after the first 180 min, the substrate is practically absent in the solution while the concentration of SO 4 2− ions increases to 1.1 mmol L −1 which corresponds with about 55 % loss of the substrate. That indicates the formation of other products containing the sulfonic group. The concentration of SO 4 2− ions, as a product of desulfonation grows linearly and is about three times higher than lowering the αTOC value. After 300 min of the reaction, 93 % desulfonation of the substrate and 35 % decrease in αTOC were observed. It proves an almost complete desulfonation of the substrate and other containing sulfur reaction products as well as the formation in the solution of organic compounds free from sulfur, which oxidize harder than the substrate. It is worth remembering that in electrochemical and photochemical reaction in NaClO 4 solution (100 mmol L −1 ) the substrate undergoes the mineralization in 5 % and 8 %, respectively, whereas in the photoelectrochemical reaction the mineralization increases to 35 %. It indicates that apart from the additive effect of both reactions, the following factors may influence the increase in mineralization: generating photocurrent, easier oxidation of possibly excited substrate, the photocatalytic effect of electrode and the formation of oxidants. During the electrochemical reaction in NaClO 4 solution oxygen and • OH radicals are formed. Hydroxyl and O •− radicals resulting from the radiation of molecular O 2 in an inert environment have the oxidation potential 1.8 V vs. NHE, while in the acidic environment the oxidation potential of • OH radicals is 2.7 V vs. NHE. During the photoelectrochemical reaction of SCS in NaClO 4 (100 mmol L −1 ), after about 60 min pH of the solution decreases systematically from the value of 7.5 to about 3.5 after 300 min of the reaction. This suggests that if a sufficient number of hydroxyl radicals were formed, an increase in the mineralization should be observed along with the decrease of pH. However, it is not confirmed by the dependence of αTOC on the reaction time.
The above analysis shows that during the photoelectrochemical reaction of SCS in NaClO 4 (100 mmol L −1 ) not sufficient amount of oxidants with a higher than 1.8 V potential allowing a complete mineralization of the substrate is formed. Therefore, the experiments of the photoelectrochemical reaction of SCS in NaClO 4 (100 mmol L −1 ) solutions, containing different concentrations of NaClO or NaCl (from 0 to 16 mmol L −1 ) and in monocomponent NaCl solution (from 2 to 16 mmol L −1 ) were carried out. The reaction time was 120 min. The results are presented in Fig. 8.
In (NaClO 4 +NaCl) solution (curve 3) along with the increase in concentration of chloride ions, an almost linear increase in αTOC up to about 90 % at Cl − of 16 mmol L −1 is observed. In the case of (NaClO 4 + NaClO) solution (curve 1) two ranges of increase in αTOC can be distinguished depending on the concentration of ClO − ions: a relatively sharp within the concentration range from 0 to 6 mmol L −1 and much lower in the range from 6 to 16 mmol L −1 . The changes of αTOC during the SCS reaction in the NaCl solution (curve 2) are the same as in (NaClO 4 +NaClO) mixture. SCS degradation in NaClO 4 solution with an addition of Cl − ions is accelerated in comparison to the reaction rate in NaClO 4 itself due to the formation on the anode gaseous chlorine and its chemical and photochemical transformations. However, the amount of Cl 2 formed depends on the concentration of Cl − and ClO 4 − ions deactivating the surface of the anode. It is well known that ClO 4 − oxidizes to ClO 4 and takes up an active site on the surface of Ti/TiO 2 as follows: The electrons occupy the vacancies in the valence band of TiO 2 left by the electrons which have been excited to the conduction band of TiO 2 . Such processes will be repeated upon the illumination of the cell (Rahman et al. 2007).
Practically the linear dependence of the αTOC on the reaction time in NaClO 4 solution and the proportional increase in αTOC with the increase in the concentration of chloride ions in NaClO 4 solution suggests that oxidation of the substrate in monocomponent NaClO 4 solution can be basically caused by radicals formed from the products of NaClO 4 electrochemical reduction and photodecomposition.
To summarize, the discussed results indicate that the efficiency of SCS degradation in each of the considered cases is mainly connected with the Cl • and Cl 2 •− radicals formed from the products of electrochemical, chemical and photochemical reactions of the basic electrolyte and Cl − and ClO − ions added. According to Brown (1986) the perchlorate ion is electrochemically reduced to the chloride ion at an active titanium electrode in aqueous solutions. Negative current values can be observed on the positive sweep in the potential range from 200 to 700 mV. Therefore, further studies of SCS degradation in a photoelectrochemical reactor with an immersion lamp in the solutions: NaClO 4 (100 mmol L −1 ), NaClO 4 (100 mmol L −1 ) with the addition of NaClO (2 mmol L −1 ), and NaCl (16 mmol L −1 ) were performed.
Additionally, the products of electroreduction, photodestruction, and photoelectrochemical changes of the electrolyte were analyzed.

Photoelectrochemical Treatment of SCS in Heraeus Photoreactor
Due to the increase in the rate of the substrate destruction in the presence of Cl − and ClO − ions, the studies of photoelectrochemical degradation of SCS were carried out for a larger volume of solution (160 mL) in the reactor with an immersion mercury lamp. The measurements were taken in the following solutions: NaClO 4 (100 mmol L −1 ), NaClO 4 containing NaClO (2 mmol L −1 , NaClO to SCS ratio 1:1) and NaCl (16 mmol L −1 ). In the reaction products, TOC and the concentration of SCS, SO 4 2− , and ClO 3 − ions were analyzed.
Due to the comparable effect of SCS mineralization in NaCl and (NaClO 4 +NaClO) solutions, at the current intensity of 0.3 A, the measurements of the influence of the current intensity in the range from 0.1 to 0.45 A on the effect of degradation of the substrate in NaCl (16 mmol L −1 ) solution were taken. Figure 9 shows αTOC vs. current intensity during photoelectrochemical degradation of SCS (2 mmol L −1 ) in NaCl (16 mmol L −1 ) solution. An increase in αTOC can be explained by the generation of molecular oxygen and chlorine and their chemical, electrochemical and photochemical reactions, whose result is the generation of radicals. For further measurements current intensity 0.3 A was selected due to the only slight increase in αTOC for higher values of current intensity. Basic electrolyte NaClO 4 in the photoelectrochemical reaction with the use of Ti/TiO 2 and RuO 2 anode and platinum cathode can undergo different reactions. Bokos and Horanyi (1993) as well as  proved that ClO 4 − ions may undergo reduction on the platinum electrode. They presented the mechanism of ClO 4 − reduction on a rhodium electrode stating that the reduction process begins with the adsorption of ClO 4 − ions on the active sites of the metal surface and the Cl − ions adsorb on the electrode, inhibiting the process of reduction (Lang et al. 2008). The standard potentials in relation to NHE of particular stages of ClO 4 − ions reduction are as follows : NaClO 4 undergoes photochemical decomposition and the products contain mostly oxygen, a small amount of chloride ions and chlorine oxides (Pai Verneker and Maycock 1968). All the products of NaClO 4 cathodic reaction as well as its photodecomposition can be subjected to electrochemical, photochemical and chemical transformations. Chloride ion formed on the anode as a result of NaClO 4 reduction or just present in the solution undergoes oxidation to Cl 2 and is submitted to chemical and photochemical changes according to the reactions (Kang et al. 2006;Neta et al. 1988;Huie et al. 1991):   Fig. 11 The change of the concentration of ClO 3 − ions vs. reaction time after: E electrochemical process (right axis), Ph photochemical process, and Ph-E photoelectrochemical process (left axis) in NaClO 4 (100 mmol L −1 ) solution, V=160 mL, UV lamp 15 W, λ=254 nm, current intensity of 0.3 A, pH=7 To prove the presence of the products of electroreduction and photodecomposition of NaClO 4 , electrochemical, photochemical, and photoelectrochemical reactions of NaClO 4 were carried out. Figure 10 presents an example of ion chromatogram of the products of the photoelectrochemical reaction of NaClO 4 solution. The chromatograms show that a slight amount of ClO 3 − and Cl − or ClO − ions is formed. The method used failed to separate Cl − and ClO − ions. In the photochemical and photoelectrochemical reaction of NaClO 4 the same ions are formed and their concentration is comparable. The concentration of ClO 3 − ions, which were formed in NaClO 4 electrolyte during electrochemical, photochemical, and photoelectrochemical reactions, shows Fig. 11. Perchlorate can be generated as a final product of the photochemical reaction of aqueous solutions containing NaClO, NaClO 2 , and NaClO 3 salts exposed to UV radiation. However, it can only be formed if the concentration of precursors (NaClO, NaClO 2 , and NaClO 3 ) is higher than 1,000 mg L −1 . Perchlorate is a thermodynamically stable molecule in comparison with NaClO, NaClO 2 , and NaClO 3 (Kang et al. 2006). Therefore, one can conclude that under experimental conditions, ClO 3 − and Cl − or/and ClO − are the final products of photoelectrochemical changes of NaClO 4 .
The substrate underwent photoelectrochemical reaction in NaClO 4 solution. It was proved that as in the basic electrolyte, along with the reaction time, the concentration of ClO 3 − and Cl − or ClO − ions as well as ClO 2 − ions in the case of photoelectrochemical reaction increases. Exemplary chromatograms of the solution after the photoelectrochemical reaction of substrate in NaClO 4 solution are presented in Fig. 12.
The results obtained during the photoelectrochemical degradation of SCS in NaClO 4 solution are presented in Fig. 13. The effect of this reaction is a rapid decrease in the concentration of the substrate, an increase in the content of SO 4 2− ions and the increase in the αTOC up to about 35 %. Also, the increase in the rate of αTOC after about 90 minutes is observed. The increase in the concentration of ClO 3 − ions, particularly after an almost complete decay of the substrate in the electrolyte, is practically proportional to the increase in the content of SO 4 2− ions as a product of substrate desulfonation and to the decline in the content of organic carbon. Figure 14 presents the results of photoelectrochemical reaction of SCS in NaClO 4 solution with an addition of NaClO (2 mmol L −1 ). The addition of ClO − ions causes to that in pure NaClO 4 . Therefore, it was tested whether the addition of ClO 3 − ions to NaClO 4 solution could result in the increase in the reaction products, connected with the formation of hydroxyl radicals, according to the reaction 35 (Kang et al. 2006).
It was stated that during the photoelectrochemical reaction of SCS in NaClO 4 solution with the addition of ClO 3 − (2 mmol L −1 ) of ions, the same αTOC as in pure NaClO 4 solution was obtained. It proves that the presence of ClO 3 − ions in the photoelectrochemical reaction is insignificant. Another photoelectrochemical reaction of SCS was carried out in NaCl (16 mmol L −1 ) solution. Figure 15 presents ion chromatograms characterizing a decrease in SCS, accompanied by the increase in SO 4 2− and ClO 3 − content in this reaction. As expected, the reaction of photoelectrochemical degradation of SCS in NaCl (16 mmol L −1 ) solution leads to even better results (Fig. 16). After 120 minutes, a 90 % of αTOC is achieved and the acceleration of the reaction is observed after about 40 minutes. At the same time the concentration of the ClO 3 − ions formed is almost two times higher than in the solution described previously. Similarly as in previous reactions, along with the increase of ClO 3 − concentration, an increase in αTOC and the amount of arising SO 4 2− ions is observed. This fact indicates a cyclic use of the resulting radicals in the SCS degradation.
The concentration of ClO 3 − ions as a final product of radicals transformation in the presence of SCS is always smaller than in the electrolyte. An example of the change in ClO 3 − concentration during the photoelectrochemical reaction in NaCl and SCS in NaCl solutions is presented in Fig. 17.

Optimization of Photoelectrochemical Process with Brandon Method
The mathematical model of the process was constructed using the Brandon method (Kukiełka 2002;Trusov et al. 2002). This method was used to determine the relationship between αTOC conversion and parameters which influence the photoelectrochemical process of SCS degradation. The order of the variables in the equation influences the precision of the results; t-time and i-current were used in the optimization process, the solution 16 mmol L −1 NaCl was assumed in all experiments. It is necessary to build a model by a consistent decrease in the number of statistically significant and less significant factors. Using the Brandon method of multiple regression a mathematical dependence of αTOC (y) on the reaction time (t) and current (i) was determined. The form of the equation is as follows, Eq. (36) y ¼ 0:95 −4 10 −5 t 3 þ 9:8 10 −3 t 2 þ 7 10 −3 t þ 5:63 À Á −5 10 −6 i 2 þ 5 10 −3 i þ 7 10 −2 À Á Based on this dependence, the parameters t and i, which allowed maximum αTOC conversion, were determined. For the parameters t=135 min and i=350 mA, αTOC achieved 99.5 % at energy consumption about 1.2 kWh per g of TOC removed. Energy consumption was calculated by the adding of energy consumption during photochemical process (UV lamp 15 W) to energy consumption during electrochemical process (voltage was 10 V, i=0.35 A and t=2.25 h) and divided by weight of TOC removed. The dependence of αTOC vs. reaction time and current is shown in Fig. 18.  4 Conclusions SCS is reduced on mercury electrode in three steps (E 1/2 = −1.25, −1.35, and −1.42 V vs. SCE) in the potential range lower than the potential at which hydrogen evolution started. The substrate in acetonitrile is oxidized in two stages (E 1/2 =2 and 2.25 V vs. SCE) on the platinum electrode. SCS is adsorbed on applied electrodes surface during the electrooxidation and electreduction process. Adsorption and a high potential of oxidation and reduction cause low mineralization of substrate during the electrochemical reaction (about 5 %).
It was proved that during electrochemical, photochemical and photoelectrochemical reactions, NaClO 4 decomposes forming mainly Cl − and ClO 3 − ions. It was concluded that the main cause of synergy in the photoelectrochemical destruction of SCS in NaClO 4 solution is its photochemical decomposition leading to the generation of Cl • , ClO •− , ClO 2 •− , and ClO 3 •− radicals. The increase in the αTOC is proportional to the increase in the concentration of added Cl − ions into NaClO 4 solution which is caused by the increase in the number of radicals resulting from the electrochemical, photochemical and photoelectrochemical reactions of Cl − ions and their inhibitory effect on ClO 4 − reaction on the electrode surface. The photoelectrochemical mineralization of the substrate in NaCl solution at the concentration of 16 mmol L −1 is comparable with the efficiency of the reaction in NaClO 4 solution containing more than 8 mmol L −1 of NaClO. Total mineralization of SCS was achieved in the photoelectrochemical reactor with an immersion UV lamp 15 W in the period of 135 minutes and current intensity of 350 mA. Under these conditions the energy consumption was about 1.2 kWh per g of TOC removed.
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