key: cord-0028360-ohd556sr
authors: Din, Syed Taj Ud; Lee, Hankyu; Yang, Woochul
title: Z-Scheme Heterojunction of 3-Dimensional Hierarchical Bi(3)O(4)Cl/Bi(5)O(7)I for a Significant Enhancement in the Photocatalytic Degradation of Organic Pollutants (RhB and BPA)
date: 2022-02-24
journal: Nanomaterials (Basel)
DOI: 10.3390/nano12050767
sha: 299cc480d53674af1a85020bc49b1105af7a84aa
doc_id: 28360
cord_uid: ohd556sr

In this study, we report the synthesis of a 3-dimensional (3D) hierarchical Bi(3)O(4)Cl/Bi(5)O(7)I (BOC/BOI) heterostructure for the photocatalytic degradation of Rhodamine-B (RhB) dye and colorless Bisphenol-A (BPA) pollutant under visible light. The heterostructure was prepared using in situ solvothermal and calcination methods. BOC/BOI exhibits a 3D hierarchical structure constructed with thin nano-platelets. The photocatalytic performance of the BOC/BOI photocatalyst demonstrated that the degradation efficiencies of RhB and BPA were 97% and 92% after light illumination within 90 and 30 min, respectively. In comparison, bare BOC and BOI efficiencies were only 20% and 10% for RhB dye, respectively, and 2.3% and 37% for BPA aqueous pollutants, respectively. Moreover, radical trapping measurements indicated that (•)O(2)(−) and (•)OH radicals played prominent roles in RhB and BPA degradation into mineralization. Analysis of band structures and photochemical redox reactions of BOC/BOI revealed a Z-scheme charge transfer between BOC and BOI by an internal electric field formed at the interface. Therefore, the highly improved photocatalytic performance of the BOC/BOI heterostructure is attributed to the synergetic effects of large surface area, high visible-light absorption, and the enhanced separation and transport of photo-excited electron–hole pairs induced by the hierarchical and Z-scheme heterojunction of the BOC/BOI.

As water pollutants have become an increasingly severe threat to life in this industrialized society, removing hazardous pollutants is currently a major social challenge. The pollutants mostly included in water are hazardous organic dyes and phenolic compounds. Rhodamine-B (RhB) is a common water-soluble organic dye used widely in various industry fields. Since it is classified as carcinogenic and neurotoxic, it poses health risks to humans [1] . Thus, its maximum allowable concentration is in the range from 14 to 140 µg/L in water [2] . Other than dyes, the colorless Bisphenol-A is the other frequently used compound. It is also a widely used raw material for the fabrication of numerous polymeric materials [3] . Its no-effect concentration is required to be less than 0.06 µg/L because its long-term exposure causes endocrine-based, neurological, and reproductive developmental disorders [4] . Therefore, the removal of RhB and BPA from the wastewater is crucial before discharging into water reservoirs and landfills. In general, adsorption through microbial treatment and chemical redox reaction has been used to remove these pollutants. However, these approaches have some limitations, due to low efficiency, high cost, and incomplete removal of contaminants [5] . Therefore, the effective elimination of these hazardous organic pollutants from wastewater remains a challenge. 2 of 20 To solve these issues, photocatalysis has attracted substantial attention due to environmental friendliness and its use of freely available solar light [6] [7] [8] . The photocatalytic process of a semiconductor consists of the absorption of photons, the separation and transport of photo-excited charge carriers, and the redox reaction on the surface. Although various semiconducting photocatalysts with high photocatalytic performance have been reported, there are still some limitations, such as high electron-hole recombination, inappropriate redox potentials, and low capability of visible-light absorption [9] . In particular, to enhance the separation and transport of photo-excited charge carriers, which is a key process during the photocatalytic process, various strategies have been explored including nonmetal doping [10] , the deposition of noble or non-noble metal as a cocatalyst on the semiconducting photocatalyst [11] [12] [13] [14] , type-II heterojunction [15] , and Z-scheme heterojunction photocatalyst [16] through the coupling of two semiconducting materials.

The Z-scheme heterojunction photocatalyst has attracted extensive attention due to the direct transfer and spatial separation of photogenerated charge carriers between two photocatalysts, and maintaining its high redox ability of both surfaces [17] . Various nanocomposites or heterojunctions, such as MoS 2 /Bi 2 WO 6 , g-C 3 N 4 /WO 3 , CdS/Bi 3 O 4 Cl, etc. [13] [14] [15] , have been used to synthesize Z-scheme photocatalysts for the degradation of aqueous organic pollutants. Recently, bismuth oxyhalides (BiOX (X = Cl, Br, I))-based nanocomposites are considered to be promising candidates for use as Z-scheme heterojunction photocatalysts. The layered crystal structure of BiOX composed of the [X]-[BiO]- [X] gives it unique electronic and structural properties, such as bandgap tunability [18] , easy adjustment of conduction, and valence band potentials via the different compositions [19] , formation of internal electric field between interlayers [20] , and possible growth in multiple dimensions [21] . In particular, Bi 3 O 4 Cl (BOC) and Bi 5 O 7 I (BOI) are photochemically stable and have suitable bandgaps of 2.60 eV and 3.01 eV for visible-light absorption, respectively [22, 23] . Furthermore, the more negative conduction band (CB) potential of BOI and the more positive valence band (VB) potential of BOC are ideal for the maximum generation of super-oxide ( • O 2 − ) and hydroxyl ( • OH) radicals, respectively, which are beneficial for the degradation of organic pollutants [24] .

Therefore, various Z-scheme heterostructures of the other group semiconductors combined with BOC or BOI have been developed for photocatalytic applications. For instance, Zhou et al. prepared a series of BOI/MIL-53(Fe) nanocomposites [6] . The wellmatched energy levels of BOI with MIL-53(Fe) enabled the construction of a direct Z-scheme heterojunction for the degradation of RhB under visible-light irradiation. Similarly, Jiang et al. used a facial pH control route to develop a BOC/Bi 12 O 17 Cl 2 Z-scheme composite by the in situ growth of BOC on the surface of Bi 12 O 17 Cl 2 for high photodegradation efficiency under visible light [25] . In another study, Che et al. prepared a Z-scheme BOC/g-C 3 N 4 heterostructure to remove antibiotics, dye, and heavy metal from water under visible light [26] . The high photocatalytic performance is attributed to the Z-scheme heterojunction and the strong interfacial functionalization between the BOC nano-flakes and the g-C 3 N 4 nanosheets interface.

Meanwhile, the morphology of the photocatalyst strongly affects the photocatalytic performance. Therefore, various morphologies, such as zero-dimensional (0D) nanodots [27] , 1D nanorods [28] , 2D nanosheets [29] , and 3D hierarchical [30, 31] nanostructures, have attracted significant attention due to their high surface-to-volume ratio, which increases the amount of photoactive sites [32] . Use of the nanostructures with 3D hierarchical morphologies is a promising approach to develop efficient photocatalysts, as this design inhibits self-aggregation of nanostructures due to high surface energies. However, the photocatalytic performances of 3D hierarchical single semiconductors and conventional heterostructures are far from ready for implementation in the photocatalytic degradation of organic pollutants. Therefore, it is necessary to develop a 3D hierarchical Z-scheme heterostructure to benefit from the synergy of its high surface area, high electron-hole separation, and high redox ability.

In this study, we prepared a Z-scheme BOC/BOI heterojunction photocatalyst with a 3D-hierarchical morphology for enhancement in the photocatalytic degradation of RhB and BPA. The heterojunction was fabricated using an in situ two-step solvothermal-calcination method. Morphological characterizations show that BOC/BOI has a 3D-hierarchical structure constructed with thin nano-flakes. Analysis of energy-band structures of BOC/BOI heterojunction proves that the generation of an internal electric field directed from BOI to BOC facilitates Z-scheme charge transfer between BOC and BOI. Thus, the BOC/BOI demonstrated a higher reaction rate and degradation efficiency than the bare BOC and BOI during RhB and BPA degradation. Furthermore, the degradation pathway was suggested by identifying the mineralization and reaction intermediates using liquid chromatography-mass spectroscopy. The excellent performances of the BOC/BOI heterostructure are attributed to more active sites induced by its unique 3D hierarchical morphology and the enhancement of the separation of photogenerated electrons and holes through the Z-scheme transfer process. This research presents that the Z-scheme BOC/BOI heterojunction with a 3D-hierarchical structure is a suitable photocatalyst for the degradation of environmental pollutants. 

An in situ two-step solvothermal method was used to prepare the BOC/BOI heterojunction, as shown in Figure S1 . In Step (a), Bi(NO 3 ) 3 ·5H 2 O (4.5 mmol) was dissolved in 15 mL of ethylene glycol (EG). The mixture was then sonicated and stirred vigorously for 30 min. In Step (b), the PVP (10 mmol) was dissolved in 10 mL of EG, which was then sonicated and stirred vigorously for 30 min. In Step (c), the PVP solution (prepared in Step (b)) was added dropwise into the Bi(NO 3 ) 3 ·5H 2 O solution (prepared in Step (a)) and stirred for 15 min at 400 rpm. Next, in Step (d), various molar ratios of potassium chloride (KCl) and potassium iodide (KI) were dissolved in 10 mL of EG by stirring for 30 min. In Step (e), the KCl:KI solution was added dropwise into the Bi(NO 3 ) 3 ·5H 2 O solution (prepared in

Step (c)) under continuous stirring. In Step (f), the mixture was then transferred to a 50 mL Teflon-lined autoclave and sealed. Next, the autoclave was heated at 160 • C for 12 h and cooled naturally to room temperature. After that, the raw BOC/BiOI composite powder was isolated from the EG solution using centrifugation at a speed of 8000 rpm for 10 min and washed with distilled (DI) water and ethanol. The washed BOC/BiOI powder was then dried overnight at 60 • C and put into alumina crucibles. The powder was calcinated in a muffle furnace at 450 • C for 1 h with a ramp rate of 5 • C/min. As a result, the targeted BOC/BOI composites were prepared. The samples with various molar ratios of 1:1, 1:2, 1:3.3, and 1:4.6 of KCl and KI were synthesized, and these were respectively denoted as BOC/BOI-1, BOC/BOI-2, BOC/BOI-3, and BOC/BOI-4. In addition, for comparison, bare BOC and BOI samples were prepared with a similar method as the one used for BOC/BOI. For the preparation of bare BOC and BOI, KCl and KI were added relative to the molar ratio of Bi in Bi(NO 3 ) 3 ·5H 2 O solution, such as Bi:Cl with 3:1 and Bi:I with 1:1.

Structural analysis of the prepared samples was conducted using X-ray powder diffractometer (XRD)(Ultima IV, Rigaku Inc., Tokyo, Japan) with Cu-Kα as an X-ray source Nanomaterials 2022, 12, 767 4 of 20 (wavelength of 1.5409 Å) operated at a scan rate of 5 • /min in the diffraction angle (2θ) range from 10 • to 80 • . The crystalline phase was characterized through Micro-Raman spectroscopy measurement (XperRAM100, Nanobase Inc., Seoul, Korea), equipped with a green laser source (wavelength of 532 nm and power of 6 mW). The morphology and elemental compositions were examined using a field emission scanning electron microscope (SEM) (JSM-6700F, JEOL Ltd., Tokyo, Japan) equipped with an Energy-dispersive X-ray spectroscope (EDX). A UV-visible spectrophotometer (V-750, Jasco Inc., Tokyo, Japan) equipped with a 60 mm integrating sphere was used to investigate the optical properties, including the diffuse reflectance spectrum and optical bandgap. X-ray photoemission spectroscopy (XPS) (Veresprobe II, ULVAC-PHI Inc., Kanagawa, Japan) with a Monochromatic Al Kα X-ray source was used to examine the chemical composition of samples. The collected XPS data were calibrated with a non-oxygenated carbon peak that originated at 284.8 eV [30, 31] . The photoluminescence (PL) spectra of the samples were obtained using fluorescence spectrophotometer (Fp-8600, Jasco Inc., Tokyo, Japan) with an excitation wavelength of 330 nm. The time-resolved photoluminescence (TRPL) decay spectra were obtained using Spectrofluorometer (FS5-TCSPC, Edinburgh Instruments Ltd., Edinburgh, UK) using 375 nm picosecond pulsed laser diode (EPL-375) as an excitation source. The TG/DTA analyzer (STA 6000, Perkin Elmer, Waltham, MA, USA) was used to collect the thermo-gravimetric analysis (TGA) and differential scanning calorimetric (DSC) data of the synthesized samples ( Figure S2 ). The microstructures of the samples were analyzed using high-resolution transmission electron microscopy (HRTEM: Talos F200X TEM, FEI Co., Hillsboro, OR, USA) operated at an accelerating voltage of 200 kV. The Gatan microscopy software (digital micrograph™, version 3.7.4, GATAN Inc., Pleasanton, CA, USA) was used to obtain fast Fourier transform (FFT), inverse fast Fourier transform (IFFT), and TEM line profile from the HRTEM images.

The photocatalytic characteristics of the samples were determined using a visible light source with a 300 W Xenon lamp (1000 W/m 2 ) (CEL-HXF300, CEAULIGHT Co., Beijing, China) equipped with a UV-IR cutoff filter (420 nm > λ > 780 nm). RhB dye and BPA colorless pollutants were used to evaluate the degradation efficiency of the synthesized photocatalysts. The pollutant aqueous solution in a double wall jacket beaker (80 cm 2 surface area) connected with a water chiller was kept perpendicular to the light source at a distance of 30 cm. Each photocatalyst with 10 mg and 40 mg was used to degrade 40 mL of RhB dye (17 ppm) and BPA colorless pollutant (15 ppm), respectively. Initially, the RhB and BPA solution was stirred for 60 min and 30 min, respectively, under the dark condition to attain adsorption-desorption equilibrium of the photocatalysts. Next, after a specific time interval, a 2 mL solution was taken from each solution, which was then centrifuged for 3 min at 3000 rpm to separate the solution from the photocatalyst. The absorbance spectrum of the separated solution was determined using a UV-visible spectrophotometer, which established the rate of degradation to light irradiation time.

Radical trapping experiments were conducted to determine the radical's dominant species involved in the photocatalytic decomposition of RhB. IPA, BQ, and KI of 2 mmol were used as trapping reagents to determine the active species such as • O 2 − , • OH radicals and holes, respectively. NBT (0.025 mmol) was used as an indicator to determine the amount of • O 2 − radical. We also employed a liquid chromatography-mass spectrometry (LC-MS) system (Agilent 6460 Triple Quad LC/MS, Agilent technologies Inc., Santa Clara, CA, USA), installed with a column (ZORBAX SB-C18 18 µL, 2.1 × 50 mm 2 ) for the degradation pathway and reaction intermediates investigation.

The electrochemical impedance spectroscopy (EIS) analysis was conducted on a threeelectrode workstation (VSP Potentiostat, Biologic, Seyssinet-Pariset, France). The Pt-spiral wire and standard calomel were used as counter and reference electrodes, respectively. An aqueous solution of 0.5 M Na 2 SO 4 (50 mL) was used as an electrolyte. A clean fluorinedoped tin oxide (FTO) glass was employed as a substrate of the working electrode. The working electrode was prepared from the slurry, which was made by dispersing the photocatalyst (0.1 mg) in DMF (1 mL), then sonicated for an hour. The slurry was coated over the FTO by a drop-casting technique and dried at 160 • C for 1 h before being used as a working electrode.

The structural phases of the BOC, BOI, and BOC/BOI-3 were analyzed using XRD patterns, as shown in Figure 1a . The XRD pattern of the prepared BOC was well matched with the monoclinic characteristic of BOC (PDF#36-0760) [33] . Similarly, the XRD pattern of the prepared BOI was the same as the orthorhombic phase of BOI (PDF#040-0548) [34] . The characteristic peaks of BOC and BOI were found to co-exist in the XRD patterns of BOC/BOI-3 samples. Furthermore, the XRD pattern of BOI exhibited an intense and robust peak at 28.08 • , which confirmed the preferential growth of BOI in the (312) plan. In addition, the XRD pattern of BOC exhibited a broad peak at 29.64 • , which confirmed the growth of BOC in the (411) plan. These results provide evidence that the targeted phase of the composite was synthesized successfully. The structural characteristics of the BOC, BOI, and BOC/BOI-3 were further analyzed using Raman measurements, as shown in Figure 1b . For BOC, a peak at 146.8 cm −1 corresponds to A 1g vibration originating from the stretching mode of the Bi-Cl bond [35] , while the remaining peaks between 161.8 cm −1 to 627.3 cm −1 correspond to the Bi-O bond vibration [36] . For BOI, the peak at 146.8 cm −1 indicates E 1g vibration due to the internal stretching mode of Bi-I [37] . The higher-frequency peaks observed between 184.2 cm −1 and 591.8 cm −1 are related to Bi-O bonding, which are generated due to the oxygen-rich environment in BOI [38, 39] . Furthermore, the presence of BOC and BOI characteristic peaks in the Raman spectra of BOC/BOI-3 verified the successful formation of a BOC/BOI heterostructure. In addition, although the positions of all observed peaks in the heterostructure are similar to the BOC and BOI samples, the peak at 506.1 cm −1 in the BOC/BOI-3 composite is blue-shifted and red-shifted compared to BOI and BOC, respectively. These shifts indicate that BOI and BOC in the BOC/BOI-3 composites are strongly interconnected due to the interfacial interaction between oxygen and bismuth atoms.

To investigate the morphology and microstructure of the synthesized samples, FESEM and TEM measurements were performed. The microstructure of the BOC/BOI heterojunction was investigated using HRTEM. Figure 3a reveals that BOC/BOI-3 composite has a 2D nano-platelets morphology with sizes varying from 50 nm to 300 nm. The HRTEM image of the yellow rectangle region marked in Figure 3a shows that 2D nano-platelets of BOC are grown on the surface of BOI (Figure 3b ). A small portion (enclosed in a red rectangle in Figure 3b ) is taken to obtain the IFFT pattern, as shown in Figure 3c . The intensity line profiles of the planes observed from IFFT patterns are shown in Figure S3a ,b, respectively. The fringe spacings of the perpendicular planes of BOC and BOI are determined to be 0.410 nm and 0.507 nm, respectively. According to the XRD reference file (PDF#36-0760), these measured fringe spacings correspond to the (011) and (400) planes of BOC in Figure 3c , respectively. Similarly, a small portion (enclosed in a white rectangle in Figure 3b ) is taken to determine the IFFT pattern for bare BOI, as shown in Figure 3d . The intensity line profiles of these oriented planes are defined with a fringe spacing of 0.315 nm ( Figure S3c ), which corresponds to the (312) plan of BOI according to the XRD reference file (PDF#040-0548). Altogether, the TEM analysis confirms the successful coupling of BOC with BOI, as illustrated in Figure 3e . The elemental composition of BOC/BOI-3 is confirmed by EDS mapping of the region in Figure  S4a , as shown in Figure S4 . The sum EDS image shows the uniform distribution of the corresponding elements ( Figure S4b ). The elemental mapping of individual Bi, O, Cl, and I clearly show that each element is uniformly distributed ( Figure S4c-f ). In addition, the EDS spectrum indicates that the Bi, O, Cl, and I contents are about 44.66%, 44.25%, 4.34%, and 5.03%, respectively, as listed in the inset table of Figure S4g . Moreover, the elemental compositions of BOC, BOI and BOC/BOI-3 were further investigated using XPS. The survey XPS spectrum of the BOC/BOI-3 composite shows the presence of O 1s, I 3d, Cl 2p, and Bi 4f peaks, thus confirming the existence of BOI and BOC in the composite ( Figure S5 ). Meanwhile, the C1s peak observed at 284.800 eV originates from the carbon tape used as a substrate for XPS measurements [40, 41] . The Bi 4f XPS spectra of all samples exhibit the typical peaks of Bi 4f 5/2 and Bi 4f 7/2 , which are attributed to the Bi-O bonding (Figure 4a ). Both peaks of BOC/BOI shift to lower binding energies (0.300 eV and 0.425 eV) than BOC and higher binding energies (0.325 eV and 0.200 eV) than BOI. The O 1 s spectra of each sample were deconvoluted into two peaks, as shown in Figure 4b . The main peak at the lower binding energy and the satellite peak at the higher binding energy originate from Bi-O and adsorbed oxygen, respectively [42] . In particular, the position of the main peak in BOC/BOI is lower than that in BOC and higher than that in BOI [43] , which is similar to the tendency of the Bi 4f spectra. We also compared the I 3d spectrum of BOI and the Cl 2p spectrum of BOC with the BOC/BOI composite, as depicted in Figure 4c ,d. Figure 4c shows the I 3d spectra of the BOI and BOC/BOI-3 samples [44] . It can be seen that a more oxygenated environment was generated in the form of composite. Therefore, the position of both the I 3d 1/2 and I 3d 5/2 peaks in the composite were shifted by 0.075 eV toward a higher binding energy than BOI. The blue shift may result from a more oxygenated environment in the composite. In the Cl 2p spectrum in Figure 4d , the deconvoluted Cl 2p 1/2 and Cl 2p 3/2 peaks of the Cl 2p peak in the composite were also shifted by 0.300 eV and 1.000 eV toward a lower binding energy than BOC, respectively. In XPS analysis, it is observed that all peak positions of BOC/BOI composite were shifted toward higher and lower binding energies than BOI and BOC, respectively. Since Iodine (I) is less electronegative than chlorine (Cl), it is easy for I to leave electrons. Theoretically, when I donate electrons, the concentration of the outer shell's electron decreases, resulting in a reduced shielding effect and corresponding to an increase in the binding energy of the inner electrons. As a result, the corresponding XPS peaks shift toward a high binding energy. Therefore, this high energy shift indicates the electron density migration from BOI to BOC in the BOC/BOI-3 heterojunction. The vice versa effect is responsible for the shift of the BOC peaks to lower binding energies.

The photocatalytic performances of the BOC, BOI and BOC/BOI samples were evaluated by degrading RhB dye and BPA colorless pollutant in an aqueous solution under visible-light irradiation, as shown in Figure 5 . Figure 5a shows that the degradation ratio (C/C o ) of RhB dye solution over BOC/BOI composites is substantially higher than that of pure BOC and BOI. Specifically, the BOC/BOI-3 and BOC/BOI-2 composites completely decomposed RhB dye solution within 160 and 220 min, respectively. The temporal absorp-Nanomaterials 2022, 12, 767 9 of 20 tion spectra of RhB dye solution with BOC/BOI-3 show a gradual decrease in absorbance intensity with irradiation time ( Figure S6 ). Eventually, the absorbance peak completely disappears after 160 min, indicating complete decolorization of RhB dye. Furthermore, during photocatalytic degradation, the position of the peak shifts from 554.5 nm to 498.5 nm, which is caused by the deethylation of the RhB dye [45] . Furthermore, the degradation rate of the RhB solution in the presence of each sample can be calculated using the pseudo-first-order kinetic model, as expressed in Equation (1),

where k, C 0 , and C represent the reaction rate constant, initial concentration, and the remaining concentration of RhB in the solution at light-exposed time t, respectively. We obtained the k of each sample via curve fitting with Equation (1) ( Figure S7 ). The obtained reaction rate and degradation efficiency for each sample are shown in Figure 5b . BOC/BOI-3 had the highest degradation rate of 0.040 min −1 as well as the highest degradation efficiency of 97.68% after 90 min of light irradiation. In addition, the photocatalytic performances of BOC, BOI and BOC/BOI-3 were evaluated by decomposing the BPA in an aqueous solution under visible light (Figures 5c,d and S8 ). The degradation efficiency of BOC/BOI-3 over BPA was~92.89% within 30 min, which was much higher than those of the BOC and BOI samples. The degradation rate of BOC/BOI-3 was 0.094 min −1 , which was 120 and 6 times higher than those of bare BOC and BOI, respectively. Moreover, we compared the degradation performance of our synthesized sample with previously reported bismuth oxyhalide-based heterostructures and other bismuth-based heterostructures, as shown in Tables S2 and S3 . Importantly, our grown BOC/BOI-3 sample exhibits a high degradation rate and efficiency for both RhB and BPA under visible-light illumination, compared to the reported literature. Next, radical trapping analysis was conducted to explore the active radicals generated in the BOC/BOI-3 sample during RhB degradation, as shown in Figure 6 . BQ, IPA, and KI were used as trapping agents for • O 2 − , • OH, and h + , respectively. Figure 6a depicts the degree of suppression of RhB degradation in the presence of BQ, IPA, and KI scavengers. The degradation of RhB in the presence of IPA is higher than those of BQ and KI. The corresponding degradation efficiency of RhB was reduced from 97% (no scavenger) to 54%, 46%, and 40% with IPA, BQ, and KI, respectively ( Figure S9a) . Next, Figure S9b shows that the degradation of RhB followed the first-order reaction kinetic model, wherein the degradation rate was reduced from 0.0400 min −1 (no scavenger) to 0.008, 0.007, and 0.005 min −1 with IPA, BQ, and KI, respectively. Thus, the results indicate that • OH, • O 2 − radical, and h + can be generated during RhB degradation [46] . To confirm the direct formation of each radical during RhB degradation, we employed NBT as a probe molecule for the detection of the • O 2 − radical. To directly investigate the • O 2 − radical, the temporal absorption spectra of NBT with UV light were obtained in the presence of the BOC, BOI, and BOC/BOI-3 samples, as shown in Figure S10 . Please note that the decrease in UV absorbance at the main peak at 259 nm indicates the generation of • O 2 − radicals during the transformation from NBT to Formazan [47] . Compared to BOC and BOI, BOC/BOI-3 has the lowest absorbance at 259 nm after 150 min, corresponding to the highest generation of • O 2 − radicals ( Figure S10a-c) . Based on the reaction relationship between • O 2 − and NBT (4:1 in molar ratio) ( Figure S10d ), the amount of • O 2 − radicals can be calculated to be 37.6, 46.12, and 73.84 µmol/L after 150 min for BOC, BOI, and BOC/BOI-3, respectively (Figure 6b ).

Finally, we performed LC-MS to elucidate the reaction intermediates, photocatalytic degradation pathway, and mineralization process of RhB and BPA over BOC/BOI-3 sample, as shown in Figure S11 . It can be seen that the degradation products were measured at rials 2022, 12, x FOR PEER REVIEW 11 of 21 reaction proceeds, the RhB molecules gradually divide into small molecules from m/ɀ =443 to m/ɀ =130 via N-deethylation and degradation of RhB chromophore structure. In the process of N-deethylation, the OH radicals will attack the central carbon of the RhB molecule with a high negative density charge, resulting in the degradation of RhB (m/ɀ = 443) molecules into N-deethylated intermediates first (m/ɀ = 391). Then, these N-deethylated intermediates (m/ɀ = 391) are transformed into intermediates with the m/ɀ value of 354 and 340 by OH or O2 radical attack on the bonding between benzene and chromophore, and further degraded into smaller m/ɀ intermediates with the m/ɀ value of 254, 251 and then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleavage of the chromophore. In Figure 7b , the systematic degradation pathway for BPA shows that the BPA molecules gradually convert into small molecules via two degradation routes. Rout (1) presents the BPA conversion into 4-n-octylphenol-mono-ethoxylate (m/ɀ: 249) by attacking active radicals on the isopropyl/aliphatic chain between the two benzene rings. In rout (2) Figure S11a . The possible degradation pathway and some relative degradation products can be proposed according to mass fragmentation results, as shown in Figure 7a . This result shows that as the photocatalytic reaction proceeds, the RhB molecules gradually divide into small molecules from Nanomaterials 2022, 12, x FOR PEER REVIEW reaction proceeds, the RhB molecules gradually d to m/ɀ =130 via N-deethylation and degradation process of N-deethylation, the OH radicals will a ecule with a high negative density charge, resulti molecules into N-deethylated intermediates first intermediates (m/ɀ = 391) are transformed into i and 340 by OH or O2 radical attack on the bondi and further degraded into smaller m/ɀ intermed then to m/ɀ 194 and finally convert to m/ɀ = 130 Figure 7b , the systematic degradation pathway gradually convert into small molecules via two d BPA conversion into 4-n-octylphenol-mono-etho icals on the isopropyl/aliphatic chain between t converts into (m/ɀ: 208), which may be allocated ates; (i) 1,1-di(p-toly)ethylene, (ii) 3,3-diphenylac nylpropene, and then converted into 4-isopropy

Nanomaterials 2022, 12, x FOR PEER REVIEW reaction proceeds, the RhB molecules to m/ɀ =130 via N-deethylation and process of N-deethylation, the OH ra ecule with a high negative density ch molecules into N-deethylated interm intermediates (m/ɀ = 391) are transfo and 340 by OH or O2 radical attack o and further degraded into smaller m then to m/ɀ 194 and finally convert t Figure 7b , the systematic degradatio gradually convert into small molecu BPA conversion into 4-n-octylphenol icals on the isopropyl/aliphatic chai converts into (m/ɀ: 208), which may b ates; (i) 1,1-di(p-toly)ethylene, (ii) 3,3 nylpropene, and then converted into =130 via N-deethylation and degradation of RhB chromophore structure. In the process of Ndeethylation, the OH radicals will attack the central carbon of the RhB molecule with a high negative density charge, resulting in the degradation of RhB ( Nanomaterials 2022, 12, x FOR PEER REVIEW reaction proceeds, the RhB molecules gradually di to m/ɀ =130 via N-deethylation and degradation process of N-deethylation, the OH radicals will at ecule with a high negative density charge, resultin molecules into N-deethylated intermediates first intermediates (m/ɀ = 391) are transformed into in and 340 by OH or O2 radical attack on the bondin and further degraded into smaller m/ɀ intermedi then to m/ɀ 194 and finally convert to m/ɀ = 130 o Figure 7b , the systematic degradation pathway f gradually convert into small molecules via two de BPA conversion into 4-n-octylphenol-mono-ethox icals on the isopropyl/aliphatic chain between th = 443) molecules into N-deethylated intermediates first ( Nanomaterials 2022, 12, x FOR PEER REVIEW reaction proceeds, the RhB molecules gradually divide into small molecules fro to m/ɀ =130 via N-deethylation and degradation of RhB chromophore struc process of N-deethylation, the OH radicals will attack the central carbon of th ecule with a high negative density charge, resulting in the degradation of RhB molecules into N-deethylated intermediates first (m/ɀ = 391). Then, these Nintermediates (m/ɀ = 391) are transformed into intermediates with the m/ɀ v and 340 by OH or O2 radical attack on the bonding between benzene and ch and further degraded into smaller m/ɀ intermediates with the m/ɀ value of 2 then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleavage of the chrom Figure 7b , the systematic degradation pathway for BPA shows that the BPA gradually convert into small molecules via two degradation routes. Rout (1) p BPA conversion into 4-n-octylphenol-mono-ethoxylate (m/ɀ: 249) by attacking = 391). Then, these N-deethylated intermediates ( erials 2022, 12, x FOR PEER REVIEW 11 of 21 reaction proceeds, the RhB molecules gradually divide into small molecules from m/ɀ =443 to m/ɀ =130 via N-deethylation and degradation of RhB chromophore structure. In the process of N-deethylation, the OH radicals will attack the central carbon of the RhB molecule with a high negative density charge, resulting in the degradation of RhB (m/ɀ = 443) molecules into N-deethylated intermediates first (m/ɀ = 391). Then, these N-deethylated intermediates (m/ɀ = 391) are transformed into intermediates with the m/ɀ value of 354 and 340 by OH or O2 radical attack on the bonding between benzene and chromophore, and further degraded into smaller m/ɀ intermediates with the m/ɀ value of 254, 251 and then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleavage of the chromophore. In Figure 7b , the systematic degradation pathway for BPA shows that the BPA molecules gradually convert into small molecules via two degradation routes. Rout (1) presents the = 391) are transformed into intermediates with the Nanomaterials 2022, 12, x FOR PEER REVIEW reaction proceeds, the RhB molecules gradually divide to m/ɀ =130 via N-deethylation and degradation of R process of N-deethylation, the OH radicals will attack ecule with a high negative density charge, resulting in molecules into N-deethylated intermediates first (m/ intermediates (m/ɀ = 391) are transformed into interm and 340 by OH or O2 radical attack on the bonding b and further degraded into smaller m/ɀ intermediates then to m/ɀ 194 and finally convert to m/ɀ = 130 on t Figure 7b , the systematic degradation pathway for B gradually convert into small molecules via two degra value of 354 and 340 by OH or O 2 radical attack on the bonding between benzene and chromophore, and further degraded into smaller reaction proceeds, the RhB molecules gradually divide into small molecules from m/ɀ =443 to m/ɀ =130 via N-deethylation and degradation of RhB chromophore structure. In the process of N-deethylation, the OH radicals will attack the central carbon of the RhB molecule with a high negative density charge, resulting in the degradation of RhB (m/ɀ = 443) molecules into N-deethylated intermediates first (m/ɀ = 391). Then, these N-deethylated intermediates (m/ɀ = 391) are transformed into intermediates with the m/ɀ value of 354 and 340 by OH or O2 radical attack on the bonding between benzene and chromophore, and further degraded into smaller m/ɀ intermediates with the m/ɀ value of 254, 251 and then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleavage of the chromophore. In Figure 7b , the systematic degradation pathway for BPA shows that the BPA molecules gradually convert into small molecules via two degradation routes. Rout (1) presents the BPA conversion into 4-n-octylphenol-mono-ethoxylate (m/ɀ: 249) by attacking active radicals on the isopropyl/aliphatic chain between the two benzene rings. In rout (2), BPA converts into (m/ɀ: 208), which may be allocated to the formation of 3 possible intermediates; (i) 1,1-di(p-toly)ethylene, (ii) 3,3-diphenylacrylaldehyde and (iii) 2-methyl-1,1diphenylpropene, and then converted into 4-isopropyle-3-methylphenol (m/ɀ: 150) by the disconnection of two aromatic rings owing to redox reaction. Thereafter, the benzene ring opens with the oxidization resulting in the breaking of C-C bonds, leading to the formation of succinic acid (m/ɀ: 118). Finally, it converts into smaller molecules, CO2 and H2O. intermediates with the Nanomaterials 2022, 12, x FOR PEER REVIEW reaction proceeds, the RhB molecules gradually divide into sm to m/ɀ =130 via N-deethylation and degradation of RhB chro process of N-deethylation, the OH radicals will attack the cen ecule with a high negative density charge, resulting in the deg molecules into N-deethylated intermediates first (m/ɀ = 391). intermediates (m/ɀ = 391) are transformed into intermediates and 340 by OH or O2 radical attack on the bonding between and further degraded into smaller m/ɀ intermediates with th then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleav Figure 7b , the systematic degradation pathway for BPA sho gradually convert into small molecules via two degradation r BPA conversion into 4-n-octylphenol-mono-ethoxylate (m/ɀ: 2 icals on the isopropyl/aliphatic chain between the two benz converts into (m/ɀ: 208), which may be allocated to the format ates; (i) 1,1-di(p-toly)ethylene, (ii) 3,3-diphenylacrylaldehyde nylpropene, and then converted into 4-isopropyle-3-methylp connection of two aromatic rings owing to redox reaction. T opens with the oxidization resulting in the breaking of C-C mation of succinic acid (m/ɀ: 118). Finally, it converts into s H2O. 

Nanomaterials 2022, 12, x FOR PEER REVIEW 11 o reaction proceeds, the RhB molecules gradually divide into small molecules from m/ɀ = to m/ɀ =130 via N-deethylation and degradation of RhB chromophore structure. In process of N-deethylation, the OH radicals will attack the central carbon of the RhB m ecule with a high negative density charge, resulting in the degradation of RhB (m/ɀ = 4 molecules into N-deethylated intermediates first (m/ɀ = 391). Then, these N-deethyla intermediates (m/ɀ = 391) are transformed into intermediates with the m/ɀ value of and 340 by OH or O2 radical attack on the bonding between benzene and chromopho and further degraded into smaller m/ɀ intermediates with the m/ɀ value of 254, 251 a then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleavage of the chromophore Figure 7b , the systematic degradation pathway for BPA shows that the BPA molecu gradually convert into small molecules via two degradation routes. Rout (1) presents BPA conversion into 4-n-octylphenol-mono-ethoxylate (m/ɀ: 249) by attacking active r icals on the isopropyl/aliphatic chain between the two benzene rings. In rout (2) = 130 on the cleavage of the chromophore. In Figure 7b , the systematic degradation pathway for BPA shows that the BPA molecules gradually convert into small molecules via two degradation routes. Rout (1) presents the BPA conversion into 4-n-octylphenol-mono-ethoxylate ( Nanomaterials 2022, 12, x FOR PEER REVIEW reaction proceeds, the RhB molecules gradually divide into sm to m/ɀ =130 via N-deethylation and degradation of RhB chr process of N-deethylation, the OH radicals will attack the cen ecule with a high negative density charge, resulting in the deg molecules into N-deethylated intermediates first (m/ɀ = 391) intermediates (m/ɀ = 391) are transformed into intermediate and 340 by OH or O2 radical attack on the bonding between and further degraded into smaller m/ɀ intermediates with th then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleav Figure 7b , the systematic degradation pathway for BPA sho gradually convert into small molecules via two degradation r BPA conversion into 4-n-octylphenol-mono-ethoxylate (m/ɀ: icals on the isopropyl/aliphatic chain between the two benz converts into (m/ɀ: 208), which may be allocated to the forma ates; (i) 1,1-di(p-toly)ethylene, (ii) 3,3-diphenylacrylaldehyde nylpropene, and then converted into 4-isopropyle-3-methylp connection of two aromatic rings owing to redox reaction. T opens with the oxidization resulting in the breaking of C-C mation of succinic acid (m/ɀ: 118). Finally, it converts into s H2O. : 249) by attacking active radicals on the isopropyl/aliphatic chain between the two benzene rings. In rout (2), BPA converts into ( nomaterials 2022, 12, x FOR PEER REVIEW 11 of 21 reaction proceeds, the RhB molecules gradually divide into small molecules from m/ɀ =443 to m/ɀ =130 via N-deethylation and degradation of RhB chromophore structure. In the process of N-deethylation, the OH radicals will attack the central carbon of the RhB molecule with a high negative density charge, resulting in the degradation of RhB (m/ɀ = 443) molecules into N-deethylated intermediates first (m/ɀ = 391). Then, these N-deethylated intermediates (m/ɀ = 391) are transformed into intermediates with the m/ɀ value of 354 and 340 by OH or O2 radical attack on the bonding between benzene and chromophore, and further degraded into smaller m/ɀ intermediates with the m/ɀ value of 254, 251 and then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleavage of the chromophore. In Figure 7b , the systematic degradation pathway for BPA shows that the BPA molecules gradually convert into small molecules via two degradation routes. Rout (1) presents the BPA conversion into 4-n-octylphenol-mono-ethoxylate (m/ɀ: 249) by attacking active radicals on the isopropyl/aliphatic chain between the two benzene rings. In rout (2), BPA converts into (m/ɀ: 208), which may be allocated to the formation of 3 possible intermediates; (i) 1,1-di(p-toly)ethylene, (ii) 3,3-diphenylacrylaldehyde and (iii) 2-methyl-1,1diphenylpropene, and then converted into 4-isopropyle-3-methylphenol (m/ɀ: 150) by the disconnection of two aromatic rings owing to redox reaction. Thereafter, the benzene ring opens with the oxidization resulting in the breaking of C-C bonds, leading to the formation of succinic acid (m/ɀ: 118). Finally, it converts into smaller molecules, CO2 and H2O. : 208), which may be allocated to the formation of 3 possible intermediates; (i) 1,1di(p-toly)ethylene, (ii) 3,3-diphenylacrylaldehyde and (iii) 2-methyl-1,1diphenylpropene, and then converted into 4-isopropyle-3-methylphenol ( Nanomaterials 2022, 12, x FOR PEER REVIEW reaction proceeds, the RhB molecules gradually divide int to m/ɀ =130 via N-deethylation and degradation of RhB process of N-deethylation, the OH radicals will attack the ecule with a high negative density charge, resulting in the molecules into N-deethylated intermediates first (m/ɀ = intermediates (m/ɀ = 391) are transformed into intermed and 340 by OH or O2 radical attack on the bonding betw and further degraded into smaller m/ɀ intermediates wit then to m/ɀ 194 and finally convert to m/ɀ = 130 on the c Figure 7b , the systematic degradation pathway for BPA gradually convert into small molecules via two degradat BPA conversion into 4-n-octylphenol-mono-ethoxylate (m icals on the isopropyl/aliphatic chain between the two converts into (m/ɀ: 208), which may be allocated to the fo ates; (i) 1,1-di(p-toly)ethylene, (ii) 3,3-diphenylacrylaldeh nylpropene, and then converted into 4-isopropyle-3-met connection of two aromatic rings owing to redox reactio opens with the oxidization resulting in the breaking of mation of succinic acid (m/ɀ: 118). Finally, it converts in H2O. : 150) by the disconnection of two aromatic rings owing to redox reaction. Thereafter, the benzene ring opens with the oxidization resulting in the breaking of C-C bonds, leading to the formation of succinic acid ( nomaterials 2022, 12, x FOR PEER REVIEW 11 of 21 reaction proceeds, the RhB molecules gradually divide into small molecules from m/ɀ =443 to m/ɀ =130 via N-deethylation and degradation of RhB chromophore structure. In the process of N-deethylation, the OH radicals will attack the central carbon of the RhB molecule with a high negative density charge, resulting in the degradation of RhB (m/ɀ = 443) molecules into N-deethylated intermediates first (m/ɀ = 391). Then, these N-deethylated intermediates (m/ɀ = 391) are transformed into intermediates with the m/ɀ value of 354 and 340 by OH or O2 radical attack on the bonding between benzene and chromophore, and further degraded into smaller m/ɀ intermediates with the m/ɀ value of 254, 251 and then to m/ɀ 194 and finally convert to m/ɀ = 130 on the cleavage of the chromophore. In Figure 7b , the systematic degradation pathway for BPA shows that the BPA molecules gradually convert into small molecules via two degradation routes. Rout (1) presents the BPA conversion into 4-n-octylphenol-mono-ethoxylate (m/ɀ: 249) by attacking active radicals on the isopropyl/aliphatic chain between the two benzene rings. In rout (2), BPA converts into (m/ɀ: 208), which may be allocated to the formation of 3 possible intermediates; (i) 1,1-di(p-toly)ethylene, (ii) 3,3-diphenylacrylaldehyde and (iii) 2-methyl-1,1diphenylpropene, and then converted into 4-isopropyle-3-methylphenol (m/ɀ: 150) by the disconnection of two aromatic rings owing to redox reaction. Thereafter, the benzene ring opens with the oxidization resulting in the breaking of C-C bonds, leading to the formation of succinic acid (m/ɀ: 118). Finally, it converts into smaller molecules, CO2 and H2O. 

We further conducted the recycling experiments to evaluate the photocatlytic reusability and stability of BOC/BOI-3 heterojunction photocatalyst, as illustrated in Figure 8 . It can be seen that BOC/BOI-3 provides 100% RhB degradation efficiency (Figure 8a ) and 95% BPA degradation efficiency (Figure 8b ) after the first cycle, while a subsequent decrease in catalytic activity is observed after the second and third run. After the 3rd cycle, 85.34% of RhB and 51.64% of BPA were degraded in 160 min and 40 min, respectively. The observed decrease in efficiency is probably caused by the adsorption of organic intermediates on the catalyst surface [48] . Therefore, the structural and morphological stability of BOC/BOI-3 was verified using XRD, Raman, and SEM for the BOC/BOI-3 after the recycling experiment. In Figure 8c and Figure S12 , we observed negligible variation in the XRD pattern and morphology, confirming structural and morphological stability. Additionally, the BOC/BOI-3 sample shows robust Raman intensity in a wide range because of the adsorption of the RhB molecule on the surface of BOC/BOI-3, which also reduced its photocatalytic performance in the 2nd and 3rd cycle during photocatalytic degradation (Figure 8d ). However, no extra peak is observed in the Raman spectra of BOC/BOI-3 after degrading BPA due to the low concentration and less intense Raman active modes of BPA in the 125-1000 cm −1 range [49] . 

PL measurements were conducted to investigate the recombination behavior of photoinduced e − -h + pairs in BOC, BOI, and BOC/BOI-3, as shown in Figure 9a . The BOC/BOI-3 composite exhibited a lower PL emission intensity than BOC and BOI, which indicates the reduced recombination of e − -h + pairs in the BOC/BOI-3 sample. Furthermore, we adapted time-resolved photoluminescence spectroscopy (TRPL) to estimate the lifetime of the excited charge carriers (Figure 9b and Table S1 ). The average lifetimes (τ avg ) of BOC/BOI-3 (8.80 ns) are longer than that of the BOC (7.42 ns) and BOI (7.91 ns). The longer τ avg indicates that the recombination rate of the photogenerated charge carriers is reduced. Thus, the BOC/BOI composite led to more efficient separation of electron-hole pairs. We also measured the transient photocurrent response of the samples to examine the separation efficiency of the photo-excited charge carriers, as shown in Figure 9c . The BOC/BOI-3 has a higher photocurrent response than both the pristine BOC and BOI samples. The strong photocurrent response reveals the enhanced separation and transfer of the photogenerated charge carriers in the BOC/BOI composite. Next, an EIS Nyquist plot was taken to examine the electrode/electrolyte interfacial charge transfer resistance, as shown in Figure 9d . The Nyquist plot can be well-reproduced into solution-spreading resistance (R s ) and charge transfer resistance (R ct ), in parallel with the constant-phase element (CPE) (inset of Figure 9d ) [50] . The R ct values for BOC, BOI, and BOC/BOI-3 are 0.43, 0.64, and 0.32 MΩ, respectively. The smallest R ct of BOC/BOI-3 has a lower charge transfer resistance than BOC and BOI. Therefore, these results suggest that the BOC/BOI-3 heterojunction can effectively suppress the recombination of photo-excited charge carriers, which will effectively improve the photocatalytic performance of the BOC/BOI-3 heterostructure. 

To elucidate the photocatalytic mechanism of the BOC/BOI heterostructure, the electronic structures of BOC, BOI, and BOC/BOI-3 were investigated through measurements of UV-Vis diffuse reflectance spectra (DRS), Mott-Schottky (MS) plots, and valence band (VB) XPS spectra, as shown in Figure 10 . First, the UV-Vis DRS of BOC, BOI, and BOC/BOI-3 were measured to investigate optical absorption ability (Figure 10a ). The absorption edges for the BOC and BOI were located at around 450 nm and 425 nm, respectively. In comparison, the absorption edge of the BOC/BOI-3 was extended to a longer wavelength of 460 nm. The extended absorption edge of BOC/BOI-3 is attributed to the strong contribution of BOC in BOC/BOI-3 to the absorption of visible light. Moreover, the optical bandgap of BOC and BOI could be obtained by curve fitting of Tauc plotting of (αhν) n versus E g (inset of Figure 10a) , where n = 1/2 for the indirect band gap semiconducting behavior of BOC and BOI [51, 52] . The obtained band gaps were 2.67 eV and 3.07 eV for BOC and BOI, respectively. Second, the Fermi energy levels (E f ) of the prepared BOC and BOI samples were obtained using MS analysis, as shown in Figure 10b ,c. The MS plots of BOC and BOI both show the positive slopes, thus indicating their n-type semiconducting behavior [53] . Furthermore, by extrapolating MS plots, the flatband potentials of BOC and BOI were obtained to be −0.645 V and −1.101 V vs. standard calomel electrode (SCE). Please note that the flatband potential (E fb ) of the n-type semiconductor represents the E f level [54] . The E f vs. normal hydrogen electrode (NHE) scale were calculated using Equation (2) [55] ; as a result, the E f of BOC and BOI were found to be −0.401 eV and −0.857 eV vs. NHE, respectively (Figure 11a ).

Furthermore, valence band (VB) XPS measurement was carried out to determine the VB potential for BOC and BOI, as shown in Figure 10d . The VB XPS spectra reveal the VB maxima of 2.44 eV and 2.60 eV for BOC and BOI, respectively. Thus, the VB potentials with respect to E f level are calculated to be 2.039 V and 1.743 V vs. NHE for BOC and BOI, respectively (Figure 11a) .

Furthermore, the CB minima of BOC and BOI were determined using the following Equation (3) . where E CB , E VB , and E g , denote the CB potential, VB potential and band gap of the sample, respectively. As a result, the calculated CB potentials for BOC and BOI are −0.631 V and 1.327 V vs. NHE, respectively (Figure 11a ). Thus, based on the above analysis, the BOC/BOI will make a type-II heterojunction. When BOC and BOI formed the BOC/BOI heterojunction, the electrons would spontaneously migrate from BOI to BOC through the BOC/BOI interface to align the Fermi level because BOI has a higher E f than BOC. The migration behavior of the charge carriers at the interface is also consistent with the elemental analysis in XPS spectra (as discussed in Section 3.1). This electron migration generates a depletion region at the BOC and BOI interface with an internal electric field (IEF) oriented from BOI to BOC, therefore resulting in the band bending upward for BOI and downward for BOC, respectively, as shown in Figure 11b .

Regarding the analysis of the band structure of the BOC/BOI-3 sample, a possible Z-scheme photocatalytic mechanism for BOC/BOI could be proposed (Figure 11c ). Under visible-light irradiation, the charge carriers are excited simultaneously from the VB to the CB in both BOC and BOI to produce photogenerated e − and h + (as shown in the below reactions (4) and (5)). Then, the photo-excited electrons in the CB of BOC will be easily transferred to the VB of BOI due to the IEF at the interface in the heterojunction; this initiates the Z-scheme charge transport of the photo-excited charge carriers in the photocatalytic processes (reaction (6) and in Figure 10c ). As a result, the remaining photogenerated holes in the VB of BOC with strong oxidation ability will split H 2 O into • OH and hydrogen ions (H + ) (reaction (7)) due to the fact that the VB of BOC (2.039 eV) is more positive than +1.99 eV (H 2 O/ • OH vs. NHE). At the same time, the remaining photogenerated electrons in the CB of BOI will reduce the O 2 molecules in aqueous solution into highly active • O 2 − radical (reaction (8)), then the • O 2 − and • OH − radicals further react with RhB or BPA aqueous solution to degrade it into H 2 O, CO 2 , and small molecules (reaction (9) ). Moreover, the unique 3D morphology of BOC/BOI-3 will provide more catalytic centers and increase the active sites. Accordingly, BOC/BOI-3 shows enhanced photocatalytic performance for degrading RhB and BPA pollutants.

BOI + hν → BOI * e − + h + ,

BOC * e − + h + + BOI e − + h + → BOC * h + + BOI * e − ,

In this study, a simple solvothermal growth technique was used to synthesize the 3D hierarchical BOC/BOI heterostructure photocatalyst. The heterostructure demonstrated direct Z-scheme photocatalytic behavior in the photocatalytic degradation of RhB and BPA. The 3D hierarchal morphology of BOC/BOI can increase active sites due to its high surface area, and can improve visible-light absorption via multiple reflections inside the sample. XPS and mechanistic studies proved the generation of an internal electric field from BOI to BOC at their interface, which contributed to Z-scheme transport of photogenerated charge carriers in the BOC/BOI heterojunction. Thus, the BOC/BOI sample demonstrated a higher reaction rate and a higher degradation efficiency than the bare BOC and BOI during RhB and BPA degradation. Radical trapping analysis showed that • O 2 − , and • OH radicals played a crucial role in RhB and BPA degradation. Through LC-MS results of RhB and BPA during photodegradation, its mineralization and degradation pathway were proposed. Therefore, the excellent photocatalytic performances of BOC/BOI are attributed to its large surface area, visible-light absorption, and low electron-hole recombination, which are due to its unique 3D hierarchical morphology and the direct Z-scheme photocatalytic process. Conclusively, direct Z-scheme BOC/BOI heterostructure is a suitable photocatalyst for use in the photodegradation of environmental pollutants.

Supplementary Materials: The following supporting information can be downloaded at: https: //www.mdpi.com/article/10.3390/nano12050767/s1, Figure S1 : Steps involved in the synthesis of heterostructure BOC/BOI composite; Figure S2 : TGA and DSC plot of BiOI photocatalyst; Figure S3 : Intensity line profiles of the inverse FFT of (a,b) BOC and BOI (c) in the BOC/BOI heterostructure; Figure S4 : FESEM image of (a) BOC/BOI-3 composite and (b) its corresponding EDS sum image consists of four different colors: light red, dark red, green, and blue; these denote the presence of (c) Bi, (d) O, (e) Cl, and (f) I in the BOC/BOI-3 heterostructure, respectively (g) EDS spectrum of BOC/BOI-3 composite, with the inset table showing the atomic and elemental weight percentages of BOC/BOI-3 nano composite; Figure S5 : XPS survey spectra for BOC, BOI, and BOC/BOI-based photocatalysts; Figure Table S1 : Obtained parameters from the TRPL curves; Table S2 : Comparison of photocatalytic degradation of RhB with recently reported literature; Table S3 : Comparison of photocatalytic degradation of BPA with recently reported literature. References [15, 16, 26, 37, are cited in the Supplementary Materials. Institutional Review Board Statement: Not applicable.

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Enhancing Visible-Light-Induced Photocatalytic Activity of BiOI Microspheres for NO Removal by Synchronous Coupling with Bi Metal and Graphene

Probing the Facet-Dependent Intermediate in the Visible-Light Degradation of RhB by Carbon-Coated Anatase TiO 2 Nanoparticles

Enhanced Photocatalytic Activity of Fe-Doped Bi 4 O 5 Br 2 Nanosheets Decorated with Au Nanoparticles for Pollutants Removal

Excellent Visible Light Responsive Photocatalytic Behavior of N-Doped TiO 2 toward Decontamination of Organic Pollutants

Thermally Treated Fungal Manganese Oxides for Bisphenol A Degradation Using Sulfate Radicals

Raman Spectroscopy of 'Bisphenol A

Steering Charge Kinetics of Tin Niobate Photocatalysts: Key Roles of Phase Structure and Electronic Structure

Bi 3 O 4 Cl Hybrid Junction with Enhanced Photocatalytic Performance in Removing Methyl Orange, Bisphenol A, Tetracycline and Escherichia Coli

Novel P-n Type Porous Ag 2 O/Bi 5 O 7 I Heterojunction for Uv-Vis-NIR Activated High Efficient Photocatalytic Degradation of Bisphenol A: Photoelectric Properties and Degradation Mechanism

Room-Temperature Controllable Synthesis of Bi 5 O 7 I Nanostrips for Improved Photocatalytic Activity

Constraints to the Flat Band Potential of Hematite Photo-Electrodes

Template-Free Precursor-Surface-Etching Route to Porous, Thin g-C 3 N 4 Nanosheets for Enhancing Photocatalytic Reduction and Oxidation Activity

Bi 12 O 17 Cl 2 /(BiO) 2 CO 3 Nanocomposite Materials for Pollutant Adsorption and Degradation: Modulation of the Functional Properties by Composition Tailoring

0D to 3D Controllable Nanostructures of BiOBr via a Facile and Fast Room-Temperature Strategy

Novel Bi 3 O 5 I 2 Hollow Microsphere and Its Enhanced Photocatalytic Activity. Catalysts

Preparation of Bismuth Oxyiodides and Oxides and Their Photooxidation Characteristic under Visible/UV Light Irradiation

Controlled Synthesis of Bismuth Oxyiodide toward Optimization of Photocatalytic Performance

Fabrication of BiOIO 3 with Induced Oxygen Vacancies for Efficient Separation of the Electron-Hole Pairs

Synthesis and Characterization of BiOI Microspheres under Standardized Conditions

Understanding the Composition and Electronic Structure Dependent Photocatalytic Performance of Bismuth Oxyiodides

Synthesis of AgCl/Bi 3 O 4 Cl Composite and Its Photocatalytic Activity in RhB Degradation under Visible Light

Situ Preparation of Z-Scheme AgI/Bi 5 O 7 I Hybrid and Its Excellent Photocatalytic Activity

Synthesis of G-C 3 N 4 /Bi 5 O 7 I Microspheres with Enhanced Photocatalytic Activity under Visible Light

Situ Co-Crystallization for Fabrication of g-C 3 N 4 /Bi 5 O 7 I Heterojunction for Enhanced Visible-Light Photocatalysis

One Pot Controllable Synthesis of Palygorskite/Bismuth Oxyiodide Hierarchical Microspheres for Improved Visible-Light Photocatalytic Performance

Situ Co-Precipitation for the Synthesis of an Ag/AgBr/Bi 5 O 7 I Heterojunction for Enhanced Visible-Light Photocatalysis

Synthesis of One-Dimensional Bi 5 O 7 Br 0.5 I 0.5 Solid Solution for Effective Real Oilfield Wastewater Treatment via Exciton Photocatalytic Process

Preparation and Photocatalytic Activity of BiOI/MnxZn1-XFe 2 O 4 Magnetic Photocatalyst

Rational Design on 3D Hierarchical Bismuth Oxyiodides via in Situ Self-Template Phase Transformation and Phase-Junction Construction for Optimizing Photocatalysis against Diverse Contaminants

Strengthened Photocatalytic Removal of Bisphenol a by Robust 3D Hierarchical N-p Heterojunctions Bi 4 O 5 Br 2 -MnO 2 via Boosting Oxidative Radicals Generation

A Novel Synergy of Er 3+ /Fe 3+ Co-Doped Porous Bi 5 O 7 I Microspheres with Enhanced Photocatalytic Activity under Visible-Light Irradiation

Photodegradation of Seven Bisphenol Analogues by Bi 5 O 7 I/UiO-67 Heterojunction: Relationship between the Chemical Structures and Removal Efficiency

Thermodynamic and Dynamic Dual Regulation Bi 2 O 2 CO 3 /Bi 5 O 7 I Enabling High-Flux Photogenerated Charge Migration for Enhanced Visible-Light-Driven Photocatalysis

Bifunctional Bi 12 O 17 Cl 2 /MIL-100(Fe) Composites toward Photocatalytic Cr(VI) Sequestration and Activation of Persulfate for Bisphenol A Degradation

Heterojunction Photocatalyst of Cavity Shaped Bi 2 S 3 /g-C 3 N 4 for Bisphenol a Degradation: Regulation of Internal Electric Field via Assistance of Interfacial Functional Groups

Metal-Organic Frameworks Derived C/TiO 2 for Visible Light Photocatalysis: Simple Synthesis and Contribution of Carbon Species

Architecting Epitaxial-Lattice-Mismatch-Free (LMF) Zinc Oxide/Bismuth Oxyiodide Nano-Heterostructures for Efficient Photocatalysis

Surface Oxygen Vacancy Modified Bi 2 MoO 6 /MIL-88B(Fe) Heterostructure with Enhanced Spatial Charge Separation at the Bulk & Interface

Construction of Ultra-Thin 2D CN-Br 0.12 /2%RhOx Photo-Catalyst with Rapid Electron and Hole Separation for Efficient Bisphenol A Degradation

Novel Ag Decorated, BiOCl Surface Doped AgVO 3 Nanobelt Ternary Composite with Z-Scheme Homojunction-Heterojunction Interface for High Prolific Photo Switching, Quantum Efficiency and Hole Mediated Photocatalysis

Construction of Ultrathin MoS 2 /Bi 5 O 7 I Composites: Effective Charge Separation and Increased Photocatalytic Activity

Data Availability Statement: Not applicable.

The authors declare no conflict of interest.