• <tr id="yyy80"></tr>
  • <sup id="yyy80"></sup>
  • <tfoot id="yyy80"><noscript id="yyy80"></noscript></tfoot>
  • 99热精品在线国产_美女午夜性视频免费_国产精品国产高清国产av_av欧美777_自拍偷自拍亚洲精品老妇_亚洲熟女精品中文字幕_www日本黄色视频网_国产精品野战在线观看 ?

    Activation of sulfite by ferric ion for the degradation of 2,4,6-tribromophenol with the addition of sulfite in batches

    2022-12-07 08:26:30ZongpingWngFnBiLisnCoSiyngYueJingwenWngSonglinWngJunPenghoXie
    Chinese Chemical Letters 2022年11期

    Zongping Wng, Fn Bi, Lisn Co, Siyng Yue, Jingwen Wng, Songlin Wng,Jun M, Pengho Xie,?

    a School of Environmental Science and Engineering, Key Laboratory of Water & Wastewater Treatment (MOHURD), Hubei Provincial Engineering Research Center for Water Quality Safety and Pollution Control, Huazhong University of Science and Technology, Wuhan 430074, China

    b School of Architecture & Urban Planning, Huazhong University of Science and Technology, Wuhan 430074, China

    c State Key Laboratory of Urban Water Resource and Environment, Harbin Institute of Technology, Harbin 150090, China

    Keywords:Fe(III)/S(IV)2,4,6-Tribromophenol (TBP)Sulfate radical (SO4?–)Batches Acute toxicity

    ABSTRACT In this work, the removal of 2,4,6-tribromophenol (TBP) by ferric ion-activated sulfite [Fe(III)/S(IV)] process was systematically investigated with determining the intermediate products and evaluating the influences of some operational conditions and water matrices.Our results show that batching addition of S(IV) benefits the S(IV) utilization efficiency and TBP removal, with SO4?– being the primary reactive radical accounting for TBA degradation.The maximum TBP removal in the Fe(III)/S(IV) process was observed at pH 4.0 and oxygen is essential in this process.With increasing Fe(III) and S(IV) dosages from 0.05 and 0.1 mmol/L to 0.2 and 2.0 mmol/L, respectively, TBP removal followed trends of first increase then decrease.As the acute toxicity of the TBP solution was significantly reduced, the Fe(III)/S(IV) process was believed to be a good choice in the treatment of TBP.

    Aromatic phenols are important environmental micro-organic pollutants and have attracted extensive attentions [1–3].2,4,6-Tribromophenol (TBP) which is commonly used as a pesticide,wood conservative and intermediate for brominated flame retardants has been widely studied in environmental field due to its worldwide use, environmental persistence and related health issues [3,4].The extensive application of TBP makes it easy to enter environmental matrices, such as surface water, landfill leachates,air, and sediment [4,5].As TBP that has a toxicological risk is difficult to be removed by conventional treatment processes [6,7], it is necessary to develop effective techniques to remove TBP from contaminated environments.

    Due to the high degradation efficiency, advanced oxidation processes (AOPs) with producing high oxidative radicals have been widely applied for the treatment of organic pollutants [8,9].In comparison with hydroxyl radical (HO?) (2.4–2.7 V), sulfate radical (SO4?–) has a comparable redox potential (2.5–3.1 V), wider pH range, longer half-life and higher selectivity [10].Over the past decades, SO4?–-based advanced oxidation processes (SR-AOPs)have gained increasing attention [9,11-14].Due to the selectivity of SO4?–towards the bond of C–Br, SR-AOPs have been widely studied for the degradation of brominated organic pollutants such as bromophenols and tetrabromobisphenol A [15,16].Usually, SO4?–is obtained through the activation of persulfate (PS) including peroxydisulfate (PDS) and peroxymonosulfate (PMS) [11,12].However, the application of PDS or PMS in water/wastewater treatment might be limited due to their expensive price and the formation of bromate (BrO3–) in the presence of bromide (Br–) [15,17,18].Thus,it is meaningful to develop other economic SR-AOPs that can reduce the formation of BrO3–.

    Recently, a promising SR-AOP through the activation of sulfite[S(IV)] has received increasing attention [19–21].Among the activated S(IV) processes, the iron-activated S(IV) is considered to have bright prospects [9,22].As for the iron-activated S(IV) process, a series of reactive radicals, such as SO3?–, SO5?–and SO4?–, are producedviathe reactions shown in Eqs.S6-S17 (Supporting information) [9,23].Additionally, HO?can also be produced through the reaction between SO4?–and OH–(or H2O) [10,20,21].As a strong reducing and complexing agent, S(IV) could transfer Fe(III) to Fe(II)and complex with iron ions, which can accelerate the Fe(II)/Fe(III)cycle, reduce the formed sludge, and broaden the adequate pH range [22,24,25].

    In the traditional SR-AOPs, bromate (BrO3–) would be produced in the presence of bromide (Br–) with producing a sequence of intermediate oxidative bromine including Br?, Br2?–and HBrO[15,17,18].As a strong reducing agent, S(IV) can fast react with these oxidative bromine to re-convert them to Br–, which can inhibit BrO3–formation [23,24].As TBP can be fast degraded by SO4?–[26,27], the iron-activated S(IV) process would be a good choice in the treatment of TBP with simultaneous controlling BrO3–formation.However, S(IV) can also fast react with the oxidative radicals, which would cause the waste of S(IV) and lower the treatment efficiency [24,25].It is important to develop methods to increase the utilization efficiency of S(IV).As lowering the initial S(IV) concentration can slow down the rate of S(IV) reacting with the oxidative radicals, adding S(IV) in batches is proposed to increase the utilization efficiency, which still needs to be further studied.

    The objectives of this study were to (1) determine the efficiency of iron-activated S(IV) process on TBP removal and disclose the roles of reactive radicals; (2) make clear whether the addition of sulfite in batches benefits TBP degradation; (3) investigate the influences of some typical operational parameters and water matrices; (4) and evaluate the transformation of bromine and the acute toxicity variation.

    In this work, all solutions were prepared in ultra-pure water produced from a water purifier (MicroPure UV, Thermo Fisher Scientific, Germany), and the experimental procedures and analytic methods were offered in Text S1 (Supporting information).All the samples were replicated for two times at least and the errors stand for the standard deviations among the replicated samples.

    As shown in Fig.1, negligible difference of TBP removal was observed in the presence of sulfite or Fe(III) compared to the control sample, meaning that the addition of sulfite or Fe(III) had no effect on TBP removal.It should be noted that the TBP concentration reduced by about 9% for the control sample, which might be due to that some TBP could be separated out from water solution during the continuous stirring, which was also observed in some previous studies focusing on the treatment of insoluble pollutants [22,24].In contrast, about 70.2% of TBP was removed by the combined process of Fe(III) and sulfite [Fe(III)/S(IV)] in 6 min at the selective experimental conditions, which was similar to the results obtained in other previous studies [22,28], suggesting that the iron-activated S(IV) process would be a good choice in the degradation of TBP.Additionally, different iron-activated processes including Fe(III)/S(IV), Fe(II)/S(IV), Fe0/S(IV), Fe2O3/S(IV)and Fe3O4/S(IV) were comparatively studied.As shown in Fig.S1(Supporting information), both Fe(III)/S(IV) and Fe(II)/S(IV) systems were observed to efficiently degrade TBP with similar removal efficiency at the same iron species concentration (0.1 mmol/L).However, negligible TBP degradation was observed in Fe0/S(IV),Fe2O3/S(IV) and Fe3O4/S(IV) systems with equivalent iron concentration (0.1 mmol/L).As ferric ion is much stable than ferrous ion,Fe(III)/S(IV) system was selected as a typical iron-activated process to evaluate the removal of TBP in the subsequent experiments.

    Fig.1 .TBP removal in different systems.Conditions: [TBP]0= 10 μmol/L, [Fe(III)]0=0.1 mmol/L, [S(IV)]0= 0.4 mmol/L, pH 4.0, temperature 25°C.

    As for the Fe(III)/S(IV) process, fast TBP degradation was observed in the initial 3 min and the TBP degradation reached 68.6%at 3 min (Fig.1), while only a little removal was observed with further prolonging reaction time to 6 min, which might be due to the lack of S(IV) [23,25].To make clear the reason, the variation of S(IV) concentration was monitored.Fig.S2 (Supporting information) illustrates that S(IV) was fast consumed and reduced to nearly zero after reaction for 3 min due to the fact that S(IV) in the Fe(III)/S(IV) system can quickly complex with Fe(III) to form FeSO3+and can be further transformed to SO5?–and SO4?–in the presence of oxygen [29–31], which was in line with the variation of TBP concentration, evidencing that the lack of S(IV) stopped the further degradation of TBP from 3 min to 6 min.Our previous studies also found that the supplement of S(IV) can further increase the treatment efficiency of iron-activated S(IV) processes [20].As S(IV)can fast react with the reactive radicals, such as SO4?–, SO5?–and HO?, in the iron-activated S(IV) systems to consume both S(IV) and reactive radicals [23,30], lowering the initial S(IV) dosage and increasing the dose times would benefit the utilization efficiency of S(IV).

    Fig.2 shows the effect of adding S(IV) in batches on TBP removal at 25°C with the initial reaction pH being 4.0.During the experiment, the total S(IV) dosages for all the samples were 0.4 mmol/L, and the three specific methods of adding S(IV) in batches are as follows: 0.4 mmol/L S(IV) was introduced into the system at 0 min in a time, adding S(IV) at 0 and 3 min separately with 0.2 mmol/L S(IV) each time, and adding S(IV) at 0, 2 and 4 min separately with 0.133 mmol/L S(IV) each time.With increasing S(IV) dosing times from 1 to 2 and 3, the removal of TBP was significantly increased from 70.8% to 87.5% and 91.5% after reaction for 6 min, respectively, evidencing that adding S(IV) in batches benefits the utilization efficiency of S(IV).Additionally, the variations of S(IV) concentration and solution pH during the reaction were monitored.As shown in Fig.S2, the S(IV) concentration decreased rapidly after the reaction started in all systems.As the reaction of Fe(III) and HSO3–could produce H+(Eq.S8 in Supporting information), the solution pH for all the samples also decreased at the beginning of the reaction (Fig.S3a in Supporting information),which was similar to other previous studies [22,24].From Figs.S2 and S3a, it is observed that the S(IV) was consumed completely in 6 min when adding S(IV) in a time, along with that the pH value gradually decreased to around 3.55 within 6 min.However, the pH values for the samples with multiple S(IV) addition suddenly increased after adding S(IV), which can be explained by that SO32?can react with H+to produce HSO3–.Along with the increase of TBP removal efficiency (Fig.2), the residual S(IV) after reaction for 6 min also gradually increased with increasing the S(IV) addition times from 1 to 3 (Fig.S2).The results suggest that adding S(IV)in batches was not only beneficial to increase the utilization effi-ciency of S(IV), but also can ease the pH reduction.

    Fig.2 .Effect of sulfite dose times on TBP removal in the Fe(III)/S(IV) system.Conditions: [TBP]0= 10 μmol/L, [Fe(III)]0= 0.1 mmol/L, [S(IV)]total=0.4 mmol/L, pH 4.0,temperature 25 °C.

    As the removal of TBP after reaction for 6 min was similar for the samples of adding S(IV) in 2 times and 3 times (Fig.2), the experimental condition with adding S(IV) in 2 times was selected for the next experiments in this study.The changes of Fe(III), Fe(II) and total Fe concentration in the system were also monitored when S(IV) was dosed in 2 times (Fig.S4 in Supporting information).In the initial 15 s, the rapid decrease of Fe(III) and increase of Fe(II)were observed, which could be attributed to the rapid formation and decomposition of FeSO3+viareactions shown in Eqs.S8 and S9 (Supporting information), respectively [29,31,32].According to the sequence reactions shown in Eqs.S6-S17 (Supporting information), Fe(II) and Fe(III) would circulate dynamically, and the concentration tends to be stable.However, due to the consumption of S(IV), the Fe(III) concentration gradually increased along with the gradual decrease of Fe(II) concentration with extending the reaction time from 15 s to 3 min.At 3 min, significant transformation of Fe(III) to Fe(II) was observed with adding S(IV), meaning that batching addition of S(IV) could elevate the utilization efficiency of iron too.It is worthy to note that the total concentration of dissolved iron ions gradually decreased, which can be explained by the hydrolysis of iron ions [24].

    Previous reports have evidenced that SO3?–, SO4?–, SO5?–and HO?would be the main reactive radicals in the iron-activated S(IV)systems [24,28,33].SO4?–and SO5?–can be producedviathe sequence reactions shown in Eqs.S6-S17, and HO?can form through the oxidation of H2O and OH–by SO4?–[34].Due to the low oxidation ability of SO3?–, its role in the degradation of organic pollutants is always ignored in the activated S(IV) processes [20–23].However, the roles of SO4?–, SO5?–and HO?were different and controversial in different studies [22,24,28].In order to clarify which reactive species in the Fe(III)/S(IV) system contributed to TBP degradation, different radical inhibitors were used in this study.

    Based on the data shown in Table S2 and Fig.S5 (Supporting information), the reaction rate constants of TBP reacting with HO?and SO4?–were determined to be 5.51× 109L mol?1s?1and 1.36× 109L mol?1s?1, respectively, using a relative rate technique[10].Generally, TBA is considered as a good quencher for HO?(6×108L mol?1s?1) but not for SO4?–(9.1× 105L mol?1s?1) [35,36].As EtOH can fast react with SO4?–(7.7× 107L mol?1s?1) and HO?(1.9× 109L mol?1s?1) but is difficult to react with SO5?–(<1×103L mol?1s?1), EtOH can be used to scavenge both SO4?–and HO?in the Fe(III)/S(IV) process [35,37].Then the TBP removal efficiencies among the samples with adding different scavengers can tell the roles of different radicals on TBP degradation.Based on the discussion in Text S2 (Supporting information), the initial TBA and EtOH concentrations were set at 1 and 8.65 mmol/L, respectively.As shown in Fig.3a, in comparison with the control sample, the removal ratio of TBP decreased from 88.6% to 80.5% with the addition of TBA, suggesting that HO?played a small role in TBP degradation.However, TBP removal ratio significantly declined to 23.5%in the presence of EtOH, meaning that SO4?–played the dominant role in the system.Combing the results shown in Figs.1 and 3a,the removal efficiency of TBP in the Fe(III)/S(IV) system with the addition of EtOH was still higher than the sample without S(IV) or Fe(III) (around 9%), which means that SO5?–would also take part in the treatment of TBP in the Fe(III)/S(IV) system.

    Fig.3 .Effect of TBA or EtOH (a), initial Fe(III) concentration (b), and initial S(VI) concentration (c) on TBP degradation in the Fe(III)/S(IV) system with dosing S(IV) in two times.Conditions: [TBP]0= 10 μmol/L, [Fe(III)]0= 0.1 mmol/L (except b), [S(IV)]0= 0.4 mmol/L (except c), pH 4.0, temperature 25 °C.

    Fig.3 b shows the effect of different Fe(III) concentrations on TBP removal in the Fe(III)/S(IV) system.With 0.4 mmol/L S(IV)dosage and pH 4.0, the removal efficiencies of TBP only slightly increased from 83.8% to 87.5% after reaction for 6 min with the initial Fe(III) dosages increasing from 0.05 mmol/L to 0.1 mmol/L.However, when the initial Fe(III) dosage was further increased to 0.2 mmol/L, the removal efficiency dropped to 73.8%.The production of SO3?–increased with Fe(III) dose increasing from 0.05 mmol/L to 0.1 mmol/L, which would benefit the formation of SO5?–and SO4?–, causing the slight increase of TBP removal.However, with further elevating Fe(III) concentration, excessive Fe(III)would produce a large amount of Fe(II) to consume the formed SO4?–, which might be the reason for the inhibition of TBP removal [38,39].In addition, the formation of Fe(OH)3colloids at high Fe(III) concentration might also inhibit the degradation of TBP[23,24].

    Fig.3 c shows the effect of different S(IV) dosages on TBP degradation in the Fe(III)/S(IV) system, and a similar trend to the Fe(III)dosages was observed.When the initial Fe(III) dosage and pH were 0.1 mmol/L and 4.0, respectively, the TBP removal efficiencies increased rapidly from 43.3% to 87.5% after 6 min with S(IV) dosages increasing from 0.1 mmol/L to 0.4 mmol/L.As S(IV) dose was further elevated to 2.0 mmol/L, the TBP removal efficiency dropped rapidly from 87.5% to 43.5%, indicating that high concentration of S(IV) had an adverse effect on the removal efficiency, which was also reported in some previous studies [22,24].Although the supplement of S(IV) can affect the solution pH (Fig.S3a), the solution pH kept in the range of around 3.5–3.9 for all the samples with the addition of S(IV) at different concentration, meaning that the different TBP degradation efficiencies would not be due to the solution pH.It is expected that more radicals would be generated in the Fe(III)/S(IV) system with increasing the initial S(IV) concentration, which was beneficial to the removal of TBP.However, as a strong reducing agent, S(IV) could also fast consume the formed SO4?–, HO?and SO5?–at the meantime.Therefore, excess S(IV) dose played adverse role in the degradation of TBP.pH directly affects the distribution of Fe(III) and S(IV) species, which can significantly influence the treatment efficiency of pollutants in the Fe(III)/S(IV)system [23,29].Fig.S6a (Supporting information) presents the effect of different initial pH values on the degradation of TBP in the Fe(III)/S(IV) system with adding S(IV) in two times.The removal efficiencies initially increased from 25.9% to 87.5% as the pH varied from 2 to 4, then gradually decreased to 6.0% with further elevating the initial pH to 6.

    Although iron ions in the solution were the most at pH 2 and 3, SO2(aq) which is the dominant S(IV) species could not be combined by iron ions [22,23,29].In addition, the reactionviaEq.S8 would be inhibited because of the H+at pH 2 and 3 [20,29].HSO3–, the dominant S(IV) species at pH 4–6, could complex with Fe(III) to produce FeSO3+, which benefit the removal of TBP in the iron-activated processes.However, significant decline of TBP removal efficiency was observed with the initial solution pH increasing from 4 to 6, which was different from the results obtained in previous studies that high treatment efficiency was maintained in the initial pH range of 4–6 when the S(IV) was added in one time[20,22,23].To make clear the reason, the variations of solution pH were monitored.As shown in Fig.S6b (Supporting information), insignificant variations of solution pH were observed for the samples whose initial solution pH were 2, 3, and 6.While small decrease of solution pH was obtained for the samples whose initial solution pH were 4, 4.5 and 5, but the final solution pH after reaction for 6 min gradual increased with elevating the solution pH, which was different from some previous studies that similar final solution pH of around 3.5–3.8 was achieved in an initial solution pH range of 4–6 with dosing S(IV) in a time [22,23].Following the reactions shown in Eqs.S6-S17, lots of H+can be produced in the iron-activated S(IV) system, causing the decrease of solution pH[24,29].However, aforementioned discussion has proven that the addition of S(IV) consumed H+to efficiently ease the pH decline(Fig.S3 in Supporting information).Therefore, the significant decrease of TBP removal in the pH range of 4–6 would be because of the precipitation of Fe(III).

    The oxidation of SO3?–by oxygen to form SO5?–viathe reaction shown in Eq.S10 was an essential step for the subsequent production of SO4?–[22,29].In order to investigate the effect of O2on the degradation of TBP, experiments with no purging (control sample), continuous purging air and continuous purging N2were carried out with simultaneous monitoring the dissolved oxygen (DO) concentration.As shown in Fig.S7a (Supporting information), there was negligible difference of the removal efficiencies between the control sample and the sample of purging air because of the enough oxygen in the two systems (Fig.S7b in Supporting information), which was also obtained by some previous studies[23,24].However, the removal efficiency of TBP significantly decreased to 17.5% with continuous purging nitrogen, which would be due to that the lack of O2inhibited the transformation of SO3?–to SO5?–[20,24].The explanation was supported by the low DO concentration for the sample of purging N2(Fig.S7b).

    As shown in Fig.S8 (Supporting information), the removal effi-ciency of TBP significantly decreased from 97.6% to 32.9% when the TBP concentration increased from 5 μmol/L to 50 μmol/L.Although the overall removal efficiency decreased, the total removal amounts of TBP increased with the increase of initial TBP concentration.As the concentration of TBP increased, its ability to compete for radicals could be enhanced, resulting in the reduced concentrations of reactive radicals [22].While the stronger competition ability of reactive radicals by TBP elevated the total amounts of reduced TBP.

    Humic acid (HA) is a common seen representative substance of natural organic matter (NOM) which always shows negative effect on the degradation of pollutants in AOPs through the competition of reactive radicals [40,41].Fig.S9a (Supporting information) shows the effect of HA on the degradation of TBP in the Fe(III)/S(IV) system with adding S(IV) in two times.When the initial HA concentration increased from 0 mg/L to 10 mg/L, the removal efficiencies of TBP gradually decreased from 87.5% to 73.7%,which was also reported in iron-activated S(IV) systems in previous studies [20,22,24].Generally, the reaction rate constants of NOM reacting with HO?and SO4?–were at the levels of 108(L mol?1)carbons?1and 107(L mol?1)carbons?1, respectively [10,42].Although the reaction rate constants were slower than that of TBP,the high HA concentration made sure it could compete for reactive radicals to decrease TBP removal.Additionally, the carboxylic functional groups in HA would complex with Fe(III) and inhibit the formation of FeSO3+, which would also contribute to the decrease of TBP degradation [24].Fig.S9b (Supporting information) shows the effect of HCO3–on the degradation of TBP in the Fe(III)/S(IV) system.When the concentration of HCO3–increased from 0 mmol/L to 2 mmol/L, the removal efficiency of TBP decreased from 87.5%to 76.1% within 6 min.HCO3–could react with HO?and SO4?–to produce CO3?–which had much weaker oxidation ability than HO?and SO4?–[22,34], causing the decrease of TBP removal in the Fe(III)/S(IV) system.In addition, HCO3–could act as solution buffer and increase the solution pH to some extent during the reaction,which would also lower the removal of TBP.Fig.S9c (Supporting information) shows the effect of Cl–on the degradation of TBP in the Fe(III)/S(IV) system.When the concentration of Cl–increased from 0 mmol/L to 2 mmol/L, the removal efficiencies of TBP decreased from 87.5% to 74.0% after reaction for 6 min.SO4?–and HO?could be consumed through the reaction with Cl–, which would produce a sequence of reactive chlorine species, such as Cl?and Cl2?–[34,43].As these reactive chlorine species can also selectively degrade organic pollutants, the influence of Cl–on organic pollutants degradation in AOPs always depends on the reaction rate constants of these chlorine species reacting with organic pollutants [17,23].In this study, the inhibition of TBP degradation in the Fe(III)/S(IV) system would be because that the reaction rate constants between these chlorine species and TBP were lower than that of SO4?–and HO?.

    Although HA, HCO3–and Cl–could retard TBP degradation in the Fe(III)/S(IV) process with adding S(IV) in batches, good treatment efficiency can always be achieved for all the samples (>70%), suggesting that the Fe(III)/S(IV) process with adding S(IV) in batches might perform well for the treatment of TBP in natural water.

    The degradation of TBP might form 2,4-dibromophenol, an intermediate product that is more toxic than TBP [44–46].In addition, the presence of bromine atoms in TBP might produce a series of other toxic brominated intermediates and BrO3–.Therefore, inorganic bromine including Br–and BrO3–were monitored and shown in Fig.S10 (Supporting information).No BrO3–was detected during the treatment of TBP in the Fe(III)/S(IV) system, which was also observed when applying Fe(III)/S(IV) system to degrade TBBPA [23].However, the concentration of Br–gradually increased to around 20 μmol/L with extending the reaction time to 6 min, which means that about 67% of bromine atoms in the system were converted to nontoxic Br–.Additionally, two kinds of brominated intermediates including 2,6-dibromo-1,4-benzenediol and dibromophenol(2,4-dibromophenol or 2,6-dibromophenol) were detected by an ultimate 3000 complete ultra high performance liquid chromatography system (U-HPLC-Q-Exactive Orbitrap HRMs, Thermo Fisher Scientific, Waltham, MA) (Table S3 in Supporting information), suggesting that debromination and hydroxylation might be the initial reaction in the system.Combining with the result that the remained TBP was about 13% (4 μmol/L bromine atoms), it is calculated that only around 20% (6 μmol/L) of bromine atoms were contained in the brominated organic intermediates based on mass balance.As brominated organic matters usually contain higher toxicity [47], the treatment of TBP by Fe(III)/S(IV) process is expected to reduce the toxicity of TBP solution.To comprehensively evaluate the safety of applying Fe(III)/S(IV) system to degrade TBP, the variation of the acute toxicity during the reaction was investigated by luminescent bacteria [48].As shown in Fig.4, the inhibition ratio of the original reaction solution was 27.3%, which indicated that TBP had a certain toxic effect on luminescent bacteria.Then the inhibition ratio rapidly decreased to 17.6% within 1 min, and then gradually stabilized to 16.1% at 3 min, which was coincided with the disappearance of S(IV) (Fig.S2).After the addition of S(IV) again, the inhibition ratio gradually decreased to 0 in 6 min.The results reflect that adding S(IV)in batches can not only greatly increase the removal efficiency of TBP but also can greatly reduce the acute toxicity of the reaction solution.

    Fig.4 .The inhibition of luminescent bacteria during the treatment of TBP in the Fe(III)/S(IV) system with dosing S(IV) in two times.Conditions: [TBP]0= 10 μmol/L,[Fe(III)]0= 0.1 mmol/L, [S(IV)]0= 0.4 mmol/L, pH 4.0, temperature 25 °C.

    This study comprehensively evaluated the degradation of TBP in the Fe(III)/S(IV) system with adding S(IV) in batches, evidencing that the addition of S(IV) in batches could effectively increase the utilization efficiency of S(IV), which improved the removal efficiency of TBP.The oxidation of TBP was attributed to SO4?–, HO?and SO5?–as SO4?–was the primary radical.Highest TBP removal in the Fe(III)/S(IV) system was achieved at pH 4.0 in the system.In the selected experimental conditions, the treatment efficiencies followed trends of initial increase then decrease with increasing initial Fe(III) and S(IV) dosages from 0.05 and 0.1 mmol/L to 0.2 and 2.0 mmol/L, respectively.Additionally, the increase of initial TBP concentration lowered TBP removal efficiency, and oxygen has been found to be necessary for the degradation of TBP in the Fe(III)/S(IV) system.The typical water matrices including HA,HCO3–and Cl–performed negative impacts on the degradation of TBP.The significant decrease of acute toxicity after the treatment of TBP by the Fe(III)/S(IV) system with adding S(IV) in batches further suggests that this system would be a good AOP in the degradation of TBP.

    Declaration of competing interest

    The authors declare that they have no known competing financial interests or personal relationships that could have appeared to influence the work reported in this paper.

    Acknowledgments

    The support by the National Natural Science Foundation of China (No.51878308) and the Young Top-notch Talent Cultivation Program of Hubei Province are appreciated.We also thank the Analytical and Testing Center of Huazhong University of Science and Technology for the related measurements.

    Supplementary materials

    Supplementary material associated with this article can be found, in the online version, at doi:10.1016/j.cclet.2022.01.003.

    国产男女超爽视频在线观看| 日韩中文字幕视频在线看片| 在线观看美女被高潮喷水网站| 国内精品宾馆在线| tube8黄色片| 国产探花极品一区二区| 美女大奶头黄色视频| 国产精品国产三级国产av玫瑰| 人人澡人人妻人| 丝袜脚勾引网站| 日日啪夜夜爽| 免费少妇av软件| 尾随美女入室| 丰满迷人的少妇在线观看| 精品一区二区免费观看| 日本黄大片高清| 一区在线观看完整版| 亚洲国产欧美在线一区| 偷拍熟女少妇极品色| 色婷婷久久久亚洲欧美| 日本黄色片子视频| 黑人巨大精品欧美一区二区蜜桃 | 国产午夜精品久久久久久一区二区三区| 日韩欧美 国产精品| 欧美亚洲 丝袜 人妻 在线| 草草在线视频免费看| 亚洲怡红院男人天堂| 五月玫瑰六月丁香| 精品午夜福利在线看| 国产精品人妻久久久影院| 国产精品一区二区在线不卡| 精品卡一卡二卡四卡免费| 亚洲精品,欧美精品| 人人妻人人澡人人看| 亚洲国产精品专区欧美| 99热网站在线观看| 视频中文字幕在线观看| 美女福利国产在线| 在现免费观看毛片| 春色校园在线视频观看| 女的被弄到高潮叫床怎么办| 久久精品国产鲁丝片午夜精品| 国产精品久久久久久久久免| 亚洲三级黄色毛片| 国产色婷婷99| 黄色欧美视频在线观看| 国产精品国产av在线观看| 精品人妻熟女毛片av久久网站| 黄色日韩在线| 成年人免费黄色播放视频 | 国产精品国产三级国产av玫瑰| 伦理电影免费视频| 久久久国产一区二区| 久久韩国三级中文字幕| 2021少妇久久久久久久久久久| 少妇精品久久久久久久| 国产乱来视频区| 特大巨黑吊av在线直播| 欧美成人午夜免费资源| 不卡视频在线观看欧美| 欧美日韩一区二区视频在线观看视频在线| 男女边摸边吃奶| 观看av在线不卡| 菩萨蛮人人尽说江南好唐韦庄| 99久久精品热视频| 99久久精品热视频| 一级片'在线观看视频| 国产精品久久久久久av不卡| 能在线免费看毛片的网站| 另类精品久久| 黄色欧美视频在线观看| 久热这里只有精品99| 日韩熟女老妇一区二区性免费视频| 国产av精品麻豆| 亚洲精品亚洲一区二区| 男人舔奶头视频| 99热国产这里只有精品6| 青春草亚洲视频在线观看| 亚洲色图综合在线观看| 夜夜骑夜夜射夜夜干| 久久精品久久久久久久性| 香蕉精品网在线| 久久久精品免费免费高清| 欧美一级a爱片免费观看看| 亚洲无线观看免费| 国产伦在线观看视频一区| 看十八女毛片水多多多| 老司机影院毛片| 国产av精品麻豆| 国产精品.久久久| 久久热精品热| 深夜a级毛片| 久久久久视频综合| 黄色毛片三级朝国网站 | 免费观看av网站的网址| 国产免费一级a男人的天堂| 成人毛片a级毛片在线播放| 国产精品秋霞免费鲁丝片| 久久青草综合色| 五月天丁香电影| 乱系列少妇在线播放| 欧美xxxx性猛交bbbb| 国产亚洲一区二区精品| 久久久a久久爽久久v久久| 尾随美女入室| 亚洲第一区二区三区不卡| 深夜a级毛片| 国产精品秋霞免费鲁丝片| 欧美另类一区| 一级毛片久久久久久久久女| 在线 av 中文字幕| 国产无遮挡羞羞视频在线观看| 日韩电影二区| 内射极品少妇av片p| 国产白丝娇喘喷水9色精品| 亚洲精品日韩在线中文字幕| 少妇人妻久久综合中文| 一本—道久久a久久精品蜜桃钙片| 丰满迷人的少妇在线观看| 亚洲高清免费不卡视频| 国产精品熟女久久久久浪| 免费在线观看成人毛片| 欧美日韩亚洲高清精品| 午夜精品国产一区二区电影| 一级爰片在线观看| 亚洲av成人精品一区久久| 一个人看视频在线观看www免费| 日本与韩国留学比较| 99九九线精品视频在线观看视频| 国产 精品1| 日本黄色片子视频| 精品亚洲成国产av| 伦精品一区二区三区| 国产精品一区二区性色av| 少妇丰满av| 天堂8中文在线网| 国产老妇伦熟女老妇高清| 熟妇人妻不卡中文字幕| 国产成人一区二区在线| 久久久久久久久久久久大奶| 亚洲av.av天堂| 最近中文字幕高清免费大全6| 99热6这里只有精品| 中文字幕久久专区| 一级毛片黄色毛片免费观看视频| 亚洲激情五月婷婷啪啪| 日本猛色少妇xxxxx猛交久久| 国产黄片视频在线免费观看| 国产亚洲欧美精品永久| 热re99久久国产66热| 乱人伦中国视频| a级片在线免费高清观看视频| 欧美精品一区二区大全| 有码 亚洲区| 日韩亚洲欧美综合| 久久久久久久久久久丰满| 夫妻性生交免费视频一级片| 免费播放大片免费观看视频在线观看| 大片电影免费在线观看免费| 啦啦啦视频在线资源免费观看| 亚洲国产色片| 久久久精品免费免费高清| 亚洲第一区二区三区不卡| av播播在线观看一区| 18禁裸乳无遮挡动漫免费视频| av国产精品久久久久影院| 国产片特级美女逼逼视频| 人妻人人澡人人爽人人| 2021少妇久久久久久久久久久| 亚洲国产精品国产精品| 免费看不卡的av| 边亲边吃奶的免费视频| 精品久久国产蜜桃| 18禁在线无遮挡免费观看视频| 三级国产精品片| 人人妻人人爽人人添夜夜欢视频 | 日韩三级伦理在线观看| 亚洲欧美清纯卡通| 啦啦啦啦在线视频资源| 欧美激情国产日韩精品一区| 91aial.com中文字幕在线观看| 黑人高潮一二区| 人人澡人人妻人| 少妇 在线观看| 国产欧美日韩精品一区二区| 插逼视频在线观看| 女人精品久久久久毛片| 亚洲欧美清纯卡通| 丝瓜视频免费看黄片| 亚洲无线观看免费| 日本与韩国留学比较| 国产精品免费大片| 美女cb高潮喷水在线观看| 精品人妻一区二区三区麻豆| 亚洲久久久国产精品| 街头女战士在线观看网站| 亚洲欧美日韩卡通动漫| 狂野欧美白嫩少妇大欣赏| 国产免费又黄又爽又色| 人人妻人人澡人人爽人人夜夜| 看非洲黑人一级黄片| 黄色毛片三级朝国网站 | 18禁裸乳无遮挡动漫免费视频| 一本久久精品| 久久婷婷青草| 91久久精品电影网| 色哟哟·www| 老司机亚洲免费影院| tube8黄色片| 久久人妻熟女aⅴ| 国产男女内射视频| 亚洲av免费高清在线观看| 日日啪夜夜爽| 夜夜看夜夜爽夜夜摸| 亚洲国产欧美在线一区| 精品久久久精品久久久| 欧美日韩亚洲高清精品| 看免费成人av毛片| 国产黄频视频在线观看| 丰满迷人的少妇在线观看| 国产69精品久久久久777片| 午夜免费男女啪啪视频观看| 22中文网久久字幕| 夫妻午夜视频| 国产精品熟女久久久久浪| 精品久久久噜噜| 免费观看av网站的网址| 免费不卡的大黄色大毛片视频在线观看| 中文字幕av电影在线播放| 特大巨黑吊av在线直播| 国产成人一区二区在线| av播播在线观看一区| 国产亚洲欧美精品永久| 丝袜脚勾引网站| 亚洲丝袜综合中文字幕| 久久久亚洲精品成人影院| 一级a做视频免费观看| 午夜老司机福利剧场| 久久精品国产a三级三级三级| 成人免费观看视频高清| 亚洲精品日韩av片在线观看| 黄色怎么调成土黄色| 亚洲国产成人一精品久久久| 欧美激情国产日韩精品一区| 交换朋友夫妻互换小说| 国产精品免费大片| 久久久久网色| 久久毛片免费看一区二区三区| 婷婷色麻豆天堂久久| 亚洲欧洲精品一区二区精品久久久 | 亚洲国产毛片av蜜桃av| 制服丝袜香蕉在线| 啦啦啦在线观看免费高清www| 如何舔出高潮| 黄片无遮挡物在线观看| 国产片特级美女逼逼视频| 性高湖久久久久久久久免费观看| 青青草视频在线视频观看| 美女中出高潮动态图| 搡女人真爽免费视频火全软件| 亚洲精品第二区| 久久人妻熟女aⅴ| 91久久精品国产一区二区成人| kizo精华| 国产亚洲午夜精品一区二区久久| 涩涩av久久男人的天堂| 亚洲欧洲国产日韩| 亚洲精品456在线播放app| 亚洲av欧美aⅴ国产| 美女内射精品一级片tv| 欧美人与善性xxx| 午夜久久久在线观看| 新久久久久国产一级毛片| 精华霜和精华液先用哪个| 亚洲欧美一区二区三区国产| 成人毛片60女人毛片免费| 亚洲成人手机| 女人久久www免费人成看片| 我要看日韩黄色一级片| 中文字幕久久专区| 久久久久久久久大av| 国产精品久久久久久久久免| 如日韩欧美国产精品一区二区三区 | 国产成人免费无遮挡视频| 欧美老熟妇乱子伦牲交| 男女国产视频网站| 99久久精品一区二区三区| 一本—道久久a久久精品蜜桃钙片| 在线亚洲精品国产二区图片欧美 | 国产精品女同一区二区软件| 另类亚洲欧美激情| 久久久精品94久久精品| 一级毛片aaaaaa免费看小| 一级毛片 在线播放| 18禁动态无遮挡网站| av在线观看视频网站免费| 亚洲精品日本国产第一区| www.av在线官网国产| 美女xxoo啪啪120秒动态图| 青春草视频在线免费观看| 美女国产视频在线观看| 十八禁高潮呻吟视频 | 国产在视频线精品| 十八禁网站网址无遮挡 | 色94色欧美一区二区| 美女xxoo啪啪120秒动态图| 久热这里只有精品99| 亚洲自偷自拍三级| 丝袜喷水一区| 亚洲一级一片aⅴ在线观看| 亚洲精品乱码久久久v下载方式| 深夜a级毛片| 久久精品国产亚洲网站| 午夜福利网站1000一区二区三区| 2021少妇久久久久久久久久久| 国产高清不卡午夜福利| 嫩草影院入口| 欧美最新免费一区二区三区| 国产精品久久久久久av不卡| 黄色日韩在线| 精品卡一卡二卡四卡免费| 黄色一级大片看看| 久久 成人 亚洲| 亚洲,欧美,日韩| 我要看日韩黄色一级片| 欧美高清成人免费视频www| 九色成人免费人妻av| 丁香六月天网| 我的女老师完整版在线观看| 一个人免费看片子| 亚洲自偷自拍三级| 精品一区二区三卡| 一边亲一边摸免费视频| 久久这里有精品视频免费| 午夜激情久久久久久久| 免费人成在线观看视频色| 亚洲精品色激情综合| 精品亚洲成国产av| 亚洲精品色激情综合| 国产亚洲av片在线观看秒播厂| 成人国产麻豆网| 中文字幕免费在线视频6| 国产真实伦视频高清在线观看| 99热6这里只有精品| 一级,二级,三级黄色视频| 简卡轻食公司| a级毛片在线看网站| 下体分泌物呈黄色| a级毛片在线看网站| 精品人妻熟女av久视频| 亚洲精品亚洲一区二区| 狂野欧美白嫩少妇大欣赏| 22中文网久久字幕| 亚洲精品成人av观看孕妇| 男女啪啪激烈高潮av片| 麻豆精品久久久久久蜜桃| 日日啪夜夜撸| 啦啦啦啦在线视频资源| 美女主播在线视频| 九九爱精品视频在线观看| 人人妻人人澡人人看| 九九爱精品视频在线观看| 少妇人妻 视频| 高清毛片免费看| 精品国产一区二区久久| 精品亚洲成a人片在线观看| 日韩制服骚丝袜av| 国产亚洲av片在线观看秒播厂| 女人精品久久久久毛片| 久久国产精品男人的天堂亚洲 | 亚洲欧美成人综合另类久久久| 国产91av在线免费观看| 亚洲欧美成人综合另类久久久| 久久久久久人妻| 少妇被粗大猛烈的视频| av线在线观看网站| av免费在线看不卡| 日韩视频在线欧美| 夫妻午夜视频| 色5月婷婷丁香| 观看美女的网站| 99国产精品免费福利视频| 嫩草影院新地址| 岛国毛片在线播放| 日韩欧美精品免费久久| 制服丝袜香蕉在线| 欧美xxxx性猛交bbbb| 男人舔奶头视频| 日韩一区二区三区影片| 在线观看免费日韩欧美大片 | 日本黄色日本黄色录像| 国产成人a∨麻豆精品| 久久女婷五月综合色啪小说| 日韩欧美精品免费久久| 我的老师免费观看完整版| 国产 精品1| 亚洲一区二区三区欧美精品| 超碰97精品在线观看| 亚洲精品日韩av片在线观看| 亚洲图色成人| 五月玫瑰六月丁香| 成人午夜精彩视频在线观看| 国产精品女同一区二区软件| av有码第一页| 亚洲欧美清纯卡通| av网站免费在线观看视频| 亚洲人与动物交配视频| 国产精品无大码| 国产精品久久久久久久久免| 少妇人妻久久综合中文| 亚洲三级黄色毛片| 中国国产av一级| 内射极品少妇av片p| 91久久精品国产一区二区成人| 国产精品一区二区在线观看99| 精品久久久精品久久久| 午夜福利网站1000一区二区三区| 久久精品国产亚洲网站| 3wmmmm亚洲av在线观看| 精品亚洲成a人片在线观看| 国产精品人妻久久久影院| 一级毛片aaaaaa免费看小| 亚洲欧洲精品一区二区精品久久久 | 日韩视频在线欧美| av天堂久久9| 伊人久久精品亚洲午夜| 最后的刺客免费高清国语| 大话2 男鬼变身卡| 午夜激情福利司机影院| 欧美日韩精品成人综合77777| 欧美成人午夜免费资源| 777米奇影视久久| 少妇被粗大的猛进出69影院 | 观看av在线不卡| 亚洲图色成人| 久久久国产一区二区| kizo精华| 少妇猛男粗大的猛烈进出视频| 国产av码专区亚洲av| 五月天丁香电影| 婷婷色麻豆天堂久久| 亚洲精品456在线播放app| 日本wwww免费看| 91成人精品电影| 国产男女内射视频| 亚洲久久久国产精品| av卡一久久| 高清午夜精品一区二区三区| 久久精品夜色国产| 国产一区二区在线观看日韩| 国产精品麻豆人妻色哟哟久久| 欧美国产精品一级二级三级 | 一本久久精品| 亚洲激情五月婷婷啪啪| 中文字幕制服av| 一本—道久久a久久精品蜜桃钙片| 国产欧美日韩精品一区二区| 日本av手机在线免费观看| 免费av不卡在线播放| 大香蕉97超碰在线| 国产黄色免费在线视频| 成年av动漫网址| 国产欧美另类精品又又久久亚洲欧美| av视频免费观看在线观看| 在线观看美女被高潮喷水网站| 成人亚洲精品一区在线观看| 女性被躁到高潮视频| 亚洲精品自拍成人| 国产爽快片一区二区三区| 久久久久视频综合| 久久久欧美国产精品| 国精品久久久久久国模美| 夜夜看夜夜爽夜夜摸| 久久精品夜色国产| 又大又黄又爽视频免费| 久久狼人影院| 人人妻人人添人人爽欧美一区卜| 精品国产露脸久久av麻豆| 国产美女午夜福利| 久久精品国产自在天天线| 乱码一卡2卡4卡精品| 嫩草影院入口| 国产免费一级a男人的天堂| 国产精品一二三区在线看| 视频区图区小说| 久久国产精品男人的天堂亚洲 | 一级a做视频免费观看| 99re6热这里在线精品视频| 精品卡一卡二卡四卡免费| 日韩欧美 国产精品| 亚洲精品中文字幕在线视频 | 国产91av在线免费观看| 午夜激情久久久久久久| 精品人妻熟女毛片av久久网站| 欧美另类一区| 大香蕉久久网| 麻豆成人午夜福利视频| av免费观看日本| 国产高清三级在线| 偷拍熟女少妇极品色| 欧美日韩综合久久久久久| 亚洲欧美一区二区三区国产| 街头女战士在线观看网站| 又爽又黄a免费视频| 国产成人精品婷婷| 不卡视频在线观看欧美| 男人和女人高潮做爰伦理| 中文欧美无线码| 91成人精品电影| 国产精品一区二区在线不卡| 大陆偷拍与自拍| 99热6这里只有精品| 精品国产一区二区久久| 两个人免费观看高清视频 | 午夜福利在线观看免费完整高清在| 乱系列少妇在线播放| 亚洲精品,欧美精品| 97在线人人人人妻| 日韩强制内射视频| 黑丝袜美女国产一区| 99热6这里只有精品| 亚洲国产av新网站| 国产精品国产av在线观看| 亚洲成人手机| 亚洲av国产av综合av卡| 久久久久久久久久久丰满| av一本久久久久| 亚洲成色77777| 国产黄色视频一区二区在线观看| 一区二区av电影网| 午夜免费观看性视频| 在线观看免费高清a一片| 久久久久久久久久久久大奶| 丝瓜视频免费看黄片| 成人特级av手机在线观看| 国产精品一区二区三区四区免费观看| a 毛片基地| 日韩不卡一区二区三区视频在线| 精品一品国产午夜福利视频| 久久韩国三级中文字幕| 日韩一本色道免费dvd| 亚洲图色成人| 久久午夜综合久久蜜桃| 一级毛片黄色毛片免费观看视频| 另类精品久久| 自拍欧美九色日韩亚洲蝌蚪91 | 国产亚洲精品久久久com| 自拍偷自拍亚洲精品老妇| 极品少妇高潮喷水抽搐| 偷拍熟女少妇极品色| 亚洲电影在线观看av| 另类精品久久| 午夜激情久久久久久久| 成人免费观看视频高清| 99热6这里只有精品| 女人精品久久久久毛片| 国产精品99久久久久久久久| av不卡在线播放| 精品久久久久久久久亚洲| 久久精品熟女亚洲av麻豆精品| 中文字幕av电影在线播放| 欧美精品人与动牲交sv欧美| 国产深夜福利视频在线观看| 日韩强制内射视频| 日本免费在线观看一区| 亚洲精品456在线播放app| 亚洲内射少妇av| 亚洲av二区三区四区| 少妇熟女欧美另类| 最近最新中文字幕免费大全7| 99国产精品免费福利视频| 精品一区二区三区视频在线| 免费播放大片免费观看视频在线观看| 另类亚洲欧美激情| 亚洲欧美清纯卡通| 婷婷色综合大香蕉| 成人午夜精彩视频在线观看| 午夜老司机福利剧场| 亚洲美女黄色视频免费看| 成人综合一区亚洲| 热re99久久国产66热| 只有这里有精品99| 夜夜爽夜夜爽视频| 热re99久久国产66热| 亚洲精品,欧美精品| 国产免费又黄又爽又色| 午夜福利视频精品| 只有这里有精品99| 中文字幕久久专区| 18禁在线无遮挡免费观看视频| 国产黄频视频在线观看| 中文字幕久久专区| 王馨瑶露胸无遮挡在线观看| 国产午夜精品久久久久久一区二区三区| 精品一区二区三卡| 亚洲婷婷狠狠爱综合网| 自拍偷自拍亚洲精品老妇| 男人添女人高潮全过程视频| 六月丁香七月| 欧美日韩在线观看h| 秋霞伦理黄片| 一本久久精品| 欧美bdsm另类| 在线播放无遮挡| 成年人午夜在线观看视频| 国产一区二区在线观看av| 亚洲久久久国产精品| 亚洲欧美一区二区三区国产| 日韩大片免费观看网站| 久久久久国产网址| 久久精品国产亚洲网站| 又粗又硬又长又爽又黄的视频| 免费av不卡在线播放| 国产一级毛片在线| 多毛熟女@视频|