Boosted Photocatalytic Performance for Antibiotics Removal with Ag/PW12/TiO2 Composite: Degradation Pathways and Toxicity Assessment

Photocatalyst is the core of photocatalysis and directly determines photocatalytic performance. However, low quantum efficiency and low utilization of solar energy are important technical problems in the application of photocatalysis. In this work, a series of polyoxometalates (POMs) [H3PW12O40] (PW12)-doped titanium dioxide (TiO2) nanofibers modified with various amount of silver (Ag) nanoparticles (NPs) were prepared by utilizing electrospinning/photoreduction strategy, and were labelled as x wt% Ag/PW12/TiO2 (abbr. x% Ag/PT, x = 5, 10, and 15, respectively). The as-prepared materials were characterized with a series of techniques and exhibited remarkable catalytic activities for visible-light degradation tetracycline (TC), enrofloxacin (ENR), and methyl orange (MO). Particularly, the 10% Ag/PT catalyst with a specific surface area of 155.09 m2/g and an average aperture of 4.61 nm possessed the optimal photodegradation performance, with efficiencies reaching 78.19% for TC, 93.65% for ENR, and 99.29% for MO, which were significantly higher than those of PW12-free Ag/TiO2 and PT nanofibers. Additionally, various parameters (the pH of the solution, catalyst usage, and TC concentration) influencing the degradation process were investigated in detail. The optimal conditions are as follows: catalyst usage: 20 mg; TC: 20 mL of 20 ppm; pH = 7. Furthermore, the photodegradation intermediates and pathways were demonstrated by HPLC-MS measurement. We also investigated the toxicity of products generated during TC removal by employing quantitative structure-activity relationship (QSAR) prediction through a toxicity estimation software tool (T.E.S.T. Version 5.1.2.). The mechanism study showed that the doping of PW12 and the modification of Ag NPs on TiO2 broadened the visible-light absorption, accelerating the effective separation of photogenerated carriers, therefore resulting in an enhanced photocatalytic performance. The research provided some new thoughts for exploiting efficient and durable photocatalysts for environmental remediation.


Introduction
In recent years, photocatalysis technology, which can use solar energy for environmental purification and energy conversion, has received worldwide attention [1,2]. Photocatalytic technology has a wide range of applications in pollutants degradation, CO 2 reduction, water splitting to produce hydrogen and nitrogen fixation, etc. [3]. The core of photocatalysis is designing and developing the photocatalysts with visible-light response, prominent catalytic activity, and recyclability. Among the various photocatalysts, TiO 2 has received a lot of attention due to its low synthesis cost, lack of toxicity, and high catalytic  , respectively [27,28]. With the introduction of PW12 into TiO2, no peaks of PW12 are found in the diffraction peaks of PT, demonstrating the doping of PW12 in TiO2. When Ag NPs are deposited on PT, the main diffraction peaks of Ag/PT composite are similar to those of PT. Additionally, the main diffraction peak at 38.1°, belonging to Ag (111) phase (JCPDS no. 04-0783), is not obviously found, which might be attributed to the cover effect with diffraction peak of PT [29]. The obtained results certify the presence of PT and Ag NPs in these Ag/PT composites.  , respectively [27,28]. With the introduction of PW 12 into TiO 2 , no peaks of PW 12 are found in the diffraction peaks of PT, demonstrating the doping of PW 12 in TiO 2 . When Ag NPs are deposited on PT, the main diffraction peaks of Ag/PT composite are similar to those of PT. Additionally, the main diffraction peak at 38.1 • , belonging to Ag (111) phase (JCPDS no. 04-0783), is not obviously found, which might be attributed to the cover effect with diffraction peak of PT [29]. The obtained results certify the presence of PT and Ag NPs in these Ag/PT composites. Figure 2b displays the FT-IR spectra of various samples. TiO 2 has no obvious characteristic vibration peak, and the PW 12 exhibits four characteristic infrared absorption peaks in 700~1100 cm −1 , including the peaks at 1075, 975, 882, and 830 cm −1 , respectively. Concretely, the peak at 1075 cm −1 is caused by the vibration of the P-O bond, the peak at 975 cm −1 is assigned to the vibration of the W=O bond, and the two peaks at  [30,31]. Besides, the peak of PW 12 near 1600 cm −1 may belong to the adsorbed H 2 O molecules [32]. These peaks can be also observed in the PT and Ag/PT materials, indicating the integrity of the PW 12 Keggin unit in these composites. However, a shift in the vibrational frequencies (1060, 961, 868, and 815 cm −1 ) is detected for Ag/PT, manifesting the presence of interaction between PT and Ag [19]. The aforementioned results certify that the Ag/PT materials have been fabricated successfully.  Figure 2b displays the FT-IR spectra of various samples. TiO2 has no obvious characteristic vibration peak, and the PW12 exhibits four characteristic infrared absorption peaks in 700 ~ 1100 cm −1 , including the peaks at 1075, 975, 882, and 830 cm −1 , respectively. Concretely, the peak at 1075 cm −1 is caused by the vibration of the P-O bond, the peak at 975 cm −1 is assigned to the vibration of the W=O bond, and the two peaks at 882 and 830 cm −1 are attributable to the vibration of the two kinds of W-Oc/e-W bridge bonds [30,31]. Besides, the peak of PW12 near 1600 cm −1 may belong to the adsorbed H2O molecules [32]. These peaks can be also observed in the PT and Ag/PT materials, indicating the integrity of the PW12 Keggin unit in these composites. However, a shift in the vibrational frequencies (1060, 961, 868, and 815 cm −1 ) is detected for Ag/PT, manifesting the presence of interaction between PT and Ag [19]. The aforementioned results certify that the Ag/PT materials have been fabricated successfully.
A UV-Vis diffuse reflectance spectra (DRS) measurement was performed to evaluate the light absorption properties of the obtained specimens. According to Figure 3a, the light absorption edge of TiO2, PW12 catalysts appeared around 400 and 380 nm. For PT photocatalysts, the light absorption intensity was increased due to the adulteration of PW12. In particular, the strongest optical absorption ability in the Ag/PT composites can be attributed to the introduction of Ag NPs [33], which would be beneficial to produce more photogenerated charge carriers to participate in the reaction [34]. We found that the SPR absorption band of Ag NPs ranges from 480 nm to 550 nm ( Figure S2) [35]. Furthermore, as shown in Figure 3b, the band gaps of various catalysts were calculated by the following equation: αhν = A(hν−Eg) 1/2 , in which A, hν, and α represent the constant, photon energy, and absorption coefficient, respectively [36].  A UV-Vis diffuse reflectance spectra (DRS) measurement was performed to evaluate the light absorption properties of the obtained specimens. According to Figure 3a, the light absorption edge of TiO 2 , PW 12 catalysts appeared around 400 and 380 nm. For PT photocatalysts, the light absorption intensity was increased due to the adulteration of PW 12 . In particular, the strongest optical absorption ability in the Ag/PT composites can be attributed to the introduction of Ag NPs [33], which would be beneficial to produce more photogenerated charge carriers to participate in the reaction [34]. We found that the SPR absorption band of Ag NPs ranges from 480 nm to 550 nm ( Figure S2) [35]. Furthermore, as shown in Figure 3b, the band gaps of various catalysts were calculated by the following equation: αhν = A(hν−E g ) 1/2 , in which A, hν, and α represent the constant, photon energy, and absorption coefficient, respectively [36].  Figure 2b displays the FT-IR spectra of various samples. TiO2 has no obvious characteristic vibration peak, and the PW12 exhibits four characteristic infrared absorption peaks in 700 ~ 1100 cm −1 , including the peaks at 1075, 975, 882, and 830 cm −1 , respectively. Concretely, the peak at 1075 cm −1 is caused by the vibration of the P-O bond, the peak at 975 cm −1 is assigned to the vibration of the W=O bond, and the two peaks at 882 and 830 cm −1 are attributable to the vibration of the two kinds of W-Oc/e-W bridge bonds [30,31]. Besides, the peak of PW12 near 1600 cm −1 may belong to the adsorbed H2O molecules [32]. These peaks can be also observed in the PT and Ag/PT materials, indicating the integrity of the PW12 Keggin unit in these composites. However, a shift in the vibrational frequencies (1060, 961, 868, and 815 cm −1 ) is detected for Ag/PT, manifesting the presence of interaction between PT and Ag [19]. The aforementioned results certify that the Ag/PT materials have been fabricated successfully.
A UV-Vis diffuse reflectance spectra (DRS) measurement was performed to evaluate the light absorption properties of the obtained specimens. According to Figure 3a, the light absorption edge of TiO2, PW12 catalysts appeared around 400 and 380 nm. For PT photocatalysts, the light absorption intensity was increased due to the adulteration of PW12. In particular, the strongest optical absorption ability in the Ag/PT composites can be attributed to the introduction of Ag NPs [33], which would be beneficial to produce more photogenerated charge carriers to participate in the reaction [34]. We found that the SPR absorption band of Ag NPs ranges from 480 nm to 550 nm ( Figure S2) [35]. Furthermore, as shown in Figure 3b, the band gaps of various catalysts were calculated by the following equation: αhν = A(hν−Eg) 1/2 , in which A, hν, and α represent the constant, photon energy, and absorption coefficient, respectively [36].  The band gap values were 3.17, 3.29, 2.83, 2.80, 2.72, and 2.61 eV for TiO 2 , PW 12 , PT, and x% Ag/PT (x = 5, 10 and 15), respectively. The doping of H 3 PW 12 O 40 introduces additional electronic states and energy levels into the band structure of TiO 2 . These additional electronic states can interact with the electron energy levels of TiO 2 , leading to adjustments in the band structure, thereby reducing the band gap [11,27]. Obviously, in comparison with PT, the band gap of Ag/PT was reduced, which suggests that Ag might introduce a local energy level to the band gap of PT, resulting in a reduced energy gap [37].
The composition and chemical state information of as-prepared specimens were probed with X-ray photoelectron spectroscopy (XPS). The elemental composition of 10% Ag/PT was demonstrated by the signal detection of P, W, O, Ti, and Ag elements in the full XPS spectra (Figure 4a). Figure 4b-f shows the high resolution XPS profiles for Ag 3d, P 2p, W 4f, Ti 2p, and O 1s of PT and 10% Ag/PT, confirming the successful preparation of the composites. As presented in Figure 4b, the 10% Ag/PT composite showed two peaks at Ag 3d, located at 367.61 eV and 373.59 eV, belonging to Ag 0 3d 5/2 and Ag 0 3d 3/2 metallic silver monomers, respectively [38,39]. The P 2p XPS profile for PT ( Figure 4c) has a peak at 133.70 eV, and this binding energy was considered to be the presence of P 5+ [40]. The P 2p peak of 10% Ag/PT was shifted towards the lower binding energy region in comparison with PT. In the PT material, the high-resolution XPS spectrum of the W 4f region (Figure 4d) showed two peaks at 35.58 eV and 37.63 eV for the W 4f 7/2 and W 4f 5/2 binding energies, respectively, and, in 10% Ag/PT, W 4f was shifted toward the lower binding energy with binding energies of 35.28 eV and 37.32 eV [41,42]. Figure 4e shows the presence of Ti 2p 3/2 and Ti 2p 1/2 characteristic peaks observed at 458.49 eV and 464.16 eV in PT, which are features of Ti 4+ in TiO 2 [43]. Notably, the binding energies of Ti 2p XPS for 10% Ag/PT were shifted to 458.45 eV and 464.13 eV, providing evidence of the interaction between PT and Ag [44]. Figure 4f shows the XPS spectra of O 1s. Two peaks, at 529.57 eV (PT) and 529.48 eV (10% Ag/PT), were found, which were considered as Ti-O [45]; meanwhile, two peaks are found at 531.21 eV and 532.12 eV (PT) and 531.11 eV and 532.01 eV (10% Ag/PT), corresponding to W-O and P-O, respectively [46]. Notably, these peaks in 10% Ag/PT composites shifted to lower binding energies compared to PT, which indicated the presence of interfacial interaction between Ag and PT [47].   Figure 5a demonstrates that the N 2 adsorption and desorption isotherms of different specimens conform to type IV, while the hysteresis line follows type H1, indicating the presence of a mesoporous structure [48,49]. The specific surface areas (SSA) were 30.39, 146.85, 156.42, 155.09, and 166.91 m 2 /g for TiO 2 , PT and x% Ag/PT (x = 5, 10 and 15), respectively. The result suggested that the introduce of PW 12 is beneficial to enhance the SSA of TiO 2 , which would demonstrate an improved catalytic performance. Figure 5b presents the pore size distributions of as-obtained samples. The average pore volumes were 11.57, 5.32, 4.25, 4.61, and 4.40 nm for TiO 2 , PT, and x% Ag/PT (x = 5, 10 and 15), respectively. It is clear that the average pore volume of Ag/PT composites decreased, which might be due to the accumulation of Ag NPs on the PT surface.

Photocatalytic Removal of TC
TC was chosen as an organic pollutant to explore the photocatalytic capacity of obtained samples [50,51]. As presented in Figure 6a, the adsorption-desorption equilibrium was reached between the catalyst and TC under dark conditions within 20 min. The control experiment was designed and demonstrated that the self-photolysis process of TC can

Photocatalytic Removal of TC
TC was chosen as an organic pollutant to explore the photocatalytic capacity of obtained samples [50,51]. As presented in Figure 6a, the adsorption-desorption equilibrium was reached between the catalyst and TC under dark conditions within 20 min. The control experiment was designed and demonstrated that the self-photolysis process of TC can be excluded. TiO 2 exhibits a negative effect on the TC degradation. The degradation efficiencies of TC on PT and 10% Ag/TiO 2 were significantly higher compared to pure TiO 2 , which reached 26.53% and 43.52% within 60 min, respectively. This indicates that the photocatalytic activity of TiO 2 can be improved with the proper introduction of H 3 PW 12 O 40 or Ag NPs. Moreover, the photocatalytic property of Ag/PT was further boosted, benefiting from the remarkable contribution of the SPR effect originating from the Ag NPs. The 10% Ag/PT composite shows the optimal degradation efficiency of 78.19% ( Figure S3a), which exhibits better performance compared to numerous other catalysts, in terms of TC removal (Table S1). Besides, the removal of total organic carbon (TOC) for TC degradation reached 60.08% within 1 h using 10% Ag/PT material ( Figure S4), which implies that the TC degradation was incomplete. Nevertheless, when more Ag was deposited on the PT, the TC removal rate of the synthesized 15% Ag/PT composite reduced to 71.12%. Because excessive Ag occupies a part of the active sites of PT, the adsorption capacity and degradation rate of Ag/PT composite towards TC molecules is reduced.
As presented in Figure 6b, the fitting results of the TC degradation rate indicate that it was in accordance with the first-order kinetic model. Distinguishingly, the reaction rate constant k for TC degradation with 10% Ag/PT was 0.0227 min −1 , which was about 29-and 8-times higher than those of TiO 2 and PT, respectively. Therefore, the doping of PW 12 and the modification of Ag NPs are effective methods to boost the photocatalytic performance of TiO 2 . dation rate of Ag/PT composite towards TC molecules is reduced.
As presented in Figure 6b, the fitting results of the TC degradation rate indicate that it was in accordance with the first-order kinetic model. Distinguishingly, the reaction rate constant k for TC degradation with 10% Ag/PT was 0.0227 min −1 , which was about 29-and 8-times higher than those of TiO2 and PT, respectively. Therefore, the doping of PW12 and the modification of Ag NPs are effective methods to boost the photocatalytic performance of TiO2. Effect of different pH values: The degradation of TC in aqueous solution undergoes protonation and deprotonation reactions, and the pH of the solution will lead to different charge states, which affects the decomposition of TC. As shown in Figure 6c, the TC degradation efficiency gradually increased with the increase of pH, which achieved the optimal value of 87.42% at pH 11. The alkaline environment favors the generation of •O 2 − , which is one kind of active species during the pollutant degradation process [52]. Besides, TC molecules exhibit a high susceptibility to photolysis in alkaline conditions, benefiting from the transition from the π to π* states of the (HOMO-1 to LUMO) chromophore [53]. At neutral pH, the TC removal rate was 78.19% after 60 min of light exposure. However, under acidic conditions, the degradation efficiency of TC further decreased. In Figure 6c, the adsorption removal efficiency of TC by 10% Ag/PT at different pH conditions were 10.04% (pH 1.0), 15.41% (pH 3.0), 16.28% (pH 5.0), 16.78% (pH 7.0), 14.61% (pH 9.0), and 8.67% (pH 11.0). This may be related to the zeta potential of the catalyst, which was examined for 10% Ag/PT at different pH conditions (Figure 6d). Obviously, the zeta potential of 10% Ag/PT was positive at pH < 2.4 and negative at pH > 2.4. Moreover, when pH < 3.3, TC appeared as a cation (TCH 3 + ); when pH = 3.3~7.7, TC existed as an ampholyte (TCH 2 0 ); when pH was greater than 7.7, TC appeared as an anion (TCH 3 − ) [54]. Therefore, when pH = 1.0, the surface of 10% Ag/PT was positively charged and the TC molecules were present in the protonated (TCH 3 + , pH < 3.3), which generated an intense electrostatic repulsion and weak adsorption ability. With the increase of pH from 3 to 7, the positive surface charge of 10% Ag/PT decreased from −4.64 mV to −21.07 mV, and the TC molecules were in neutral (TCH 2 0 , pH 3.3-7.7), indicating that the electrostatic repulsion was suppressed, thus promoting the adsorption capacity. When the pH was 9.0 and 11.0, the electrostatic repulsion existed between the catalyst with a negative charge and TC (TCH 3 − , pH > 7.7). Furthermore, the excess OH − could occupy the adsorption sites of the catalyst, generating a slight reduction of adsorption ability [55].
Influence of catalyst dosage: As shown in Figure 6e, the degradation efficiency was significantly enhanced from 60.35% to 78.19%, with the catalyst quantity from 10 to 20 mg, which could be assigned to the increase of active sites [56]. However, the TC degradation rate increased indistinctively (78.19% to 82.64%) upon further increasing the catalyst usage from 20 to 30 mg, which may be due to the poor light transmission of the solution applying too much catalyst [57].
Effects of initial TC concentration: Figure 6f provides the effect of TC concentration on the photodegradation performance. The TC degradation rate decreased continuously, with the TC concentration ranging from 10 to 80 ppm. The explanation may be that the limited number of photogenerated carriers lead to restrict TC degradation when the initial TC concentration was too high. In addition, the higher TC concentration affected the penetration ability of photons and, thus, negatively affects the photocatalytic activity [58].

Photocatalytic Degradation of ENR and MO
The catalytic performance for Ag/PT composites were further evaluated by degrading ENR and MO in visible-light. During the dark reaction, the pollutants molecules were adsorbed on the photocatalyst surface for 20 min to obtain the adsorption-desorption equilibrium. As presented in Figure 7a, the photocatalytic degradation efficiencies of ENR with control, TiO 2 , 10% Ag/TiO 2 , PT, 5% Ag/PT, 10% Ag/PT, and 15% Ag/PT were 1.99%, 20.17%, 58.84%, 63.09%, 87.93%, 93.65%, and 89.98%. Specially, 10% Ag/PT had the best photocatalytic activity of 93.65% (k = 0.0194) (Figures 7b and S3b), which was 4.64-, 1.48-, and 1.59-times higher than that of TiO 2 , 10% Ag/TiO 2 , and PT, respectively. Similarly, the degradation profiles in Figure 7c manifesting 10% Ag/PT also displayed an excellent MO degradation rate of 99.29% (k = 0.1549) (Figures 7d and S3c). The influencing parameters of catalyst dosage and MO concentration were also studied in Figure S6. Moreover, the degradation efficiencies of Ag/PT composites are superior to other catalysts for ENR and MO removal (Tables S2 and S3). These data verify that as-prepared Ag/PT is one kind of multi-functional material in the field of environmental remediation.
Molecules 2023, 28, x FOR PEER REVIEW 9 of 22 and 1.59-times higher than that of TiO2, 10% Ag/TiO2, and PT, respectively. Similarly, the degradation profiles in Figure 7c manifesting 10% Ag/PT also displayed an excellent MO degradation rate of 99.29% (k = 0.1549) (Figures 7d and S3c). The influencing parameters of catalyst dosage and MO concentration were also studied in Figure S6. Moreover, the degradation efficiencies of Ag/PT composites are superior to other catalysts for ENR and MO removal (Tables S2 and S3). These data verify that as-prepared Ag/PT is one kind of multi-functional material in the field of environmental remediation.   Figure 8a shows the cycling experiments of 10% Ag/PT as a visible-light catalyst for the degradation of various contaminants. After 20 cycles of reuse, the degradation efficiency of MO, ENR, and TC exhibited a slight decrease, and by using ICP-6000 test, the leaching amount of Ag after degradation was 2.1 ppm, indicating that the as-obtained Ag/PT composites had good reuse performance. Moreover, the photocatalytic stability of Ag/PT materials was confirmed with XRD and FT-IR. As shown in Figure 8b,c, the XRD diffraction peaks and FT-IR spectra of the used 10% Ag/PT remained unchanged in comparison with the fresh sample, verifying the good structural stability of these materials. Furthermore, the TEM image after TC removal (Figure 8d) also demonstrated the good cycling stability of the catalyst.  Figure 8a shows the cycling experiments of 10% Ag/PT as a visible-light catalyst for the degradation of various contaminants. After 20 cycles of reuse, the degradation efficiency of MO, ENR, and TC exhibited a slight decrease, and by using ICP-6000 test, the leaching amount of Ag after degradation was 2.1 ppm, indicating that the as-obtained Ag/PT composites had good reuse performance. Moreover, the photocatalytic stability of Ag/PT materials was confirmed with XRD and FT-IR. As shown in Figure 8b,c, the XRD diffraction peaks and FT-IR spectra of the used 10% Ag/PT remained unchanged in comparison with the fresh sample, verifying the good structural stability of these materials. Furthermore, the TEM image after TC removal (Figure 8d) also demonstrated the good cycling stability of the catalyst.

Photogenerated Carriers Behavior Analysis
The photoluminescence (PL) spectra were measured to reflect the separation efficiency of photoinduced carriers from the synthesized catalysts. As demonstrated in Figure  9a, these materials exhibited similar peaks at 425 nm. The fluorescence intensity for Ag/PT composite exhibited a significant decrease compared to TiO2, PT, and 10% Ag/TiO2, implying that the recombination of photogenerated charge carriers was effectively suppressed [59,60]. In addition, the 10% Ag/PT catalyst had the lowest peak intensity, implying a higher separation rate of electron-hole pairs and better catalytic capacity compared

Photogenerated Carriers Behavior Analysis
The photoluminescence (PL) spectra were measured to reflect the separation efficiency of photoinduced carriers from the synthesized catalysts. As demonstrated in Figure 9a, these materials exhibited similar peaks at 425 nm. The fluorescence intensity for Ag/PT composite exhibited a significant decrease compared to TiO 2 , PT, and 10% Ag/TiO 2 , implying that the recombination of photogenerated charge carriers was effectively suppressed [59,60]. In addition, the 10% Ag/PT catalyst had the lowest peak intensity, implying a higher separation rate of electron-hole pairs and better catalytic capacity compared to the remaining specimens. The fluorescence lifetimes of PT and 10% Ag/PT were determined by time-resolved fluorescence attenuation spectrometry (TRPL). As revealed in Figure 9b, the fluorescence intensity of PT and 10% Ag/PT both decreased exponentially. The average fluorescence lifetime τ ave of PT and 10% Ag/PT were calculated to be 0.18 ns and 0.06 ns, respectively (Table S4). The result shows that 10% Ag/PT has a shorter average decay time than PT, which indicates that the deposition of Ag nanoparticles is beneficial to delay the recombination of photoinduced carriers [61]. The corresponding quenching and lifetime reduction of TRPL implies a high non-radiative decay rate at 10% Ag/PT, and the establishment of a fast electron transfer pathway for accumulated photoproduced electrons is conducive to the enhancement of catalytic capacity [62]. The electrochemical impedance spectroscopy (EIS) and instantaneous photocurrent have been employed for examining the separation and migration ability of photogenerated electron-hole pairs. Figure 9c illustrates the EIS Nyquist plots form distinct electrodes, and the equivalent circuit are provided as an insert. Generally, the small EIS radian of the electrochemical impedance corresponds to the low charge transfer resist [63]. It is clear that the radius of these Ag/PT materials were much smaller than those of TiO2, PT, and 10% Ag/TiO2. Specially, 10% Ag/PT has the smallest radius, which strongly manifested that the composite possessed fastest transfer and migration ability of carriers [64]. Additionally, Figure S7 presents the Bode plots of PT and 10% Ag/PT, which confirmed a prolonged lifetime of photoinduced electrons for 10% Ag/PT in comparison to PT. The photocurrents of obtained specimens were measured in Figure 9d. The photocurrent was found to be stable and reproducible in three cycles. The photocurrent density obeyed the following order: 10% Ag/PT > 15% Ag/PT > 5% Ag/PT > 10% Ag/TiO2 > PT > TiO2. Specifically, the photocurrent density of 10% Ag/PT (0.23 µA/cm 2 ) was much larger than that of PT (0.09 µA/cm 2 ) and 10% Ag/TiO2 (0.05 µA/cm 2 ), which would lead to a remarkable enhancement in photocatalytic capability [65]. The results of various measurements collectively demonstrated that the Ag/PT composites have low charge transfer resistance and high separation efficiency of photogenerated carriers, which would reveal an outstanding catalytic performance. The electrochemical impedance spectroscopy (EIS) and instantaneous photocurrent have been employed for examining the separation and migration ability of photogenerated electron-hole pairs. Figure 9c illustrates the EIS Nyquist plots form distinct electrodes, and the equivalent circuit are provided as an insert. Generally, the small EIS radian of the electrochemical impedance corresponds to the low charge transfer resist [63]. It is clear that the radius of these Ag/PT materials were much smaller than those of TiO 2 , PT, and 10% Ag/TiO 2 . Specially, 10% Ag/PT has the smallest radius, which strongly manifested that the composite possessed fastest transfer and migration ability of carriers [64]. Additionally, Figure S7 presents the Bode plots of PT and 10% Ag/PT, which confirmed a prolonged lifetime of photoinduced electrons for 10% Ag/PT in comparison to PT. The photocurrents of obtained specimens were measured in Figure 9d. The photocurrent was found to be stable and reproducible in three cycles. The photocurrent density obeyed the following order: 10% Ag/PT > 15% Ag/PT > 5% Ag/PT > 10% Ag/TiO 2 > PT > TiO 2 . Specifically, the photocurrent density of 10% Ag/PT (0.23 µA/cm 2 ) was much larger than that of PT (0.09 µA/cm 2 ) and 10% Ag/TiO 2 (0.05 µA/cm 2 ), which would lead to a remarkable enhancement in photocatalytic capability [65]. The results of various measurements collectively demonstrated that the Ag/PT composites have low charge transfer resistance and high separation efficiency of photogenerated carriers, which would reveal an outstanding catalytic performance.

Active Species in Photocatalytic Reactions
To elucidate the degradation mechanism of TC, the radical capture experiments were performed, and the results were presented in Figure 10a. Herein, 4-hydroxymethylpropane (TEMPO, ·O 2 − quencher), triethanolamine (TEOA, h + quencher), and isopropyl alcohol (IPA, ·OH quencher) were employed as free radical trapping agents [66,67]. Distinctly, the addition of TEOA to the reaction system significantly inhibited the degradation efficiency, and the addition of TEMPO also reduced the degradation activity to some extent, verifying the important function of h + and ·O 2 − in TC degradation. Meanwhile, the degradation rate was almost unchanged with the addition of IPA, implying that ·OH was not the dominating active substance.
Molecules 2023, 28, x FOR PEER REVIEW 12 of 22 verifying the important function of h + and ·O2 − in TC degradation. Meanwhile, the degradation rate was almost unchanged with the addition of IPA, implying that ·OH was not the dominating active substance. To directly verify the reactive species involved in the reaction process, electron spin resonance (ESR) measurement was conducted, applying 5,5-dimethyl-1-pyrroline N-oxide (DMPO) and 2,2,6,6-Tetramethyl-1-piperidinyloxy (TEMPO) as spin-trapping agents [68]. TEMPO can trap the photogenerated holes and form TEMPO-h⁺ spin-products, which exhibit silent ESR signals. As displayed in Figure 10b, under dark conditions, three distinctive peaks corresponding to the TEMPO were identified, which were obviously declined under visible-light, demonstrating the production of TEMPO-h + spin-products [69]. Meanwhile, ·OH and ·O2 − can be captured with DMPO, generating evident ESR signals. In Figure 10c, no characteristic peaks were found under both dark and light conditions in the ·OH test, indicating that ·OH did not play a role in the catalytic reaction. In Figure 10d, in the ·O2 − test, no characteristic peaks were detected under dark conditions; nevertheless, the characteristic peaks corresponding to DMPO-·O₂⁻ were clearly observed upon visiblelight irradiation, authenticating successful generation of ·O2 − radicals. These results indicated that the photodegradation of TC was primarily driven with the involvement of ·O2 − radicals and h + .

Degradation Pathways of TC and Toxicity Assessment
As revealed in Figures 11 and S5, the pathways of TC photodegradation were explored by HPLC-MS. The molecular weight of TC is expressed as the product m/z = 444. To directly verify the reactive species involved in the reaction process, electron spin resonance (ESR) measurement was conducted, applying 5,5-dimethyl-1-pyrroline N-oxide (DMPO) and 2,2,6,6-Tetramethyl-1-piperidinyloxy (TEMPO) as spin-trapping agents [68]. TEMPO can trap the photogenerated holes and form + TEMPO-h + spin-products, which exhibit silent ESR signals. As displayed in Figure 10b, under dark conditions, three distinctive peaks corresponding to the TEMPO were identified, which were obviously declined under visible-light, demonstrating the production of TEMPO-h + spin-products [69]. Meanwhile, ·OH and ·O 2 − can be captured with DMPO, generating evident ESR signals. In Figure 10c, no characteristic peaks were found under both dark and light conditions in the ·OH test, indicating that ·OH did not play a role in the catalytic reaction. In Figure 10d, in the ·O 2 − test, no characteristic peaks were detected under dark conditions; nevertheless, the characteristic peaks corresponding to DMPO-·O 2 − were clearly observed upon visible-light irradiation, authenticating successful generation of ·O 2 − radicals. These results indicated that the photodegradation of TC was primarily driven with the involvement of ·O 2 − radicals and h + .

Degradation Pathways of TC and Toxicity Assessment
As revealed in Figures 11 and S5, the pathways of TC photodegradation were explored by HPLC-MS. The molecular weight of TC is expressed as the product m/z = 444. Figure 11 summarizes and illustrates two possible degradation pathways. In pathway 1, the intermediate of T1 (m/z = 463) may be derived from the dehydroxylation of TC, after which T1 forms T2 (m/z = 403) through the deamidation process. Intermediate with T3 (m/z = 357) is resulted from loss of one N-2 methyl group. The product T4 (m/z = 259) is obtained by the ring-opening reaction of T3. Pathway 2 is the transition from TC to T5 (m/z = 427) after deamination. Then, T5 is dehydroxylated and dedimethylated to T6 (m/z = 398), which is deaminated and demethylated to T7 (m/z = 318). After T4, T8 is formed by the break of double-bond oxygen, and T7 is formed by ring-opening and dehydroxylation. After continuous ring-opening reactions, T8 forms T9 (m/z = 228), T10 (m/z = 182), T11 (m/z = 100), and T12 (m/z = 74). Further degradation of intermediates can produce small molecules such as CO 2 , H 2 O, and inorganic ions. According to the above analysis, it can be inferred that photocatalytic degradation of tetracycline involves deamidation, dehydroxylation, and ring-opening reactions [3,70].
Molecules 2023, 28, x FOR PEER REVIEW 13 of 22 = 398), which is deaminated and demethylated to T7 (m/z = 318). After T4, T8 is formed by the break of double-bond oxygen, and T7 is formed by ring-opening and dehydroxylation. After continuous ring-opening reactions, T8 forms T9 (m/z = 228), T10 (m/z = 182), T11 (m/z = 100), and T12 (m/z = 74). Further degradation of intermediates can produce small molecules such as CO2, H2O, and inorganic ions. According to the above analysis, it can be inferred that photocatalytic degradation of tetracycline involves deamidation, dehydroxylation, and ring-opening reactions [3,70]. Furthermore, we investigated the toxicity of TC and its 12 intermediates using QSAR prediction with a toxicity estimation software tool (T.E.S.T. Version 5.1.2) [71]. Figure 12a,b show that TC was "developmentally toxic" and "mutagenic positive" [72]. One developmentally non-toxic TC intermediate (T10) and four mutagenic-negative TC intermediates (T7, T10, T11, T12) were produced after light treatment. Furthermore, most intermediates were less toxic than TC. As illustrated in Figure 12c, the bioaccumulation factors of intermediates T9 and T6 were lower than those of TC, and the photodegradation process could reduce the bioaccumulation factor for TC, which was primarily attributed to the hydroxylation reaction [73].
In Figure 12d-f, three evaluation indicators were used to evaluate the acute toxicity of TC and its intermediates: (i) Fathead minnow LC50 (96 h) represents the concentration at which 50% of fathead minnows are killed after 96 h; (ii) Daphnia magna LC50 (48 h) represents the concentration at which 50% of Daphnia magna are killed after 48 h; and (iii) Oral rats LD50 represents the concentration at which 50% of rats are killed after 48 h of oral ingestion. The LC50 values of 0.90 mg/L for blackhead minnow, 12.70 mg/L for Daphnia magna, and 1105.75 mg/kg for TC in rats were defined as "highly toxic", "harmful", and "toxic" compounds, respectively [74]. Obviously, T1, T6, T7, and T8 intermediates all showed low LD50 values (Figure 12d). Daphnia magna showed lower LC50 values than TC intermediates, except for T6, T7, T1, T2, T3, and T8 (Figure 12e). With the exception of intermediates T5 and T11, rats exhibited lower toxicity to TC intermediates (Figure 12f). According to the aforementioned toxicity prediction results, the toxicity of several intermediates still exists, which could be reduced by extending the reaction time. Furthermore, we investigated the toxicity of TC and its 12 intermediates using QSAR prediction with a toxicity estimation software tool (T.E.S.T. Version 5.1.2) [71]. Figure 12a,b show that TC was "developmentally toxic" and "mutagenic positive" [72]. One developmentally non-toxic TC intermediate (T10) and four mutagenic-negative TC intermediates (T7, T10, T11, T12) were produced after light treatment. Furthermore, most intermediates were less toxic than TC. As illustrated in Figure 12c, the bioaccumulation factors of intermediates T9 and T6 were lower than those of TC, and the photodegradation process could reduce the bioaccumulation factor for TC, which was primarily attributed to the hydroxylation reaction [73].
In Figure 12d-f, three evaluation indicators were used to evaluate the acute toxicity of TC and its intermediates: (i) Fathead minnow LC50 (96 h) represents the concentration at which 50% of fathead minnows are killed after 96 h; (ii) Daphnia magna LC50 (48 h) represents the concentration at which 50% of Daphnia magna are killed after 48 h; and (iii) Oral rats LD50 represents the concentration at which 50% of rats are killed after 48 h of oral ingestion. The LC50 values of 0.90 mg/L for blackhead minnow, 12.70 mg/L for Daphnia magna, and 1105.75 mg/kg for TC in rats were defined as "highly toxic", "harmful", and "toxic" compounds, respectively [74]. Obviously, T1, T6, T7, and T8 intermediates all showed low LD50 values (Figure 12d). Daphnia magna showed lower LC50 values than TC intermediates, except for T6, T7, T1, T2, T3, and T8 (Figure 12e). With the exception of intermediates T5 and T11, rats exhibited lower toxicity to TC intermediates (Figure 12f). According to the aforementioned toxicity prediction results, the toxicity of several intermediates still exists, which could be reduced by extending the reaction time.

Possible Photocatalytic Mechanism
In Figure S9, the tangent slope of the Mott-Schottky profile reflects that PT belongs to n-type semiconductor. The Efb of PT relative to Hg/Hg2Cl2 was found to be −0.17 eV. Given that the conduction band energy (ECB) of n-type semiconductor is approximately 0.2 eV higher than the flat band potential (Efb) [75], the ECB for PT could be determined as −0.13 eV (vs. NHE), according to ENHE = EHg/Hg2Cl2 + 0.242 eV. From the (αhv) 2 vs. hv plot ( Figure  3b), the band gap energy (Eg) of PT is calculated to be 2.83 eV. Therefore, the VB (valence band) edge position of PT (EVB = ECB + Eg) is determined to be 2.70 eV [76]. Based on the aforementioned results, the catalytic mechanism for TC degradation by Ag/PT system with visible-light was proposed ( Figure 13). The PT was photoexcited to generate electrons and holes under visible-light irradiation (Equation (1)). Meanwhile, a large number of hot electrons are produced, due to the surface plasmon resonance (SPR) effect of Ag NPs [77,78]. The Ag NPs serving as electron traps could effectively capture photoinduced electrons on the CB of PT, while the Schottky barrier established by Ag 0 could promote the transfer of SPR-excited electrons, further accelerating the charge separation (Equation (2)). These electrons on Ag NPs react with O2 to form ·O2 − participating in oxidation reaction (Equations (3) and (4)). Moreover, the photoinduced holes in PT directly oxidize TC according to the result of ESR measurements and capturing tests (Equation (5)). Ultimately, TC was efficiently removed with the help of h + and ·O2 − active species (Equation (6)).

Possible Photocatalytic Mechanism
In Figure S9, the tangent slope of the Mott-Schottky profile reflects that PT belongs to n-type semiconductor. The E fb of PT relative to Hg/Hg 2 Cl 2 was found to be −0.17 eV. Given that the conduction band energy (E CB ) of n-type semiconductor is approximately 0.2 eV higher than the flat band potential (E fb ) [75], the E CB for PT could be determined as −0.13 eV (vs. NHE), according to E NHE = E Hg/Hg2Cl2 + 0.242 eV. From the (αhv) 2 vs. hv plot (Figure 3b), the band gap energy (E g ) of PT is calculated to be 2.83 eV. Therefore, the VB (valence band) edge position of PT (E VB = E CB + E g ) is determined to be 2.70 eV [76]. Based on the aforementioned results, the catalytic mechanism for TC degradation by Ag/PT system with visible-light was proposed ( Figure 13). The PT was photoexcited to generate electrons and holes under visible-light irradiation (Equation (1)). Meanwhile, a large number of hot electrons are produced, due to the surface plasmon resonance (SPR) effect of Ag NPs [77,78]. The Ag NPs serving as electron traps could effectively capture photoinduced electrons on the CB of PT, while the Schottky barrier established by Ag 0 could promote the transfer of SPR-excited electrons, further accelerating the charge separation (Equation (2)). These electrons on Ag NPs react with O 2 to form ·O 2 − participating in oxidation reaction (Equations (3) and (4)). Moreover, the photoinduced holes in PT directly oxidize TC according to the result of ESR measurements and capturing tests (Equation (5)). Ultimately, TC was efficiently removed with the help of h + and ·O 2 − active species (Equation (6)).

Construction of Ag/PT Photocatalysts
As shown in Scheme 1, Ag/PT composite nanofibers were prepared employing electrospinning/photoreduction methods. First of all, PT nanofibers were synthesized by the electrospinning/calcination method. Briefly, PVP was dissolved in a mixture of anhydrous ethanol, acetic acid, and tetrabutyl titanate, and stirred for 1 h. PW12 was then added and stirred until complete dissolution. The homogeneous precursor solution was subjected to electrostatic spinning operation, followed by calcination, to prepare PT nanofibers. Secondly, Ag NPs were modified on the PT nanofibers by photoreduction. PT nanofibers powder was added to the solution of Vwater:Visoprobanol = 1:1, which was then sonicated for 30 min. Then, the solution was evacuated, and the suspension was illuminated for 1 h using a 300 W xenon lamp with full spectrum light. Then, AgNO3 solution was added and stirred for 60 min. The Ag/PT composite was prepared. Figure 13. The photocatalytic mechanism of TC degradation using Ag/PT system.

Construction of Ag/PT Photocatalysts
As shown in Scheme 1, Ag/PT composite nanofibers were prepared employing electrospinning/photoreduction methods. First of all, PT nanofibers were synthesized by the electrospinning/calcination method. Briefly, PVP was dissolved in a mixture of anhydrous ethanol, acetic acid, and tetrabutyl titanate, and stirred for 1 h. PW 12 was then added and stirred until complete dissolution. The homogeneous precursor solution was subjected to electrostatic spinning operation, followed by calcination, to prepare PT nanofibers. Secondly, Ag NPs were modified on the PT nanofibers by photoreduction. PT nanofibers powder was added to the solution of V water :V isoprobanol = 1:1, which was then sonicated for 30 min. Then, the solution was evacuated, and the suspension was illuminated for 1 h using a 300 W xenon lamp with full spectrum light. Then, AgNO 3 solution was added and stirred for 60 min. The Ag/PT composite was prepared.

Conclusions
Herein, a novel Ag/PT composite material has been constructed utilizing electrospinning/photoreduction methods, which exhibited remarkable photocatalytic activities for degradation TC, ENR, and MO. The results of mechanism investigation showed that the excellent catalytic property could be due to the following two reasons: (1) the doping of PW 12 to TiO 2 can enhance the utilization of visible spectrum and redox reaction activity of titanium dioxide; (2) the precious metal Ag possesses the LSPR effect, which can improve the utilization of sunlight and generate more charge carriers. Besides, the LSPR effect will have a high-intensity small range electromagnetic field, which will greatly improve the separation rate of photogenerated electron-hole pairs. Moreover, the degradation intermediates and pathways were revealed through HPLC-MS. The toxicity of TC degradation products was also investigated using QSAR prediction. This current work offers novel thoughts for developing efficient and stable catalysts for environmental remediation.