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Water 2019, 11(12), 2532;

Efficient Degradation of Mordant Blue 9 Using the Fenton-Activated Persulfate System
Hubei Provincial Engineering Laboratory for Clean Production and High Value Utilization of Bio-based Textile Materials, Wuhan Textile University, Wuhan 430200, Hubei, China
Sanitary Environmental Engineering Division (SEED), Department of Civil Engineering, University of Salerno, via Giovanni Paolo II 132, 84084 Fisciano (SA), Italy
Department of Inorganic Chemistry, Ivanovo State University of Chemistry and Technology, 7, Sheremetevsky Ave, Ivanovo 153000, Russia
Engineering Research Centre for Clean Production of Textile Dyeing and Printing, Ministry of Education, Wuhan Textile University, Wuhan 430200, Hubei, China
Authors to whom correspondence should be addressed.
Received: 15 October 2019 / Accepted: 26 November 2019 / Published: 30 November 2019


In this study, a Fenton-activated persulfate (Fe2+/PS) system was introduced for the efficient degradation of Mordant Blue 9 (MB 9) as a textile dye in an aqueous solution. Results showed that the degradation of MB 9 was markedly influenced by operational parameters, such as initial pH, PS concentration, Fe2+ concentration, and initial dye concentration. Optimal reaction conditions were then determined. Inorganic anions, such as Cl and HCO3, enhanced the degradation efficiency of MB 9 under optimal conditions. Addition of HCO3 reduced the degradation performance of MB 9, whereas the addition of Cl increased the degradation percentage of MB 9. In addition, quenching experiments were conducted using methanol and tert-butyl alcohol as scavengers, and methanol was identified as an effective scavenger. Thus, the degradation of MB 9 was attributed to S O 4 and OH radicals. The degradation and mineralization efficiency of MB 9 was significantly reduced using the conventional Fenton process i.e., Fe2+/ hydrogen peroxide (HP) because of the formation of a Fe complex during degradation. Meanwhile, the Fe2+/persulfate (PS) system improved the degradation and mineralization performance.
Fenton-activated; Fe-complex; persulfate; mordant dyes; scavengers

1. Introduction

Dyes have prompted serious widespread concern because of their substantial contribution to water pollution. The presence of these colorants in effluents not only deteriorates water aesthetically but also harms the social system and health; moreover, these colorants present a threat to environmental sustainability [1,2,3]. Mordant dyes derived from acid dyes have been widely used for the coloration of textile fibers, such as wool, silk, polyester, cotton, and some modified cellulose fibers [4,5]. During coloration, some transition metal ions are typically used with mordant dyes to form a durable dye–metal complex ligand, which enhances fastness to light and washing in dyed fabrics [6]. However, treatment of these dye effluents before they are discharged to the environment has received significant attention because of the potential adverse effects of dyes [7].
Various technologies have been adopted for the degradation of dyes from wastewater, including advanced oxidation processes (AOPs), adsorption, biological and chemical methods, and the use of membrane modules [8,9,10]. Fenton oxidation-based AOPs are among the most effective processes because of their relative ease of operation, low-cost facility, and high removal efficiency [11,12]. The Fenton process oxidizes organic pollutants using hydroxyl radicals (HO•), which are generated from the hydrogen peroxide (H2O2)–ferrous sulfate reaction in an acidic medium [13]. However, the widespread application of Fenton oxidation is impeded by several constraints, such as the limited pH range, sludge generation and large consumption of chemicals [14]. In addition, some studies [15,16,17] have reported that the mordant dye degradation efficiency in Fenton oxidation was inhibited because of the formation of an iron complex with dye ligands. Determining a useful process for the efficient degradation of mordant dyes is desirable and can be a significant step in solving environmental issues.
Persulfate (PS) oxidant has recently been recognized as an essential substitute for hydrogen peroxide (HP) in Fenton processes for the effective removal of pollutants [18,19]. PS can be decomposed to produce sulfate radicals (S O 4 ) via an activation process that can efficiently remove pollutants from wastewater [20]. S O 4   possesses higher redox potential and half-life span stability than HO• [21]. PS activation by transition metal ions (Fe2+, Co2+, etc.) has received particular attention owing to the generation of a significant amount of S O 4 radicals [22]. Ferrous sulfate (Fe2+) is the most widely used PS activator because of its cheap, non-toxic, and high natural abundance compared with other transition metals [23]. As shown in Equation (1), sulfate radicals can be obtained in the presence of Fe2+ ions. Moreover, in the reaction, a stronger oxidant, sulfate radical, is converted to a weaker oxidant, and the hydroxyl radical and both radicals contribute to the degradation, resulting in higher efficiency (Equations (2) and (3)) [24].
Fe 2 + + S 2 O 8 2 Fe 3 + + SO 4 + SO 4 2
SO 4 + H 2 O OH + HSO 4
SO 4 + OH OH + SO 4 2
The degradation of recalcitrant pollutants in wastewater using a Fe2+/PS system has been the focus of many previous studies. Rastogi et al. [25] reported that 90% of polychlorinated biphenyl could be removed within 24 h by Fe(II)/Fe(III)-mediated activation of the PS system. In addition, several contaminants, such as carbamazepine [26], acetaminophen [27], diatrizoate [28], and iohexol [29], could be successfully degraded using the Fe2+/PS system. Studies on the degradation of dyes from textile wastewater by using the Fe2+/PS system have thus far been rarely investigated. Kusic et al. [30] reported that the degradation efficiency of reactive azo dyes was strongly influenced by the Fe (II)-activated persulfate system. A large amount of Orange G dye could be successfully degraded from aqueous solution by using the iron (II)-activated persulfate system instead of the conventional Fenton’s reagent [30,31]. However, this study was prompted by a previous report regarding the lack of studies on the degradation of mordant dyes in the presence of the Fenton-activated persulfate system and compared with the conventional Fenton process.
Therefore, the main purpose of the present study is to evaluate the enhancement of Mordant Blue 9 (MB 9) degradation and mineralization efficiency using the Fenton-activated PS system with an innovative approach. The results demonstrated that the inhibition of degradation during the conventional Fenton process could be overcome by the wide-scale application of the Fenton-activated persulfate system. Moreover, the effects of the operational parameters, such as initial MB 9 concentration, initial pH, and oxidant dosage on the degradation efficiency of MB 9 were evaluated to determine the optimal conditions. The results can potentially provide an invaluable resource for MB 9 degradation from wastewater.

2. Experimental

2.1. Reagents and Materials

Mordant Blue 9 (MB 9, 50%) with molecular weight 502.8 g mol−1 was obtained from Sigma-Aldrich Co. (St. Louis, Mo, USA). Hydrogen peroxide (H2O2), ferrous sulfate (FeSO4·7H2O), sodium persulfate (Na2S2O8), sulfuric acid (H2SO4), and sodium hydroxide (NaOH) were supplied by Aladdin Chemistry Co., Ltd. (Shanghai, China). All selected materials and reagents were used without further purification. Double-distilled water was collected from the analytical chemistry lab of Wuhan Textile University, China.

2.2. MB 9 Degradation Procedures

The degradation procedures were conducted in a 100 mL beaker at a constant temperature of 25 °C. Specific amounts of MB 9 and ferrous sulfate were introduced into the beaker from their stock solution prepared using a preset molar ratio. The initial solution pH was adjusted using both 0.1 M H2SO4, and 0.1 M NaOH whenever required. The reaction was then initiated by adding PS at a predetermined concentration. The final volume of the solution was fixed at 100 mL, and the solution was magnetically stirred (DF-101S, Tianjin Gongxing Experimental Instrument Co., Ltd., Tianjin, China) at 120 rpm for 1 h to ensure proper mixing. At a specific time interval, 1 mL of the sample was withdrawn from the reactor. Quenching experiments were immediately started by adding methanol solution, and the solution was filtered using a membrane with a pore size of 0.38 μm for further analysis. To degrade MB 9 by using the conventional Fenton process, PS was replaced by hydrogen peroxide under the same aforementioned experimental conditions, and the entire experimental procedure was repeated for verification (Scheme 1).

2.3. Analytical Methods

The concentration of MB 9 was measured using an ultraviolet–visible (UV–vis) spectrometer (Tianmei Techcomp Ltd., Shanghai, China) at a maximum wavelength of 522 nm (pure dye) and 469 nm (Fe2+/PS system). The degradation percentage (%) was calculated using Equation (4):
Degradation   ( % ) =   A 0 A t A 0   × 100
where A0 is the initial concentration of MB 9 and At is the concentration of MB 9 at time t, respectively. The mineralization performance of the samples was investigated through the total organic carbon (TOC) with a Shimadzu TOC-5050 analyzer (Shimadzu, Japan). PS decomposition studies were conducted as described in the literature [32].

3. Results and Discussion

3.1. Comparative Studies on MB 9 Degradation Efficiency

The comparative results on MB 9 degradation efficiency by HP, PS, Fe2+, Fe2+/HP oxidation system, and Fe2+/PS oxidation system were evaluated (Figure 1a). MB 9 was hardly removed by solely using Fe2+. The degradation efficiency of the HP oxidant alone was also not satisfactory; however, the removal efficiency slightly increased when PS oxidant was solely used over a period of 30 min. This improvement is related to the higher solubility, oxidation potential, and stability of PS at room temperature (25 °C) than those of HP [33]. The MB 9 degradation efficiency of the Fe2+/HP system was considerably higher than the sum of the efficiencies of Fe2+ alone and HP alone. However, the degradation percentage increased significantly when Fe2+ and PS were used together. Complete removal of MB 9 was achieved after 30 min. These results suggest that SO 4 and •OH radicals were generated, causing MB 9 degradation in this system [34]. Figure 1a also shows the two steps involved in MB 9 degradation: (i) fast-stage degradation, which occurred within the initial 15 min because of the rapid production of S O 4 via S2O82− dissociation [30] and (ii) slow-stage degradation, which was related to the low concentration of the radicals. This result was also supported by the decomposition of PS dosage during degradation (Figure 1b). The consumption rate of PS was more than 40% within the first 15 min, suggesting that Fe2+ could effectively activate PS for the rapid production of S O 4 radicals.

3.2. Effect of Operational Parameters

3.2.1. Effect of Initial pH

In Fenton oxidation, the initial solution pH is commonly regarded as one of the most significant parameters influencing the degradation efficiency of pollutants [35]. Therefore, the effect of variations in initial solution pH on MB 9 degradation by the Fe2+/PS system was measured. In Figure 2, the degradation efficiency of MB 9 is strongly influenced by the initial pH of the solution, which shows that the percentage of degradation decreases from 82% to 32% with increasing pH from 2.65 to 9.24 within 30 min. The maximum degradation percentage of MB 9 (94%) was achieved at pH 4.88 and was considered as the optimal solution pH for the subsequent experiments. Acidic conditions were largely favorable for MB 9 degradation in the Fe2+/PS system. At a lower pH level, SO 4 achieved a higher redox potential and even oxidized water to generate HO• radicals [23]. Hydrolysis of S2O82− could also produce hydrogen peroxide, increasing the efficiency of MB 9 degradation in the presence of a Fe(II)-activated process [36]. Meanwhile, higher pH levels are suitable for generating Fe2+ hydroxyl complexes and Fe3+ oxyhydroxides, both of which are considered as weak activators for PS [37]. Thus, the efficiency of MB 9 degradation decreased as pH increased. Previous studies on carbamazepine degradation by a Fe(II)-activated PS process also demonstrated that alkaline pH leads to reduced degradation efficiency [26].

3.2.2. Effect of PS Concentration

The effect of oxidants has often been considered a parameter affecting pollutant removal because oxidants are the source of radical production in typical Fenton oxidation [34]. Thus, the influence of variations in PS concentrations on MB 9 degradation efficiency was evaluated. The results in Figure 3 show that the maximum efficiency of MB 9 degradation is achieved when PS concentration is set to 0.8 mM; at either higher or lower PS concentration, the degradation efficiency declines. By increasing the concentration from 0.2 to 0.8 mM, the efficiency of MB 9 degradation linearly improved from 50% to 95% after a 30 min reaction. Thus, the optimal PS concentration was determined to be 0.8 mM for the subsequent experiments. At higher PS concentrations, more PS molecules could react with Fe2+, and a greater amount of reactive radicals (S O 4 ) was produced for MB 9 degradation, improving the degradation efficiency during the reaction [38]. Meanwhile, the efficiency of MB 9 degradation decreased to 87% with a further increase in PS concentration to 1.0 mM. This result is attributed to the excess PS in the solution, which may act as the scavengers of radicals, inhibiting the efficiency of MB 9 degradation during the reaction. This finding is consistent with a previous report on sulfamonomethoxine degradation by an iron-activated PS process [39].

3.2.3. Effect of Fe2+ Concentration

The concentration of Fe2+ markedly affected the efficiency of MB 9 degradation. Figure 4 presents the MB 9 degradation studies under different Fe2+ concentrations. An increase in Fe2+ concentration from 0.1 to 0.7 mM caused a significant enhancement in the efficiency of MB 9 degradation from 73% to 93% (Figure 4). The higher concentration of Fe2+ ions that corresponds to a substantial amount of Fe2+ can activate PS molecules to generate S O 4 radicals in the solution, mainly improving the efficiency of MB 9 degradation in the Fe2+/PS system. Thus, 0.7 mM is determined as the optimal concentration of Fe2+. However, a further increase in Fe2+ concentration from 0.7 to 1.5 mM markedly reduced the efficiency of MB 9 degradation from 93% to 38%. This occurrence can be interpreted in two ways: first, the excessive amount of Fe2+ accelerated the scavenging activities of S O 4 radicals in the solution [40], and second, a higher concentration of Fe2+ shifts the equilibrium toward the Fe-complex formation with the MB 9 pollutant in the solution [41]. Similar findings have also been reported in the literature on the degradation of different types of pollutants in the Fe2+/PS system [28,42].

3.2.4. Effect of MB 9 Concentrations

The initial concentration of pollutants has been reported to considerably influence degradation efficiency [43,44]. In the present study, the influence of the initial MB 9 concentration of the Fe2+/PS system was evaluated, and the results are shown in Figure 5. Under these experimental conditions, reduced MB 9 concentration indicated enhanced degradation efficiency. Accordingly, the degradation efficiency was markedly reduced from 94% to 51% as the initial concentration of MB 9 increased from 0.05 to 1.5 mM. The reason is that a higher concentration of MB 9 may reduce the production of reactive radicals by the dissociation of PS molecules. In addition, more MB 9 molecules consume more radicals, resulting in an insufficient amount of radicals to degrade the excess MB 9, and a lower degradation efficiency [45,46,47]. By contrast, a lower dye concentration is suitable for efficient MB 9 degradation, due to many S O 4 radicals produced, ensuring a higher degradation percentage at a low MB 9 concentration.

3.2.5. Effect of Inorganic Anions

Various types of inorganic salt often exist in effluents from textile and dyeing industries, which may influence the efficiency of dye degradation in Fenton oxidation [48,49]. Thus, the effects of Cl and HCO3 anions on the efficiency of MB 9 degradation in the Fe2+/PS system were investigated, and the results are presented in Figure 6a. It was noticed that without the addition of inorganic ions in the solution the degradation efficiency of MB 9 was higher, whereas the addition of Cl in the solution decreased the degradation efficiency of MB 9, possibly due to the formation of less reactive chlorine species such as   Cl , Cl and Cl 2 , as shown in Equations (5)–(7) [50,51]. This result was similar to the previously reported by Fang et al. [52] demonstrated that the efficiency of polychlorinated biphenyl degradation in a PS-activated system was markedly inhibited by the addition of Cl. On the other hand, Wang et al. [53] reported that Cl positively affected the efficiency of rhodamine B degradation in the Fe2+/PS system. However, this difference in the performance of Cl in the PS-activated system was attributed to the variations in the molecular structure of pollutants [54].
SO 4 + Cl SO 4 2 +   Cl
  Cl + Cl Cl 2
Cl 2 + Cl 2 2 Cl + Cl 2
HCO3 is a vital compound in water. Here, we investigated the influence of HCO3 on MB 9 degradation performance. As shown, the degradation efficiency of MB 9 markedly decreased to 67% by the addition of HCO3 in the solution (Figure 6a). This inhibition arises from the rapid consumption of both S O 4 and •OH radicals owing to the scavenging role of bicarbonate in the solution [55]. A previous report by Weng et al. [56] described that the presence of bicarbonate induced Fe-complex formation in the solution, affecting the availability of Fe2+ for the production of S O 4 radicals to oxidize compounds in the Fe2+/PS system, hence, the degradation efficiency of MB 9 was reduced.

3.2.6. Effect of Scavengers

Pollutant degradation in the Fe2+/PS system is caused by oxidative free radicals such as S O 4 and OH [39,57]. Therefore, in the current study, radical quenching experiments were conducted in the presence of tertiary butyl alcohol (TBA) and methanol (MeOH) to determine the potentially dominant radicals for MB 9 degradation. MeOH is a strong scavenger of •OH and weak scavenger of S O 4 because the rate constant of the MeOH + S O 4 reaction is 1 × 107 M−1s−1, while that of the MeOH + •OH reaction is 8 × 108 M−1 s−1, whereas TBA can only scavenge of OH radicals [58]. The efficiency of MB 9 degradation decreased to 78% by the addition of TBA (Figure 6b). This degradation efficiency was less than that without a scavenger, but no significant difference was found. However, the efficiency of MB 9 degradation was significantly reduced to 38% with the addition of MeOH. This result indicated the presence of both S O 4 and OH radicals are responsible for MB 9 degradation in the Fe2+/PS system. This finding was consistent with previous studies in the PS activation oxidation system [59,60].

3.3. Degradation Pathway of MB 9

Structural changes in MB 9 during the conventional Fenton (Fe2+/HP) and Fenton-activated persulfate (Fe2+/PS) degradation studies were investigated by UV–vis spectroscopy; the results are shown in Figure 7a,b, respectively. In the conventional Fenton (Fe2+/HP) process, the absorption spectra of the pure dye have two characteristic peaks at wavelengths of 311 and 522 nm (Figure 7a). The maximum absorption peak in the visible region at 522 nm was responsible for the chromophore bond, and the shoulder peak at 311 nm in the UV region was attributed to the aromatic rings. During degradation, the peak maximum was shifted to 469 nm when the Fe-complex was formed in their structure. This complex also added a broad protuberance from 650 to 750 nm, which could be due to the increase in ligand conformational rigidity with Fe3+ cations after the coordination bond in their terminal hydroxyl group [17,61]. However, no new characteristic peak appeared in the presence of the Fe2+/PS system, suggesting that the chromophore—that is, the cleavage of the azo bond of the MB 9 structure—was completely destroyed during degradation studies (Figure 7b). As a result, the degradation efficiency was higher than the conventional Fenton process. Table 1 also shows that Fe2+/PS is one of the most effective systems for MB 9 degradation.
With the Fe2+/PS system, the degree of mineralization (TOC) removal percentage gradually increased to 60%, whereas with the Fe2+/HP system, TOC removal was only 38% (Figure 7c). This result demonstrates that MB 9 molecules were efficiently mineralized into H2O and CO2 using the Fe2+/PS system (Figure 7d). Therefore, the degradation and mineralization of MB 9 can be effectively obtained using the PS activation system without any complex formation during degradation.

4. Conclusions

The present study shows that Fenton-activated PS is a highly efficient system for MB 9 degradation, with a degradation percentage exceeding 95% in an aqueous solution. In the Fe2+/PS system, the optimal operating conditions were as follows: initial solution pH = 4.88, concentration of PS (PS) = 0.8 mM, concentration of iron (II) (Fe2+) = 0.7 mM, and concentration of initial dye solution (MB 9) = 0.05 mM at 25 °C. The presence of certain anions, such as HCO3, negatively affected MB 9 degradation, whereas the addition of Cl anions improved the efficiency of degradation. Methanol as a scavenger strongly inhibited the efficiency of MB 9 degradation, confirming that SO 4 and OH radicals are actively responsible for MB 9 degradation. The conventional Fenton process was not efficient for MB 9 degradation because of their Fe complex formation behavior during the reaction. Finally, Fenton-activated PS can be used as an effective oxidation system for the degradation of recalcitrant compounds from wastewater.

Author Contributions

Conceptualization, F.Y.T. and M.N.P.; formal analysis, F.Y.T., Y.C. and M.N.P.; methodology, M.N.P.; software, F.Y.T.; data curation, M.N.P.; writing—original draft preparation, M.N.P.; writing—review and editing, V.N., T.Z., F.Y.T., D.X. and Y.C.; supervision, V.N., Y.C. and F.Y.T.; funding acquisition, Y.C. and V.N.


This research work was funded by the Science and Technology Project of Educational Commission of Hubei Province (No. Q20181706).


Authors are grateful to Color Root and Runhe Chemicals Ltd., China, for providing the full M.Sc. scholarship (No. 2014 RHS017) at Wuhan Textile University, China. The PhD School in Risk and Sustainability in Civil Engineering, Environmental and Construction and the Sanitary and Environmental Engineering Division (SEED) Laboratory of the University of Salerno, Italy, are also acknowledged for the PhD scholarship (XXXIV CYCLE) of Nahid Pervez. This research activity is linked to the FARB projects funded by the University of Salerno and coordinated by Vincenzo Naddeo.

Conflicts of Interest

The authors declare no conflict of interest.


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Scheme 1. Experimental setup of Mordant blue 9 degradation in both systems.
Scheme 1. Experimental setup of Mordant blue 9 degradation in both systems.
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Figure 1. (a) MB 9 degradation under different conditions over time and (b) persulfate (PS) decomposition over time. Reaction conditions: pH = 4.88, C (PS) = 0.8 mM, C (Fe2+) = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C.
Figure 1. (a) MB 9 degradation under different conditions over time and (b) persulfate (PS) decomposition over time. Reaction conditions: pH = 4.88, C (PS) = 0.8 mM, C (Fe2+) = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C.
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Figure 2. Effect of initial pH on MB 9 degradation. Reaction conditions: C (PS) = 0.8 mM, C (Fe2+) = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C.
Figure 2. Effect of initial pH on MB 9 degradation. Reaction conditions: C (PS) = 0.8 mM, C (Fe2+) = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C.
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Figure 3. Effect of PS concentration on MB 9 degradation. Reaction conditions: pH = 4.88, C (Fe2+) = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C.
Figure 3. Effect of PS concentration on MB 9 degradation. Reaction conditions: pH = 4.88, C (Fe2+) = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C.
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Figure 4. Effect of Fe2+ concentration on MB 9 degradation. Reaction conditions: pH = 4.88, C (PS) = 0.8 mM, C (MB 9) = 0.05 mM at 25 °C.
Figure 4. Effect of Fe2+ concentration on MB 9 degradation. Reaction conditions: pH = 4.88, C (PS) = 0.8 mM, C (MB 9) = 0.05 mM at 25 °C.
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Figure 5. Effect of the initial dye concentration on MB 9 degradation. Reaction conditions: pH = 4.88, C (PS) = 0.8 mM, C (Fe2+) = 0.7 mM at 25 °C.
Figure 5. Effect of the initial dye concentration on MB 9 degradation. Reaction conditions: pH = 4.88, C (PS) = 0.8 mM, C (Fe2+) = 0.7 mM at 25 °C.
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Figure 6. (a) Effect of inorganic anions on MB 9 degradation; (b) Effect of scavengers on MB 9 degradation. Reaction conditions: pH = 4.88, C (PS) = 0.8 mM, C (Fe)+] = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C.
Figure 6. (a) Effect of inorganic anions on MB 9 degradation; (b) Effect of scavengers on MB 9 degradation. Reaction conditions: pH = 4.88, C (PS) = 0.8 mM, C (Fe)+] = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C.
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Figure 7. UV–vis spectra of MB 9 degradation in the Fe2+/HP (a) and Fe2+/PS system (b); (c) TOC removal. Reaction conditions pH = 4.88, C (PS)/ (HP) = 0.8 mM, C (Fe2+) = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C; (d) proposed mechanism of MB9 degradation in both systems.
Figure 7. UV–vis spectra of MB 9 degradation in the Fe2+/HP (a) and Fe2+/PS system (b); (c) TOC removal. Reaction conditions pH = 4.88, C (PS)/ (HP) = 0.8 mM, C (Fe2+) = 0.7 mM, C (MB 9) = 0.05 mM at 25 °C; (d) proposed mechanism of MB9 degradation in both systems.
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Table 1. Comparison of MB 9 removal using the proposed method and by other methods.
Table 1. Comparison of MB 9 removal using the proposed method and by other methods.
SamplesMethodsConc. of MB 9 Removal Efficiency (%)Ref
Fungal peroxidase enzymesbatch shake flasks10 mg L−197[62,63]
Fungal peroxidase enzymesrotating biological contactor (RBC) reactor10 mg L−198[64]
Fungal peroxidase enzymesmedia constituents10 mg L−1100[65]
Ionic liquidadsorption100 µmol98.28[66]
Fe2(SO4)3coagulation100 µmol28[66]
Fenton oxidation100 µmol98[66]
CeO2adsorption200 mg L−191[67]
Fenton oxidation0.05 mM48This work
Fenton-activated persulfateoxidation0.05 mM97This work
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