Ag2CO3 Decorating BiOCOOH Microspheres with Enhanced Full-Spectrum Photocatalytic Activity for the Degradation of Toxic Pollutants

The development of excellent full-spectrum photocatalysts is of vital significance to its practical application in environmental remediation. Herein, flower-like Ag2CO3/BiOCOOH type I heterostructures were prepared via a facile method and exhibited powerful photocatalytic activity by removing various toxic pollutants (rhodamine B, methyl blue, and tetracycline hydrochloride) under simulated sunlight irradiation. The boosted photocatalytic performance is attributed to the expanded range of the absorption spectrum and alleviated separation rate of the photo-induced electrons and holes. The photoluminescence spectra and trapping experiment were applied to clarify the photocatalytic reaction mechanism of Ag2CO3/BiOCOOH. The holes and •O2− were detected as the dominant reactive species involved in pollutant degradation. This work provides a novel full-spectrum-driven photocatalyst of Ag2CO3/BiOCOOH, which could effectively degrade toxic pollutants under simulated sunlight.

In this study, aiming at the construction of highly active sunlight-driven photocatalysts, flower-like Ag 2 CO 3 /BiOCOOH heterojunctions were prepared via a simple precipitation approach.Under simulated sunlight irradiation, the photocatalytic property of Ag 2 CO 3 /BiOCOOH in the removal of various toxic pollutants (rhodamine B (RhB), methyl blue (MB), and tetracycline hydrochloride (TC)) was evaluated.In addition, the photocatalytic mechanism of Ag 2 CO 3 /BiOCOOH was also illustrated based on the experimental results.

Synthesis of Catalysts
BiOCOOH microspheres were prepared solvothermally.Typically, Bi(NO 3 ) 3 •5H 2 O (4 mmol) is dissolved in 50 mL of glycerol under vigorous stirring.After dissolution, 20 mL of DMF and 10 mL of H 2 O were added into the above solution and stirred for 0.5 h.The obtained solution was poured into an autoclave with a volume of 100 mL and solvothermally treated at 160 • C for 24 h.After the reaction ended, the products collected from the suspension were washed with deionized water and ethanol four times, and finally transferred into an oven to get dried at 60 • C for 15 h.
Flower-like Ag 2 CO 3 /BiOCOOH heterojunctions were fabricated by chemical deposition.Firstly, a certain amount of BiOCOOH was evenly dispersed in 50 mL of deionized water during magnetic stirring.Subsequently, 1 mmol AgNO 3 was dissolved in the above system during magnetic stirring.Then, 10 mL of NaHCO 3 solution (0.05 M) was dropped into the above system slowly and stirred for another 2 h in darkness.Following this, the precipitant was washed thoroughly, and dried at 60 • C for 6 h.By changing the addition amount of BiOCOOH, the Ag 2 CO 3 /BiOCOOH heterojunctions with different mass ratios (0.3/1, 0.5/1, 1/1 and 1.5/1) were prepared and labelled as ACO/BOCH-30, ACO/BOCH-50, ACO/BOCH-100, and ACO/BOCH-150, respectively.

Photocatalytic Performance Tests
The photo-degradation of rhodamine B (RhB), methyl blue (MB) or tetracycline hydrochloride (TC) under simulated sunlight was performed to assess the activity of catalysts.Briefly, 30 mg of catalyst was dispersed evenly in 100 mL of RhB (10 mg/L), MB (10 mg/L), or TC (20 mg/L) solution while magnetically stirring for 30 min in the dark to establish an adsorption-desorption equilibrium [34,35].The reaction system was maintained at room temperature by using circulating water.Subsequently, the above system was illuminated by a 300 W xenon lamp with an average light intensity of 4.56 KW/m 2 .During illumination, approximately 2 mL of the suspensions were sampled at certain intervals, and then centrifuged to get the supernatant solutions.The concentrations of solutions were quantified by using a UV-2600 spectrophotometer.Total organic carbon (TOC) experiments were carried out by the decomposition of RhB (50 mg/L, 200 mL) solution over 200 mg of ACO/BOCH-100 under simulated sunlight.The reaction solution collected at given intervals was detected by a Shimadzu TOC-VCPH TOC analyzer.To test the stability and reusability of ACO/BOCH-100, six successive runs for RhB degradation were performed, and each run lasted 30 min.After one cycle of photocatalytic reaction, the catalysts recycled by centrifugation and were washed thoroughly with deionized water and dried at 70 • C overnight.Subsequently, the dried catalysts were used to degrade the RhB solution again.During the recycling process, about 4.7 mg of the catalyst was lost.
The morphologies of BiOCOOH and the Ag 2 CO 3 /BiOCOOH heterojunction (ACO/BOCH-100) were visualized by SEM and TEM (Figure 2 and Figure S1).Pure BiOCOOH presented a flower-like structure (diameter: 1.5-2.5 µm), which was composed of numerous nanoplates (Figure S1).After its combination with Ag 2 CO 3 , the obtained Ag 2 CO 3 /BiOCOOH (ACO/BOCH-100) displayed a similar morphology to the BiOCOOH (Figure 2a).Further magnification of the image as presented in Figure 2b revealed that Ag 2 CO 3 nanoparticles (size: 30-150 nm) were anchored onto the BiOCOOH microsphere.Further observation through TEM imaging (Figure 2c,d) confirmed that ACO/BOCH-100 was a flower-like architecture decorated by Ag 2 CO 3 nanoparticles, verifying the successful fabrication of Ag 2 CO 3 /BiOCOOH with an intimately contacted interface.Furthermore, as shown in the energy dispersive spectroscopy (EDS) spectra, Ag, C, O, and Bi in ACO/BOCH-100 could be detected, testifying that the sample was Ag 2 CO 3 /BiOCOOH (Figure 3).
The surface texturing of BiOCOOH and ACO/BOCH-100 were analyzed by the N 2 adsorptiondesorption isotherms (Figure S2).The BET specific surface areas of BiOCOOH and ACO/BOCH-100 were 26.2 and 22.7 m −2 g −1 , respectively.The BJH pore-size distributions revealed the presence of nanopores with the main pore size of 31 nm in BiOCOOH and ACO/BOCH-100 (the inset of Figure S2).The absorption band edges of pristine Ag 2 CO 3 and BiOCOOH were about 470 and 365 nm, respectively, in agreement with previously reported results.The light absorption near the band edge followed the Tauc equation: αhν = A (hν − E g ) n/2 , where α, h, ν, and A were the absorption coefficient, Planck's constant, light frequency, and the constant, respectively.According to the calculated Tauc's plot (Figure S3), the band gaps (E g ) of Ag 2 CO 3 and BiOCOOH were 2.17 and 3.40 eV, in accordance with the results previously reported [8,23,32].
The conduction band (CB) and valence band (VB) potentials of BiOCOOH and Ag 2 CO 3 were calculated by the empirical equations: where the X is the absolute electronegativity of the semiconductor, the E 0 value equals to ~4.5 eV, E g is the band gap of the semiconductor.Based on the equations above, the E CB and E VB of BiOCOOH were estimated to be −0.67 and 2.73 eV, and those of Ag 2 CO 3 were calculated as 0.43 and 2.60 eV.
The photoluminescence (PL) was measured to investigate the separation efficiency of electrons and holes [36][37][38][39].Figure 4b presents the PL spectra of BiOCOOH and ACO/BOCH-100.Clearly, BiOCOOH had a strong emission peak centered at around 370 nm.The PL emission peak of ACO/BOCH-100 was weaker than that of bare BiOCOOH, signifying that the recombination of carriers was pronouncedly reduced.
(UV) light region.The absorption band edges of pristine Ag2CO3 and BiOCOOH were about 470 and 365 nm, respectively, in agreement with previously reported results.The light absorption near the band edge followed the Tauc equation: αhν = A (hν − Eg) n/2 , where α, h, ν, and A were the absorption coefficient, Planck's constant, light frequency, and the constant, respectively.According to the calculated Tauc's plot (Figure S3), the band gaps (Eg) of Ag2CO3 and BiOCOOH were 2.17 and 3.40 eV, in accordance with the results previously reported [8,23,32].
The conduction band (CB) and valence band (VB) potentials of BiOCOOH and Ag2CO3 were calculated by the empirical equations: where the X is the absolute electronegativity of the semiconductor, the E0 value equals to ~4.5 eV, Eg is the band gap of the semiconductor.Based on the equations above, the ECB and EVB of BiOCOOH were estimated to be −0.67 and 2.73 eV, and those of Ag2CO3 were calculated as 0.43 and 2.60 eV.
The photoluminescence (PL) was measured to investigate the separation efficiency of electrons and holes [36][37][38][39].Figure 4b presents the PL spectra of BiOCOOH and ACO/BOCH-100.Clearly, BiOCOOH had a strong emission peak centered at around 370 nm.The PL emission peak of ACO/BOCH-100 was weaker than that of bare BiOCOOH, signifying that the recombination of carriers was pronouncedly reduced.

Photocatalytic Performance
The photocatalytic performances of Ag2CO3/BiOCOOH were assessed by degrading industrial dyes (RhB and MB), and antibiotic (TC) under simulated sunlight.Figure 5a presents the RhB degradation curves with various catalysts.No RhB was degraded in the absence of catalysts.The RhB degradation efficiency by using BiOCOOH, Ag2CO3 or Ag/Ag2CO3 reached 31.3%, 98.7% or 100% in 60 min of reaction.As BiOCOOH combined with Ag2CO3, the activity of these heterojunctions was pronouncedly enhanced and much higher than pure BiOCOOH.Among these Ag2CO3/BiOCOOH heterojunctions, ACO/BOCH-100 showed the highest photocatalytic activity with 100% of RhB degraded within 30 min, which was much higher than using Ag2CO3/Ag (76.1%), or Ag2CO3 (60.8%).
To illustrate the synergistic effect between Ag2CO3 and BiOCOOH, the RhB photodegradation efficiency using the mechanical mixture (50 wt% Ag2CO3 + 50 wt% BiOCOOH) as the catalyst, was tested, which was much lower than that achieved by using ACO/BOCH-100, revealing that the formation of the Ag2CO3/BiOCOOH heterojunction can effectively boost the photocatalytic performance.Notably, the content of Ag2CO3 in the heterojunction played a significant role in enhancing the photocatalytic performance of as-prepared samples.However, when the loading amount of Ag2CO3 was high (ACO/BOCH-150), BiOCOOH was decorated by excessive Ag2CO3 nanoparticles with a relatively larger size, resulting in decreased photocatalytic activity.
Figure 5b shows the degradation curves of RhB with the reaction time in the presence of ACO/BOCH-100.Obviously, the major absorption peak at 554 nm rapidly decreased as the reaction time prolonged, indicating the decomposition of the structure.After 30 min of reaction, 100% of RhB was degraded, demonstrating the distinguished photocatalytic activity of ACO/BOCH-100 under simulated sunlight.
The reaction kinetics of RhB degradation over various catalysts was further studied.The experimental data could be fitted well with the pseudo-first-order model (Figure S4).It was found that ACO/BOCH-100 had the highest rate constant value of 0.1335 min −1 , approximately 22.6, 2.1, or 5.2 folds that of pristine BiOCOOH (0.0059 min −1 ), Ag2CO3 (0.0638 min −1 ), or the mixture (0.0258 min −1 ).
MB dye and TC antibiotic, two refractory contaminants were also used to further investigate the photocatalytic activity of Ag2CO3/BiOCOOH under simulated sunlight (Figure 6, Figures S5 and S6).Notably, the MB degradation efficiency gained by employing ACO/BOCH-100 was as high as 100% within 60 min of irradiation, markedly higher than that gained by employing pristine BiOCOOH (42.7%),Ag2CO3 (79.3%),Ag/Ag2CO3 (89.7%), or a mechanical mixture (70.4%) as the photocatalyst.Additionally, a similar phenomenon was observed when using TC (Figure 6 and Figure S6) as a model contaminant.The optimal ACO/BOCH-100 possessed high photocatalytic activity with a TC

Photocatalytic Performance
The photocatalytic performances of Ag 2 CO 3 /BiOCOOH were assessed by degrading industrial dyes (RhB and MB), and antibiotic (TC) under simulated sunlight.Figure 5a presents the RhB degradation curves with various catalysts.No RhB was degraded in the absence of catalysts.The RhB degradation efficiency by using BiOCOOH, Ag 2 CO 3 or Ag/Ag 2 CO 3 reached 31.3%, 98.7% or 100% in 60 min of reaction.As BiOCOOH combined with Ag 2 CO 3 , the activity of these heterojunctions was pronouncedly enhanced and much higher than pure BiOCOOH.Among these Ag 2 CO 3 /BiOCOOH heterojunctions, ACO/BOCH-100 showed the highest photocatalytic activity with 100% of RhB degraded within 30 min, which was much higher than using Ag 2 CO 3 /Ag (76.1%), or Ag 2 CO 3 (60.8%).To illustrate the synergistic effect between Ag 2 CO 3 and BiOCOOH, the RhB photodegradation efficiency using the mechanical mixture (50 wt% Ag 2 CO 3 + 50 wt% BiOCOOH) as the catalyst, was tested, which was much lower than that achieved by using ACO/BOCH-100, revealing that the formation of the Ag 2 CO 3 /BiOCOOH heterojunction can effectively boost the photocatalytic performance.Notably, the content of Ag 2 CO 3 in the heterojunction played a significant role in enhancing the photocatalytic performance of as-prepared samples.However, when the loading amount of Ag 2 CO 3 was high (ACO/BOCH-150), BiOCOOH was decorated by excessive Ag 2 CO 3 nanoparticles with a relatively larger size, resulting in decreased photocatalytic activity.
Figure 5b shows the degradation curves of RhB with the reaction time in the presence of ACO/BOCH-100.Obviously, the major absorption peak at 554 nm rapidly decreased as the reaction time prolonged, indicating the decomposition of the structure.After 30 min of reaction, 100% of RhB was degraded, demonstrating the distinguished photocatalytic activity of ACO/BOCH-100 under simulated sunlight.
The reaction kinetics of RhB degradation over various catalysts was further studied.The experimental data could be fitted well with the pseudo-first-order model (Figure S4).It was found that ACO/BOCH-100 had the highest rate constant value of 0.1335 min −1 , approximately 22.6, 2.1, or 5.2 folds that of pristine BiOCOOH (0.0059 min −1 ), Ag 2 CO 3 (0.0638 min −1 ), or the mixture (0.0258 min −1 ).
MB dye and TC antibiotic, two refractory contaminants were also used to further investigate the photocatalytic activity of Ag 2 CO 3 /BiOCOOH under simulated sunlight (Figure 6, Figures S5 and  S6).Notably, the MB degradation efficiency gained by employing ACO/BOCH-100 was as high as 100% within 60 min of irradiation, markedly higher than that gained by employing pristine BiOCOOH (42.7%),Ag 2 CO 3 (79.3%),Ag/Ag 2 CO 3 (89.7%),or a mechanical mixture (70.4%) as the photocatalyst.Additionally, a similar phenomenon was observed when using TC (Figure 6 and Figure S6) as a model contaminant.The optimal ACO/BOCH-100 possessed high photocatalytic activity with a TC degradation efficiency of 93.4% in 120 min, much greater than those of pure BiOCOOH (31.8%),Ag 2 CO 3 (60.3%),Ag/Ag 2 CO 3 (67.2%),as well as their physical mixture (52.3%).The results indicated that Ag 2 CO 3 /BiOCOOH had no-selectivity and could effectively decompose various toxic pollutants under simulated sunlight.
Nanomaterials 2018, 8, x FOR PEER REVIEW 7 of 12 degradation efficiency of 93.4% in 120 min, much greater than those of pure BiOCOOH (31.8%),Ag2CO3 (60.3%),Ag/Ag2CO3 (67.2%), as well as their physical mixture (52.3%).The results indicated that Ag2CO3/BiOCOOH had no-selectivity and could effectively decompose various toxic pollutants under simulated sunlight.The photocatalytic performances of other reported catalysts for RhB removal were listed in Table S1.Notably, our catalyst showed a higher removal rate than other catalysts with similar/higher dosage of catalyst.Therefore, the Ag2CO3/BiOCOOH heterojunction possesses an excellent photocatalysis property for removing organic pollutants under simulated sunlight.
The mineralization ability of a catalyst is vital for its practical application [40,41].Therefore, the TOC values during the degradation of RhB (150 mL, 50 mg L −1 ) over ACO/BOCH-100 (200 mg) were determined.As shown in Figure 7a, 83.7% of TOC was removed after 5 h of irradiation, indicating that ACO/BOCH-100 holds a huge potential for the deep treatment of toxic contaminants.degradation efficiency of 93.4% in 120 min, much greater than those of pure BiOCOOH (31.8%),Ag2CO3 (60.3%),Ag/Ag2CO3 (67.2%), as well as their physical mixture (52.3%).The results indicated that Ag2CO3/BiOCOOH had no-selectivity and could effectively decompose various toxic pollutants under simulated sunlight.The photocatalytic performances of other reported catalysts for RhB removal were listed in Table S1.Notably, our catalyst showed a higher removal rate than other catalysts with similar/higher dosage of catalyst.Therefore, the Ag2CO3/BiOCOOH heterojunction possesses an excellent photocatalysis property for removing organic pollutants under simulated sunlight.
The mineralization ability of a catalyst is vital for its practical application [40,41].Therefore, the TOC values during the degradation of RhB (150 mL, 50 mg L −1 ) over ACO/BOCH-100 (200 mg) were determined.As shown in Figure 7a, 83.7% of TOC was removed after 5 h of irradiation, indicating that ACO/BOCH-100 holds a huge potential for the deep treatment of toxic contaminants.The photocatalytic performances of other reported catalysts for RhB removal were listed in Table S1.Notably, our catalyst showed a higher removal rate than other catalysts with similar/higher dosage of catalyst.Therefore, the Ag 2 CO 3 /BiOCOOH heterojunction possesses an excellent photocatalysis property for removing organic pollutants under simulated sunlight.
The mineralization ability of a catalyst is vital for its practical application [40,41].Therefore, the TOC values during the degradation of RhB (150 mL, 50 mg L −1 ) over ACO/BOCH-100 (200 mg) were determined.As shown in Figure 7a, 83.7% of TOC was removed after 5 h of irradiation, indicating that ACO/BOCH-100 holds a huge potential for the deep treatment of toxic contaminants.The reusability of ACO/BOCH-100 was investigated via recycling for six runs in the removal of RhB and each run lasted 30 min.Figure 7b shows the photocatalytic performance of recycled ACO/BOCH-100.It was observed that the degradation efficiency of RhB at 30 min of the sixth run was 89.2%, which showed no apparent decrease compared with that (100%) of the first run, demonstrating the good stability of ACO/BOCH-100.During the photocatalytic process, it was found that there was a mass loss of 30 mg for the first run to 25.3 mg for the sixth run.Thus, the slight decline in activity should be attributed to the loss of catalysts during the recycling process.Moreover, the XRD characterization has demonstrated the formation of Ag2CO3/Ag after recycling experiments (Figure S7), which has been recognized as a stable hetero-structure [25,32].These results indicate that ACO/BOCH-100 belongs to a type of stable catalysts.

Photocatalytic Mechanism
Radical trapping experiments were conducted to investigate the effect of reactive species on the degradation of RhB over Ag2CO3/BiOCOOH [3,30,42].As indicated in Figure 8, the RhB degradation efficiency reached 100% in the absence of a quencher.With the introduction of isopropanol (IPA), benzoquinone (BQ) and ammonium oxalate (AO), the photocatalytic activity of ACO/BOCH-100 was greatly suppressed, with RhB degradation efficiencies of 87.9%, 65.7% and 49.8%, respectively.The results demonstrated that •OH, •O2 − and h + were generated during photocatalysis, and •O2 − and h + were mainly responsible for RhB degradation over Ag2CO3/BiOCOOH.
On the basis of the results from systematic characterizations, the possible photocatalytic mechanism for contaminant degradation over Ag2CO3/BiOCOOH under simulated sunlight was proposed as outlined in Figure 9. Electrons and holes are produced in Ag2CO3 and BiOCOOH under simulated sunlight.Afterwards, the photo-generated electrons on CB and holes on VB of BiOCOOH tend to transfer to those of Ag2CO3 accordingly.Such a transfer process is beneficial to the separation of electrons and holes [43], as verified by the PL characterization (Figure 4b).Additionally, the photoelectrons can drift to the surface of Ag2CO3, leading to the formation of metallic Ag via the reduction of partial Ag + (Ag2CO3).The produced metallic Ag can further facilitate electron migration to retard the recombination of charge carriers [44].Finally, the electrons stored on the CB of metallic Ag can react with O2 to yield •O2 − radicals, which can be consumed to degrade toxic pollutants (RhB/MB/TC).Meanwhile, the holes that have accumulated on the VB of Ag2CO3 are involved in the degradation of toxic contaminants.Apparently, the results illustrate that the construction of type I heterojunction between Ag2CO3 and BiOCOOH can facilitate the separation of charge carriers, further improving the photocatalytic performance.The reusability of ACO/BOCH-100 was investigated via recycling for six runs in the removal of RhB and each run lasted 30 min.Figure 7b shows the photocatalytic performance of recycled ACO/BOCH-100.It was observed that the degradation efficiency of RhB at 30 min of the sixth run was 89.2%, which showed no apparent decrease compared with that (100%) of the first run, demonstrating the good stability of ACO/BOCH-100.During the photocatalytic process, it was found that there was a mass loss of 30 mg for the first run to 25.3 mg for the sixth run.Thus, the slight decline in activity should be attributed to the loss of catalysts during the recycling process.Moreover, the XRD characterization has demonstrated the formation of Ag 2 CO 3 /Ag after recycling experiments (Figure S7), which has been recognized as a stable hetero-structure [25,32].These results indicate that ACO/BOCH-100 belongs to a type of stable catalysts.

Photocatalytic Mechanism
Radical trapping experiments were conducted to investigate the effect of reactive species on the degradation of RhB over Ag 2 CO 3 /BiOCOOH [3,30,42].As indicated in Figure 8, the RhB degradation efficiency reached 100% in the absence of a quencher.With the introduction of isopropanol (IPA), benzoquinone (BQ) and ammonium oxalate (AO), the photocatalytic activity of ACO/BOCH-100 was greatly suppressed, with RhB degradation efficiencies of 87.9%, 65.7% and 49.8%, respectively.The results demonstrated that •OH, •O 2 − and h + were generated during photocatalysis, and •O 2 − and h + were mainly responsible for RhB degradation over Ag 2 CO 3 /BiOCOOH.On the basis of the results from systematic characterizations, the possible photocatalytic mechanism for contaminant degradation over Ag 2 CO 3 /BiOCOOH under simulated sunlight was proposed as outlined in Figure 9. Electrons and holes are produced in Ag 2 CO 3 and BiOCOOH under simulated sunlight.Afterwards, the photo-generated electrons on CB and holes on VB of BiOCOOH tend to transfer to those of Ag 2 CO 3 accordingly.Such a transfer process is beneficial to the separation of electrons and holes [43], as verified by the PL characterization (Figure 4b).Additionally, the photoelectrons can drift to the surface of Ag 2 CO 3 , leading to the formation of metallic Ag via the reduction of partial Ag + (Ag 2 CO 3 ).The produced metallic Ag can further facilitate electron migration to retard the recombination of charge carriers [44].Finally, the electrons stored on the CB of metallic Ag can react with O 2 to yield •O 2 − radicals, which can be consumed to degrade toxic pollutants (RhB/MB/TC).Meanwhile, the holes that have accumulated on the VB of Ag 2 CO 3 are involved in the degradation of toxic contaminants.Apparently, the results illustrate that the construction of type I heterojunction between Ag 2 CO 3 and BiOCOOH can facilitate the separation of charge carriers, further improving the photocatalytic performance.

Figure 2 .
Figure 2. (a,b) SEM and (c,d) TEM images of ACO/BOCH-100.The optical absorption behaviors of BiOCOOH, Ag 2 CO 3 , and Ag 2 CO 3 /BiOCOOH heterojunctions (ACO/BOCH-30, ACO/BOCH-50, ACO/BOCH-100, and ACO/BOCH-150) were studied by UV-vis diffuse reflectance spectrum (UV-vis DRS).As shown in Figure 4a, Ag 2 CO 3 displayed intense absorbance in the VL region, whereas BiOCOOH had absorbance in the ultraviolet (UV) light region.The absorption band edges of pristine Ag 2 CO 3 and BiOCOOH were about 470 and 365 nm, respectively, in agreement with previously reported results.The light absorption near the band edge followed the

Figure 5 .
Figure 5. (a) Photocatalytic degradation of RhB dye with various catalysts under simulated sunlight.(b) Absorption spectra of RhB with irradiation time in the presence of ACO/BOCH-100.

Figure 6 .
Figure 6.Photocatalytic degradation of TC with different catalysts under simulated sunlight.

Figure 5 .
Figure 5. (a) Photocatalytic degradation of RhB dye with various catalysts under simulated sunlight.(b) Absorption spectra of RhB with irradiation time in the presence of ACO/BOCH-100.

Figure 5 .
Figure 5. (a) Photocatalytic degradation of RhB dye with various catalysts under simulated sunlight.(b) Absorption spectra of RhB with irradiation time in the presence of ACO/BOCH-100.

Figure 6 .
Figure 6.Photocatalytic degradation of TC with different catalysts under simulated sunlight.

Figure 6 .
Figure 6.Photocatalytic degradation of TC with different catalysts under simulated sunlight.