Assessing the Photocatalytic Degradation of Fluoroquinolone Norfloxacin by Mn:ZnS Quantum Dots: Kinetic Study, Degradation Pathway and Influencing Factors

Norfloxacin (NOFX), a broadly used fluoroquinolone antibiotic, has been a subject of great concern in the past few years due to its undesirable effect on human beings and aquatic ecosystems. In this study, novel Mn doped ZnS (Mn:ZnS) quantum dots (QDs) were prepared through a facile chemical precipitation method and used as photocatalysts for NOFX degradation. Prior to photodegradation experiments, morphological and optical parameters of the QDs were examined through transmission electron microscopy, scanning electron microscopy, energy dispersive X-ray analysis, Fourier transform infrared spectroscopy, ultraviolet-visible spectroscopy, fluorescence spectroscopy, Brunauer–Emmett–Teller analysis, and differential thermal and thermogravimetric analyses. Mn:ZnS QDs exhibited excellent properties of photodegradation, not only under UV irradiation but also in sunlight, which induced NOFX to photodegrade. The utmost photodegradation efficiency was obtained under optimal conditions (25 mL of NOFX, 15 mg/L, pH 10, 60 min UV irradiation, 60 mgs QDs), adopting first order kinetics. In addition, hydroxyl radicals produced by the conduction band electrons were found to be the primary reason dominating the transformation of NOFX in basic conditions, while holes, oxygen atoms, as well as the doped metal (Mn) enhanced the degradation. The QDs showed excellent reusability and stability in four repeated cycles. Finally, four different pathways were predicted, derived from the identified intermediates, with piperazinyl ring transformation being the primary one. It is expected that the synthesized Mn:ZnS QDs could be utilized as efficient photocatalytic materials for energy conversion and ecological remediation.


Introduction
In recent years, there has been considerable worldwide expansion in the occurrence, behaviour, and fate of pharmaceutically active compounds used for the treatment of infectious diseases and for enhancing agricultural production [1]. Due to their widespread use and incomplete biodegradability, partial removal of these antibiotics is accomplished in usual wastewater treatment plants and quite large quantities are deliberately discharged into the environment. Consequently, due to the lack of effective treatments of antibiotic wastewater, these can be found in surface waters, causing unfavorable effects on aquatic and terrestrial organisms [2]. In biological treatment systems, fluoroquinolones (FQs) are Norfloxacin prepare the ZnS:Mn nanocrystal and were purchased from Merck (Mumbai, India). The laboratory reagent grade drug NOFX (Table 1) was supplied by Sigma-Aldrich (Bangalore, India). The pH values of solutions were adjusted using an aqueous solution of HCl and NaOH (Merck, Mumbai, India). Drug solutions with various concentrations were made by dilution of the stock solution, using double distillate water. The nanoparticles morphology was studied using a JEOL-JEM 2100 transmission electron microscope (Cochin, India) and a Supra 55 Zeiss field-emission scanning electron microscope (Cochin, India). Fourier transform infrared (FTIR) spectra were obtained with Thermo Nicolet Avatar 370 (Cochin, India). The optical properties were studied using the absorbance spectrum recorded on a spectrophotometer Cary Win UV. The fluorescence spectrum was recorded using a JY Fluorolog-3-11 fluorescence spectrometer (Mumbai, India). N2 gas adsorption-desorption analysis was carried out using a Belsorp mini II (BEL Japan Inc, Osaka, Japan) at −196 °C (using liquid nitrogen). Surface areas were measured by the Brunauer-Emmett-Teller (BET) method, and the pore size distribution and volume using the Barrett-Joyner-Halenda (BJH) model. A systronic pH-meter was used for measuring the pH of sample solutions. For photocatalysis, the UV irradiations were carried out, using a mercury lamp of 40 W/m 2 (Osram, Munich, Germany) with emission at 254 nm wavelength. Mass spectrometry was performed by Agilent 1290 Infinity UHPLC system (Agilent Technologies, Santa Clara, CA, USA).

Synthesis of Mn:ZnS QDs
Mn:ZnS QDs were synthesized by the chemical precipitation method [41,42]. In brief, aqueous solutions of sodium sulphide, zinc acetate and manganese carbonate were prepared. 0.5 M solutions of Zn(CH3COO)2·H2O and Na2S were employed as precursors. Then, 29.75 mL of a 0.01 M MnCO3 solution were added to 49.50 mL of a solution of (Zn(CH3COO)2·H2O) for 1% Mn 2+ doping. After that, cetylpyridinium chloride (1.0 At.wt.%) was added as a capping agent. Then, the Na2S solution was added dropwise. A white precipitate appeared soon. The stirring continued for 15 min. The reaction was refluxed at 60 °C and then the solution was centrifuged at 5000 rpm for 4-5 min. The precipitate was then filtered through Whattman filter paper followed by washing to eliminate any adhered impurities.

QDs Based Photocatalytic Experiments for NOFX Degradation
The photocatalytic experiments were conducted using Mn:ZnS QDs to degrade NOFX in aqueous media. A stock solution of NOFX (100 ppm in water) was prepared for photodegradation. 319 The nanoparticles morphology was studied using a JEOL-JEM 2100 transmission electron microscope (Cochin, India) and a Supra 55 Zeiss field-emission scanning electron microscope (Cochin, India). Fourier transform infrared (FTIR) spectra were obtained with Thermo Nicolet Avatar 370 (Cochin, India). The optical properties were studied using the absorbance spectrum recorded on a spectrophotometer Cary Win UV. The fluorescence spectrum was recorded using a JY Fluorolog-3-11 fluorescence spectrometer (Mumbai, India). N 2 gas adsorption-desorption analysis was carried out using a Belsorp mini II (BEL Japan Inc, Osaka, Japan) at −196 • C (using liquid nitrogen). Surface areas were measured by the Brunauer-Emmett-Teller (BET) method, and the pore size distribution and volume using the Barrett-Joyner-Halenda (BJH) model. A systronic pH-meter was used for measuring the pH of sample solutions. For photocatalysis, the UV irradiations were carried out, using a mercury lamp of 40 W/m 2 (Osram, Munich, Germany) with emission at 254 nm wavelength. Mass spectrometry was performed by Agilent 1290 Infinity UHPLC system (Agilent Technologies, Santa Clara, CA, USA).

Synthesis of Mn:ZnS QDs
Mn:ZnS QDs were synthesized by the chemical precipitation method [41,42]. In brief, aqueous solutions of sodium sulphide, zinc acetate and manganese carbonate were prepared. 0.5 M solutions of Zn(CH 3 COO) 2 ·H 2 O and Na 2 S were employed as precursors. Then, 29.75 mL of a 0.01 M MnCO 3 solution were added to 49.50 mL of a solution of (Zn(CH 3 COO) 2 ·H 2 O) for 1% Mn 2+ doping. After that, cetylpyridinium chloride (1.0 At.wt.%) was added as a capping agent. Then, the Na 2 S solution was added dropwise. A white precipitate appeared soon. The stirring continued for 15 min. The reaction was refluxed at 60 • C and then the solution was centrifuged at 5000 rpm for 4-5 min. The precipitate was then filtered through Whattman filter paper followed by washing to eliminate any adhered impurities.

QDs Based Photocatalytic Experiments for NOFX Degradation
The photocatalytic experiments were conducted using Mn:ZnS QDs to degrade NOFX in aqueous media. A stock solution of NOFX (100 ppm in water) was prepared for photodegradation. In order to optimize the nanocatalyst amount for drug degradation, solutions of different concentrations were taken and their pH was adjusted for the required values. The reaction solutions were prepared by the addition of QDs into each conical containing drug solution. The conduct tests were carried out in a batch reactor at constant temperature. The reaction temperature was maintained at 29 ± 1 • C. A 40 W/m 2 mercury lamp (Osram) was employed as the ultraviolet (UV) light source (λ = 254 nm) during the degradation experiment. A suitable quantity of catalyst (0.01-0.08 g/L dose) was suspended into 25 mL of the NOFX solution with constant stirring. The solution was kept in the dark for 30 min before light illumination to accomplish adsorption-desorption equilibrium. After that, the lamp was switched on, and that moment was considered as "time zero" for the photocatalysis reaction study.
The solutions were irradiated by means of a UV lamp to provide energy. The distance between the solution and the UV light was set to 10 cm for the experiments. At defined time intervals, sample aliquots were taken from the solution, using a syringe, and the drug present was analyzed by spectrophotometry, after centrifugation. The decrease in absorbance (at λ max = 275 nm) for drug samples after irradiation, for a given time interval, displayed the degradation rate, and thus the efficiency of the drug destruction and photocatalytic activity of QDs.
The reactive species capture study was also done in parallel to the photocatalysis experiments. This study was executed by addition of 0.01 M of various scavengers, for example, formic acid (HCOOH), potassium iodide (NaN 3 ), sodium chloride (NaCl) and sodium azide (NaN 3 ) before adding the photocatalyst into the NOFX solution. The percentage (%) of degradation was calculated from the following equation: where C 0 is the initial NOFX concentration and C is the concentration of NOFX solution, at time t after the UV light exposure.

Characterization of QDs
After synthesis, the characterization of the Mn:ZnS QDs was accomplished by various techniques, to obtain information about the morphology of the prepared nanocatalysts. Figure 1a-d shows high resolution transmission electron microscopy (HRTEM) images of Mn:ZnS QDs. From the TEM micrographs, it is clearly observed that particles are nearly monodispersed with an average particle size of 6 nm.
The surface morphology of Mn:ZnS QDs samples was also studied using scanning electron microscopy (SEM). Figure 2 depicts the SEM images of the prepared nanocrystalline samples. The micrographs show that the synthesis method generates crystalline agglomerated nanoparticles of ZnS. The morphology reveals that as-synthesised Mn:ZnS QDs clusters are formed by prime building units of diverse orientations. Also there is a random aggregation between small particles, which leads to the development of irregular-shaped crystallites [43]. At lower magnification ( Figure 2a) the micrograph shows un-homogeneities regarding particle size distribution. The higher magnification image ( Figure 2b) clearly reveals that large particles are, in fact, agglomerates of the smaller sized particles.
The XRD diffractogram depicted in Figure 3 shows that as prepared Mn:ZnS nanoparticles are crystalline and pure. The nanocrystals have less lattice planes than the bulk, which causes broadening of the peaks attributed to small particle effect [44]. Pure zinc blended crystal structure with the three broad peaks corresponding to the (111), (220) and (311) planes with reflections at 2θ = 28.4 • , 48.3 • , and 59.3 • are observed. These results are in conformity with other experimental studies [45][46][47]. The surface morphology of Mn:ZnS QDs samples was also studied using scanning electron microscopy (SEM). Figure 2 depicts the SEM images of the prepared nanocrystalline samples. The micrographs show that the synthesis method generates crystalline agglomerated nanoparticles of ZnS. The morphology reveals that as-synthesised Mn:ZnS QDs clusters are formed by prime building units of diverse orientations. Also there is a random aggregation between small particles, which leads to the development of irregular-shaped crystallites [43]. At lower magnification ( Figure 2a) the micrograph shows un-homogeneities regarding particle size distribution. The higher magnification image ( Figure 2b) clearly reveals that large particles are, in fact, agglomerates of the smaller sized particles.   The surface morphology of Mn:ZnS QDs samples was also studied using scanning electron microscopy (SEM). Figure 2 depicts the SEM images of the prepared nanocrystalline samples. The micrographs show that the synthesis method generates crystalline agglomerated nanoparticles of ZnS. The morphology reveals that as-synthesised Mn:ZnS QDs clusters are formed by prime building units of diverse orientations. Also there is a random aggregation between small particles, which leads to the development of irregular-shaped crystallites [43]. At lower magnification ( Figure 2a) the micrograph shows un-homogeneities regarding particle size distribution. The higher magnification image ( Figure 2b) clearly reveals that large particles are, in fact, agglomerates of the smaller sized particles.  The energy dispersive X-ray analysis (EDS) revealed the elemental composition of the samples. Figure 4a shows the EDS of the average grains of Mn:ZnS QDs sample (Figure 4b). The analysis revealed the presence of 83.92 wt.% Zn, 13.32 wt.% S, and 2.77 wt.% Mn in the samples. Zn is present at 1.1, 8.7, and 9.6 keV, Mn at 0.5 and 6 keV, and S is present at 2.4 keV in the Figure 4b. Some more peaks are visible at 0.3, 1.6, and 3.1 keV, which are artificially (the so-called escape peaks) developed when the X-rays produced by fluorescence escapes the detector during analysis, as referred by the instrument supplier. The FTIR spectrum of Mn:ZnS QDs is shown in Figure 5. There are various features in the range of 500-4000 cm −1 associated with different functional groups [48,49]. The broad band at 3430 cm −1 is due to primary amine, N-H stretching. The bands at 2840 and 2930 cm −1 are due to a weak C-H stretching band. In the spectrum, the region between 1600-1300 cm −1 generally reveals the ring stretching vibrations. The absorption involves stretching and contraction of all the bonds in the ring and interaction between these stretching modes. Thus, the strong absorption peaks between 1401 cm −1 and 1581 cm −1 are due to aromatic C=C and C=N stretch in the ring. Bands corresponding to 1339 cm −1 indicate the presence of -CH 2 group. The peaks between 730-830 cm −1 are ascribed to C-H deforming vibration. Some other small peaks are also present in the spectrum, however not discussed here. Thus, the FTIR study strongly supports the formation of CPC capped Mn:ZnS QDs.
Nanomaterials 2020, 10, x FOR PEER REVIEW 6 of 26 The XRD diffractogram depicted in Figure 3 shows that as prepared Mn:ZnS nanoparticles are crystalline and pure. The nanocrystals have less lattice planes than the bulk, which causes broadening of the peaks attributed to small particle effect [44]. Pure zinc blended crystal structure with the three broad peaks corresponding to the (111), (220) and (311) planes with reflections at 2Ѳ = 28.4°, 48.3°, and 59.3° are observed. These results are in conformity with other experimental studies [45][46][47].   The XRD diffractogram depicted in Figure 3 shows that as prepared Mn:ZnS nanoparticles are crystalline and pure. The nanocrystals have less lattice planes than the bulk, which causes broadening of the peaks attributed to small particle effect [44]. Pure zinc blended crystal structure with the three broad peaks corresponding to the (111), (220) and (311) planes with reflections at 2Ѳ = 28.4°, 48.3°, and 59.3° are observed. These results are in conformity with other experimental studies [45][46][47]. The energy dispersive X-ray analysis (EDS) revealed the elemental composition of the samples.  The FTIR spectrum of Mn:ZnS QDs is shown in Figure 5. There are various features in the range of 500-4000 cm −1 associated with different functional groups [48,49]. The broad band at 3430 cm −1 is due to primary amine, N-H stretching. The bands at 2840 and 2930 cm −1 are due to a weak C-H stretching band. In the spectrum, the region between 1600-1300 cm −1 generally reveals the ring stretching vibrations. The absorption involves stretching and contraction of all the bonds in the ring and interaction between these stretching modes. Thus, the strong absorption peaks between 1401 cm −1 and 1581 cm −1 are due to aromatic C=C and C=N stretch in the ring. Bands corresponding to 1339 cm −1 indicate the presence of -CH2 group. The peaks between 730-830 cm −1 are ascribed to C-H a deforming vibration. Some other small peaks are also present in the spectrum, however not discussed here. Thus, the FTIR study strongly supports the formation of CPC capped Mn:ZnS QDs.  There is a yellow-orange emission at about 598 nm. The 4 T1-6 A1 transition in the 3d shell of Mn 2+ ions is the reason for this emission. It is due to the proficient transfer of energy from the ZnS to the doped Mn 2+ and is assisted by the mixed electronic states [50]. Whilst the Mn 2+ ion is incorporated in the lattice of ZnS, the cationic sites get substituted, and there occurs a mixing of s-p electrons of ZnS and the d electrons of doped Mn 2+ , making the 4 T1-6 A1 forbidden transition partly possible, which leads to the yellow-orange emission of the Mn 2+ ions.  There is a yellow-orange emission at about 598 nm. The 4 T 1 -6 A 1 transition in the 3d shell of Mn 2+ ions is the reason for this emission. It is due to the proficient transfer of energy from the ZnS to the doped Mn 2+ and is assisted by the mixed electronic states [50]. Whilst the Mn 2+ ion is incorporated in the lattice of ZnS, the cationic sites get substituted, and there occurs a mixing of s-p electrons of ZnS and the d electrons of doped Mn 2+ , making the 4 T 1 -6 A 1 forbidden transition partly possible, which leads to the yellow-orange emission of the Mn 2+ ions.  Figure 7a shows the ultraviolet-visible (UV-vis) spectra of pure ZnS and Mn:ZnS QDs. The absorption band of the QDs can be found between 250 to 290 nm, but in case of bulk ZnS, the band is observed near 350 nm with an energy-gap of 3.68 eV [51]. Figure 7b shows the band gap energy curve of pure ZnS and Mn:ZnS QDs calculated from the Tauc's relation [52]. The direct optical energy gap  The absorption band of the QDs can be found between 250 to 290 nm, but in case of bulk ZnS, the band is observed near 350 nm with an energy-gap of 3.68 eV [51]. Figure 7b shows the band gap energy curve of pure ZnS and Mn:ZnS QDs calculated from the Tauc's relation [52]. The direct optical energy gap value (E g ) obtained for pure ZnS is 3.88 and for Mn doped ZnS QDs it is found to be 4.12, 4.39, 4.6, and 4.5 for 0.5%, 1%, 3%, and 5%Mn doping. The observed increase in E g value, as well as the blue shift of the absorption spectra, might be caused by the decline in the size of the particles, due to the quantum size confinement [53,54]. A slight decrease in the E g value is found above 3% Mn doping which indicates that the particle size increases with a further increase in Mn concentration [55].  Figure 7a shows the ultraviolet-visible (UV-vis) spectra of pure ZnS and Mn:ZnS QDs. The absorption band of the QDs can be found between 250 to 290 nm, but in case of bulk ZnS, the band is observed near 350 nm with an energy-gap of 3.68 eV [51]. Figure 7b shows the band gap energy curve of pure ZnS and Mn:ZnS QDs calculated from the Tauc's relation [52]. The direct optical energy gap value (Eg) obtained for pure ZnS is 3.88 and for Mn doped ZnS QDs it is found to be 4.12, 4.39, 4.6, and 4.5 for 0.5%, 1%, 3%, and 5%Mn doping. The observed increase in Eg value, as well as the blue shift of the absorption spectra, might be caused by the decline in the size of the particles, due to the quantum size confinement [53,54]. A slight decrease in the Eg value is found above 3% Mn doping which indicates that the particle size increases with a further increase in Mn concentration [55].  The thermal decomposition, stability and temperature of phase formation study of Mn:ZnS QDs was carried out by thermal analyses. Differential thermal analysis (DTA) and thermogravimetric analysis (TGA) were conducted to evaluate the thermal behaviour of the complexes. Data was collected from room temperature up to 700 • C, with a heating rate of 10 • C/min. Figure 8a,b shows the TGA and DTA curves of Mn:ZnS QDs. The endothermic peak near 200 • C is due to the loss of physically adsorbed water. In the TGA plot, various stages of weight loss are observed. The first weight loss up to 250 • C (16.67%) is related to physically adsorbed water molecules. The second weight loss (5.95%), between 260 and 360 • C, is associated with the degradation of organic groups coming from the precursor particles. The third (3.97%) deals with the release of Mn ions, as well as decomposition of residual S ions from the sample. Curve A shows that the analysis started with 2.52 mg sample weight, and after heating to 600 • C, the sample weight was 1.85 mg. Thus, the weight loss percentage up to 700 • C was 26.5%. The DTA curve at Figure 8b shows an exothermic process up to 460 • C, which might be due to a change in crystallinity or a phase change in the material.
Nitrogen adsorption-desorption experiments at −196 • C were performed to confirm the porous structure of QDs. Figure 9a shows a typical type IV isotherm curve with an adsorption hysteresis loop and Figure 9b shows the pore size distribution. The surface area value of QDs was calculated using the BET equation and the value obtained was 10 m 2 /g. The sample displayed an extensive allocation of pore sizes with an average diameter of 5.7 nm (calculated from the BJH method) and the total pore volume was 0.05 cm 3 /gm. mg sample weight, and after heating to 600 °C, the sample weight was 1.85 mg. Thus, the weight loss percentage up to 700 °C was 26.5%. The DTA curve at Figure 8b shows an exothermic process up to 460 °C, which might be due to a change in crystallinity or a phase change in the material. Nitrogen adsorption-desorption experiments at −196 °C were performed to confirm the porous structure of QDs. Figure 9a shows a typical type IV isotherm curve with an adsorption hysteresis loop and Figure 9b shows the pore size distribution. The surface area value of QDs was calculated using the BET equation and the value obtained was 10 m 2 /g. The sample displayed an extensive allocation of pore sizes with an average diameter of 5.7 nm (calculated from the BJH method) and the total pore volume was 0.05 cm 3 /gm.

Photocatalytic Degradation of NOFX Using Mn:ZnSQDs
In order to investigate the photocatalytic behaviour of the synthesized Mn:ZnS QDs, a sequence of photocatalytic experiments for the degradation of drug NOFX was carried out under UV light radiation. The UV-vis absorption spectra of NOFX drug (15 mg/L) were recorded with wavelength of 200-400 nm as a function of illumination time (Figure 10a). From the absorption spectra, the absorbance of NOFX is gradually decreased with irradiation time. The effect of various process parameters, such as solution pH, catalyst dose and initial drug quantity on the degradation efficiency

Photocatalytic Degradation of NOFX Using Mn:ZnSQDs
In order to investigate the photocatalytic behaviour of the synthesized Mn:ZnS QDs, a sequence of photocatalytic experiments for the degradation of drug NOFX was carried out under UV light radiation. The UV-vis absorption spectra of NOFX drug (15 mg/L) were recorded with wavelength of 200-400 nm as a function of illumination time (Figure 10a). From the absorption spectra, the absorbance of NOFX is gradually decreased with irradiation time. The effect of various process parameters, such as solution pH, catalyst dose and initial drug quantity on the degradation efficiency of NOFX was assessed by varying pH (2-11), catalyst dose (20-90 mgs), maintaining the fixed drug concentration (15 mg/L). Figure 10a shows that about 86% NOFX (15 mg/L, pH 10) was decomposed in the presence of the photocatalyst Mn:ZnS QDs (60 mgs) after 60 min of UV light exposure. The decrease of absorption spectra and, hence, absorbance of samples at λ max = 275 nm indicates the degradation of NOFX drug in the applied situations. As a result, the decrease in the absorbance of samples due to decrease of drug concentration is traced for the measurement of degradation rate. The photocatalytic effect of Mn:ZnS and pure ZnS QDs on the degradation process of drug NOFX can be observed in the corresponding absorption spectra in the presence of UV light (Figure 10a,b) and sunlight (Figure 10c,d). Thus, NOFX could be well degraded with different light sources, viz., UV irradiation and sunlight. It was found that Mn:ZnS QDs exhibited excellent properties of photodegradation not only under UV irradiation but also under sunlight, which caused the NOFX to photodegrade.
In Figure 11, the evaluation of photodegradation of NOFX with concentration of 15.0 mg/L is shown for pure ZnS and Mn:ZnS QDs with sunlight, UV light and other conditions with catalyst dosage 60 mgs for 60 min. The photodegradation efficiency for NOFX obtained in different conditions followed the order:

Effect of the Initial pH of NOFX Solution
The pH of the solution plays a significant role in the photocatalytic aqueous oxidation of organic compounds, since the pH value can influence various properties of the photocatalyst, for example, charge of the catalyst, size of the catalyst particles and the positions of valence and conductance bands. To get acquainted with the pH effect, degradation experiments were performed at varying pH values (2.0-12.0) with 25 mL of 15 mg/L initial NOFX concentration and 60 mgs QDs, at room temperature, for 60 min. Figure 12 shows the effect of pH values on the drug degradation over time.
As expected, the photocatalytic degradation of NOFX occurred faster at basic pH, compared to lower values of pH (Figure 12), similar to earlier experiments with the same drug [56,57]. The photocatalytic degradation increased with pH increase, but maximal adsorption and degradation were obtained at pH 10.5-11. A higher value of pH lead to a lower level of adsorption and degradation of the drug. In fact, the surface charges of NOFX and Mn:ZnS catalyst are the main aspects behind this behaviour. For ZnS, the point of zero charge (pHzpc) value is 7-7.5, thus, the surface charge of the ZnS QDs is negatively charged above pH 7, whereas, it is positively charged at pH values below 7 [53]. NOFX Blank (experiment performed without light and QDs) < ZnS QDs < UV light (no QDs) < pure ZnS in sunlight < Mn:ZnS in sunlight < pure ZnS in UV light < Mn:ZnS in UV light.

Effect of the Initial pH of NOFX Solution
The pH of the solution plays a significant role in the photocatalytic aqueous oxidation of organic compounds, since the pH value can influence various properties of the photocatalyst, for example, charge of the catalyst, size of the catalyst particles and the positions of valence and conductance bands. To get acquainted with the pH effect, degradation experiments were performed at varying pH values (2.0-12.0) with 25 mL of 15 mg/L initial NOFX concentration and 60 mgs QDs, at room temperature, for 60 min. Figure 12 shows the effect of pH values on the drug degradation over time.

Effect of the Initial pH of NOFX Solution
The pH of the solution plays a significant role in the photocatalytic aqueous oxidation of organic compounds, since the pH value can influence various properties of the photocatalyst, for example, charge of the catalyst, size of the catalyst particles and the positions of valence and conductance bands. To get acquainted with the pH effect, degradation experiments were performed at varying pH values (2.0-12.0) with 25 mL of 15 mg/L initial NOFX concentration and 60 mgs QDs, at room temperature, for 60 min. Figure 12 shows the effect of pH values on the drug degradation over time.
As expected, the photocatalytic degradation of NOFX occurred faster at basic pH, compared to lower values of pH (Figure 12), similar to earlier experiments with the same drug [56,57]. The photocatalytic degradation increased with pH increase, but maximal adsorption and degradation were obtained at pH 10.5-11. A higher value of pH lead to a lower level of adsorption and degradation of the drug. In fact, the surface charges of NOFX and Mn:ZnS catalyst are the main aspects behind this behaviour. For ZnS, the point of zero charge (pHzpc) value is 7-7.5, thus, the surface charge of the ZnS QDs is negatively charged above pH 7, whereas, it is positively charged at pH values below 7 [53]. NOFX As expected, the photocatalytic degradation of NOFX occurred faster at basic pH, compared to lower values of pH (Figure 12), similar to earlier experiments with the same drug [56,57]. The photocatalytic degradation increased with pH increase, but maximal adsorption and degradation were obtained at pH 10.5-11. A higher value of pH lead to a lower level of adsorption and degradation of the drug. In fact, the surface charges of NOFX and Mn:ZnS catalyst are the main aspects behind this behaviour.
For ZnS, the point of zero charge (pH zpc ) value is 7-7.5, thus, the surface charge of the ZnS QDs is negatively charged above pH 7, whereas, it is positively charged at pH values below 7 [53]. NOFX has two ionizable functional groups: the 3-carboxyl group and N4 of piperazine moiety inducing two different ionization constants: pKa 1 (pH = 6.34), due to deprotonation from the carboxyl moiety; and pKa 2 (pH = 8.75), due to a protonation to N4 in the piperazinyl substituent. Thus, NOFX behaves as positively charged below pH 6.34, negatively above 8.75, and zwitterionic between these two pH values [58].
When the solution is acidic, NOFX and Mn:ZnS QDs are both managed by positive charge. The like charges show repulsive action, restricting the interaction of NOFX with the QDs surface, thus decreasing the rate of degradation. The attractive force between the deprotonated carboxyl moiety and the QDs forwards the degradation reaction [59]. Most competent and optimal NOFX degradation take place at the pH values lightly exceeding the pKa 2 , i.e., between 9.5-10.5. This may be attributable to a larger concentration of hydroxyl anions (OH − ), which are the source of hydroxyl radicals during photocatalysis. The higher the OH − ion concentration, the larger will be the generation of hydroxyl radicals (OH • ) [60]. Above this pH, degradation efficiency decreases, possibly due to the repulsion between negative charges of NOFX and ZnS QDs. Thus, pH 10 was selected as optimal pH value for further studies.

Effect of Catalyst Loading
The nanophotocatalyst dose is an important parameter in the photocatalytic degradation of pollutants as the amount of the catalyst directly controls the transformation rate. In the present study, the reactions were done by varying the catalyst amounts (ranging from 20 to 90 mgs) while keeping the drug concentration fixed at 15 mg/L. The degradation of NOFX increased from 41% to 84% as the catalyst amount increased from 20 to 60 mgs/25 mL, and decreased to 79% on further increasing the catalyst loading for 1 h reaction. The initial increase in NOFX degradation may possibly be due to an augmentation in the active sites accessibility as catalyst loading increased. However, a further addition of catalysts reduced light penetration (owing to light scattering from suspension), thus the volume of photoactive suspension decreased. The results of Figure 13 illustrate that 60 mgs/25 mL catalyst is the optimal value for maximal drug degradation. As a result, further experiments were made with this amount of catalyst loading. Nanomaterials 2020, 10, x FOR PEER REVIEW 13 of 26 has two ionizable functional groups: the 3-carboxyl group and N4 of piperazine moiety inducing two different ionization constants: pKa1 (pH = 6.34), due to deprotonation from the carboxyl moiety; and pKa2 (pH = 8.75), due to a protonation to N4 in the piperazinyl substituent. Thus, NOFX behaves as positively charged below pH 6.34, negatively above 8.75, and zwitterionic between these two pH values [58]. When the solution is acidic, NOFX and Mn:ZnS QDs are both managed by positive charge. The like charges show repulsive action, restricting the interaction of NOFX with the QDs surface, thus decreasing the rate of degradation. The attractive force between the deprotonated carboxyl moiety and the QDs forwards the degradation reaction [59]. Most competent and optimal NOFX degradation take place at the pH values lightly exceeding the pKa2, i.e., between 9.5-10.5. This may be attributable to a larger concentration of hydroxyl anions (OH − ), which are the source of hydroxyl radicals during photocatalysis. The higher the OH − ion concentration, the larger will be the generation of hydroxyl radicals (OH • ) [60]. Above this pH, degradation efficiency decreases, possibly due to the repulsion between negative charges of NOFX and ZnS QDs. Thus, pH 10 was selected as optimal pH value for further studies.

Effect of Catalyst Loading
The nanophotocatalyst dose is an important parameter in the photocatalytic degradation of pollutants as the amount of the catalyst directly controls the transformation rate. In the present study, the reactions were done by varying the catalyst amounts (ranging from 20 to 90 mgs) while keeping the drug concentration fixed at 15 mg/L. The degradation of NOFX increased from 41% to 84% as the catalyst amount increased from 20 to 60 mgs/25 mL, and decreased to 79% on further increasing the catalyst loading for 1 h reaction. The initial increase in NOFX degradation may possibly be due to an augmentation in the active sites accessibility as catalyst loading increased. However, a further addition of catalysts reduced light penetration (owing to light scattering from suspension), thus the volume of photoactive suspension decreased. The results of Figure 13 illustrate that 60 mgs/25 mL catalyst is the optimal value for maximal drug degradation. As a result, further experiments were made with this amount of catalyst loading.

Effect of the Initial Concentration of Drug
Treating the effluents present in the industrial and biological wastewater produced by natural and anthropogenic sources is a major challenge. Sometimes, industrial contaminants are chemically stable, and have inhibitory effects for biological treatment systems [61]. Thus, it becomes essential to

Effect of the Initial Concentration of Drug
Treating the effluents present in the industrial and biological wastewater produced by natural and anthropogenic sources is a major challenge. Sometimes, industrial contaminants are chemically stable, and have inhibitory effects for biological treatment systems [61]. Thus, it becomes essential to develop methods for the removal of contaminants at high concentrations from the wastewater prior to releasing them into the environment. Therefore, in the present method, the photodegradation was investigated at different concentrations, including 5, 10, 15, 20, and 25 mg/L with a fixed quantity of photocatalysts, as shown in Figure 14. It can be observed that the degradation rate of drug decreases with the increasing drug concentration, showing elevated degradation efficiency for a low initial concentration. Nanomaterials 2020, 10, x FOR PEER REVIEW 14 of 26 develop methods for the removal of contaminants at high concentrations from the wastewater prior to releasing them into the environment. Therefore, in the present method, the photodegradation was investigated at different concentrations, including 5, 10, 15, 20, and 25 mg/L with a fixed quantity of photocatalysts, as shown in Figure 14. It can be observed that the degradation rate of drug decreases with the increasing drug concentration, showing elevated degradation efficiency for a low initial concentration. This decline of efficiency with rising drug concentration is attributable to two reasons. As the initial amounts of drug increases, higher extent of drug molecules will be adsorbed over the surface of the QDs and the active sites will decrease. This leads to an increase in the occupied space of catalyst surface; resulting in reduced OH • radicals generation. Moreover, higher drug concentration causes less number of photons reaching the catalyst surface. Thus, most of the light is prevented by the adsorbed drug molecules and the photoexcitation of catalyst QDs declines, causing the slow degradation rate detected in the later part of the experiment [62].

Effect of Mn 2+ Dopant Concentration
In order to study the Mn 2+ doping effect on the photodegradation efficiency of ZnS QDs, experiments were carried out under optimal conditions with different dopant amounts of Mn (0.5, 1.0, 3.0, 5.0% w/w). A brief comparison between the obtained degradation efficiency of NOFX in the presence of undoped and Mn doped ZnS QDs ( Figure 15) indicates that the doping of Mn in the crystalline structure of ZnS, as an impurity, has a positive effect on the degradation efficiency through photocatalysis. The improvement found after doping compared to the undoped sample is 4.2%, which is close to the values found in literature 2-3% [21,23,63].
Nevertheless, a negative result in photocatalysis efficiency was observed for higher dopant concentrations. As seen in Figure 16, the photodegradation efficiencies of the QDs slightly increase from 0.0% to 1.0% and decline above 1% of the dopant concentration.
The changes observed upon the doping process might possibly be due to the variations in the crystallite size of the QDs, which may influence their photocatalytic performance [64]. Moreover, the dopants make the shallow trapping sites available for the charge carriers in the structure of the semiconductors. Consequently, the quantity and recombination rates of these charge carriers may vary by separating the arrival times of charge carriers at the surface [65,66]. At low dopant concentrations, Mn 2+ ions act for h + trapping only. However, at higher concentrations, the ions work as traps both for e − and h + , leading to their recombination by quantum tunneling [64,67,68]. This decline of efficiency with rising drug concentration is attributable to two reasons. As the initial amounts of drug increases, higher extent of drug molecules will be adsorbed over the surface of the QDs and the active sites will decrease. This leads to an increase in the occupied space of catalyst surface; resulting in reduced OH • radicals generation. Moreover, higher drug concentration causes less number of photons reaching the catalyst surface. Thus, most of the light is prevented by the adsorbed drug molecules and the photoexcitation of catalyst QDs declines, causing the slow degradation rate detected in the later part of the experiment [62].

Effect of Mn 2+ Dopant Concentration
In order to study the Mn 2+ doping effect on the photodegradation efficiency of ZnS QDs, experiments were carried out under optimal conditions with different dopant amounts of Mn (0.5, 1.0, 3.0, 5.0% w/w). A brief comparison between the obtained degradation efficiency of NOFX in the presence of undoped and Mn doped ZnS QDs (Figure 15) indicates that the doping of Mn in the crystalline structure of ZnS, as an impurity, has a positive effect on the degradation efficiency through photocatalysis. The improvement found after doping compared to the undoped sample is 4.2%, which is close to the values found in literature 2-3% [21,23,63].
Nevertheless, a negative result in photocatalysis efficiency was observed for higher dopant concentrations. As seen in Figure 16, the photodegradation efficiencies of the QDs slightly increase from 0.0% to 1.0% and decline above 1% of the dopant concentration.
The changes observed upon the doping process might possibly be due to the variations in the crystallite size of the QDs, which may influence their photocatalytic performance [64]. Moreover, the dopants make the shallow trapping sites available for the charge carriers in the structure of the semiconductors. Consequently, the quantity and recombination rates of these charge carriers may vary by separating the arrival times of charge carriers at the surface [65,66]. At low dopant concentrations, Mn 2+ ions act for h + trapping only. However, at higher concentrations, the ions work as traps both for e − and h + , leading to their recombination by quantum tunneling [64,67,68].

Kinetic Studies
The mechanism and the efficiency of the photodegradation of NOFX can be elucidated from the kinetic studies. They provide an indication for the effectiveness of the photocatalytic process. The studies were done at the optimal conditions for NOFX drug solution. The first order kinetic model was applicable and carried out using a linear fitting of ln C0/Ct versus t: where Co and Ct represent the concentration of NOFX at time 0 and time t, respectively, and k is the observed first order rate constant (min −1 ). The NOFX degradation rates under sunlight and UV light were obtained from the plot slopes of Figure 17a,b. The R 2 values show that the first-order model can be applied to the obtained experimental data. The values for the first-order kinetic data, together with rate constants (k), correlation coefficients (R 2 ) and degradation efficiency for Mn:ZnS QDs for different conditions of photocatalysis are given in Table 2. The photocatalytic activity of synthesized pure ZnS and Mn:ZnS QDs under UV light and natural sunlight can be assessed by comparing the apparent rate constants. Thus, it can be seen that the photodegradation efficiencies of pure ZnS and Mn:ZnS QDs as catalysts under UV light illumination are higher than under natural sunlight irradiation.

Kinetic Studies
The mechanism and the efficiency of the photodegradation of NOFX can be elucidated from the kinetic studies. They provide an indication for the effectiveness of the photocatalytic process. The studies were done at the optimal conditions for NOFX drug solution. The first order kinetic model was applicable and carried out using a linear fitting of ln C 0 /C t versus t: where C o and C t represent the concentration of NOFX at time 0 and time t, respectively, and k is the observed first order rate constant (min −1 ). The NOFX degradation rates under sunlight and UV light were obtained from the plot slopes of Figure 17a,b. The R 2 values show that the first-order model can be applied to the obtained experimental data. The values for the first-order kinetic data, together with rate constants (k), correlation coefficients (R 2 ) and degradation efficiency for Mn:ZnS QDs for different conditions of photocatalysis are given in Table 2. The photocatalytic activity of synthesized pure ZnS and Mn:ZnS QDs under UV light and natural sunlight can be assessed by comparing the apparent rate constants. Thus, it can be seen that the photodegradation efficiencies of pure ZnS and Mn:ZnS QDs as catalysts under UV light illumination are higher than under natural sunlight irradiation.

Probable Photocatalytic Degradation Mechanism of the Photocatalyst
The semiconductor photocatalyst can be excited when irradiated with photons of light equal or slightly higher than its band gap [63]. Thus, the possible mechanism for UV light assisted photodegradation of NOFX starts with the excitation of the semiconducting QDs, resulting in the formation of e − -h + pair at the QDs surface, which are the charge carriers. These e − and h + can either recombine or drift to the surface giving rise to the photo-active centres [69]. Actually, the overall number of charge carriers (e − and h + ) at the photocatalyst surface determines the efficiency of degradation.
The h + can indirectly or directly oxidize the organic matter (NOFX drug) due to its high oxidation potential. During indirect oxidation, the reactive hydroxide radicals (OH • ) are produced due to the combination of h + with H2O or with hydroxide anions [70], as shown in the following equations: h + + Drug → Oxidation of Drug,

Probable Photocatalytic Degradation Mechanism of the Photocatalyst
The semiconductor photocatalyst can be excited when irradiated with photons of light equal or slightly higher than its band gap [63]. Thus, the possible mechanism for UV light assisted photodegradation of NOFX starts with the excitation of the semiconducting QDs, resulting in the formation of e − -h + pair at the QDs surface, which are the charge carriers. These e − and h + can either recombine or drift to the surface giving rise to the photo-active centres [69]. Actually, the overall number of charge carriers (e − and h + ) at the photocatalyst surface determines the efficiency of degradation.
The h + can indirectly or directly oxidize the organic matter (NOFX drug) due to its high oxidation potential. During indirect oxidation, the reactive hydroxide radicals (OH • ) are produced due to the combination of h + with H 2 O or with hydroxide anions [70], as shown in the following equations: h + + Drug → Oxidation of Drug, This OH • is a strong oxidative (E• = +3.06 V) and non-selectively oxidizes drugs and other organic matter to mineral species partially or completely. Moreover, oxygen atoms as well as the doped metal at the surface work as a sink for e − enhancing the e − −h + separation. The conduction band e − at the surface of ZnS could reduce molecular oxygen (O 2 ) to superoxide anion (O 2 •− ). The O 2 •− subsequently reacts with H 2 O producing H 2 O 2 , which then generates OH • radicals [71].
Depending upon the precise experimental situation, the h + , e − , OH • , O 2 •− and O 2 itself play significant roles in the photodegradation mechanism [72]. Consequently, the OH • generated by e − in the conduction band, in addition to various other stages, can cause organic matter mineralization: In case of doping the catalyst with transition metal ions, the improvement of photocatalytic degradation is due to additional OH • and O 2 •− formation. Since doping provides a means to trap charge carriers (e − and h + ), extending their lifetimes, consequently, dopants increase the photocatalytic efficiency [73].

Role of Active Oxidation Species
The generation and functions of reactive species, like h + , O 2 •-, OH • and 1 O 2 for NOFX degradation was studied by adding 0.01 M of appropriate scavengers of these species. Due to divergence in the energy gaps and phase compositions, there may be variance observed in the functions of active species for different photocatalysts. KI is known to be an efficient quencher for h + and OH • s present at the QDs surface [74,75]. As illustrated in Figure 18, NaCl has been added as h + quencher, HCOOH for e − and NaN 3 for 1 O 2 and OH • quenching [75]. The scavengers were added prior to the addition of the photocatalyst. The highest NOFX degradation (86%) was observed in the absence of any scavenger. On the contrary, the hinderance of photodegradation efficiency was about 15%, 62% and 27% when HCOOH, NaCl and NaN 3 were used as scavengers substantiating the crucial role of e − and 1 O 2 in photocatalytic method. Also, the photodegradation efficiency turned down to 38% in the presence of KI, proving that the h + and OH • s also take part in the transformation of NOFX. This OH • is a strong oxidative (E• = +3.06 V) and non-selectively oxidizes drugs and other organic matter to mineral species partially or completely. Moreover, oxygen atoms as well as the doped metal at the surface work as a sink for e − enhancing the e − −h + separation. The conduction band e − at the surface of ZnS could reduce molecular oxygen (O2) to superoxide anion (O2 •− ). The O2 •− subsequently reacts with H2O producing H2O2, which then generates OH • radicals [71].
O2 •− + H2O → H2O2, H2O2 Depending upon the precise experimental situation, the h + , e − , OH • , O2 •− and O2 itself play significant roles in the photodegradation mechanism [72]. Consequently, the OH • generated by e − in the conduction band, in addition to various other stages, can cause organic matter mineralization: HO • + O2 •− + Drug → CO2 + H2O + small less toxic species, In case of doping the catalyst with transition metal ions, the improvement of photocatalytic degradation is due to additional OH • and O2 •− formation. Since doping provides a means to trap charge carriers (e − and h + ), extending their lifetimes, consequently, dopants increase the photocatalytic efficiency [73].

Role of Active Oxidation Species
The generation and functions of reactive species, like h + , O2 •─ , OH • and 1 O2 for NOFX degradation was studied by adding 0.01 M of appropriate scavengers of these species. Due to divergence in the energy gaps and phase compositions, there may be variance observed in the functions of active species for different photocatalysts. KI is known to be an efficient quencher for h + and OH • s present at the QDs surface [74,75]. As illustrated in Figure 18, NaCl has been added as h + quencher, HCOOH for e − and NaN3 for 1 O2 and OH • quenching [75]. The scavengers were added prior to the addition of the photocatalyst. The highest NOFX degradation (86%) was observed in the absence of any scavenger. On the contrary, the hinderance of photodegradation efficiency was about 15%, 62% and 27% when HCOOH, NaCl and NaN3 were used as scavengers substantiating the crucial role of e − and 1 O2 in photocatalytic method. Also, the photodegradation efficiency turned down to 38% in the presence of KI, proving that the h + and OH • s also take part in the transformation of NOFX.

Identification of Transformation Products
It is also important to be acquainted with the degradation products resulting from the Mn:ZnS QDs assisted photodegradation of NOFX, as some of the products may be more dangerous and unsafe to the environment. The possible degradation pathway of NOFX with Mn:ZnS QDs as photocatalyst, was conjectured by the results of mass spectrometry. The structures of the intermediates produced were tentatively recognized on the basis of the fragmentation patterns acquired from high resolution liquid chromatography mass spectrometry (HRLC MS) analysis and the existing information obtained from previous literature [76,77]. Primarily, the degradation initiates by the attack of radicals on piperazinyl and quinolone moieties. A total of 14 intermediates were identified in the degradation pathway described in Figure 19. The pathways for NOFX degradation were proposed based on the recognized intermediates.
In the current case, for pathway I, a dehydroxylation reaction takes place in NOFX molecule giving rise to structure 1 (m/z 304). In several cases, structure 1 further decomposes by losing a carbonyl group thereby producing its protonated form with m/z value 276 [78]. In second pathway, defluorination reaction occurs probably generating 2, which is the protonated form with m/z 302. Finally, the 2 transmits to 3 (m/z 230) by decarboxylation and deethylation reaction [79][80][81].
As discussed earlier, the piperazinyl moiety in NOFX is further a dynamic group for radical attack. Pathway III is chiefly the obliteration of the piperazinyl group. Six intermediary structures were recognized at this stage via oxidation, ring-opening and elimination reactions [78,82]. The protonated forms occur at m/z 350, 322, 294, 279, and 251 respectively. Initially, NOFX gets oxidized, resulting in opening of the piperazine ring, generating 4. Consequently, structure 4 loses its two -CO groups and is converted into 7 (through 5 or 6), which is similar to Guo's results [56]. Again, 7 gets oxidized, producing 8, which loses a -CO group and is transformed into 9 [83]. Ultimately, the piperazinyl moiety of NOFX is entirely destroyed. Thus, cleavage of piperazine ring played an important role in the photocatalytic transformation of NOFX, which is also manifested through the preceding literature [56,[83][84][85]. Pathway IV comprises the opening of quinolone substituent and the benzene moiety. On hydrolysis, the F in NOFX gets substituted with OH • group, which forms 10 [80]. Liu et al. specified that the OH • attacks the quinolone moieties in NOFX at the carbon-carbon double bond closest to the -COOH group [82]. Hence, the protonated products with m/z 350 (product 11), followed by 322, 294, and 276 (products 12, 13, and 14) are possibly expected to be generated. Thus, from the above discussions, NOFX could be decomposed into 3, 9, 13, and 14, which are easy to be mineralized further to small molecules like CO 2 , H 2 O, NO 3 − , and F − on account of their lower stability [79].
The prepared Mn:ZnS QDs powder materials exhibit excellent degradation efficiency in comparison to other photocatalysts, due to the larger number of charge carriers caused by the addition of Mn as an impurity, and the differences in the arrival time of e − and h + at the photocatalyst surface. Therefore, it was found that TiO 2 , ZnO and some other nanocomposites (often used for degradation) are less efficient in degrading NOFX. Until now, the photocatalytic degradation of NOFX  Figure 19. Probable photocatalytic degradation pathway of NOFX.
The prepared Mn:ZnS QDs powder materials exhibit excellent degradation efficiency in comparison to other photocatalysts, due to the larger number of charge carriers caused by the addition of Mn as an impurity, and the differences in the arrival time of e − and h + at the photocatalyst surface. Therefore, it was found that TiO2, ZnO and some other nanocomposites (often used for  Figure 20 shows the recyclability of the Mn:ZnS QDs powder photocatalyst for the degradation of NOFX. After every run, the QDs were separated from the drug solution by centrifugation, washed with distilled water and dried to study the catalysts recyclability. Afterwards, the dried photocatalyst was redistributed in fresh NOFX solution for the degradation experiments under optimized conditions. The degradation efficiency decreases from 86% to 65% after the 3rd repeated cycle of photocatalysis, which may be attributed to the loss of a small amount of catalyst after every run. and degraded 95% of 5 mg/L NOFX in 120 min with 0.03 gm of the nanocomposite [90]. Shah et al. employed the as-synthesised Bi 3+ -Fe 2+ co-doped ZnO for NOFX degradation and attained 80% removal of 10 mg/L NOFX in 120 min using 1 g/L catalyst [91]. Jin et al. used N-doped TiO2 for NOFX degradation where 69.79% degradation of 12.5 mg/L NOFX was obtained after 30 min of visible light irradiation with 0.4 g/L of the photocatalyst [92]. Figure 20 shows the recyclability of the Mn:ZnS QDs powder photocatalyst for the degradation of NOFX. After every run, the QDs were separated from the drug solution by centrifugation, washed with distilled water and dried to study the catalysts recyclability. Afterwards, the dried photocatalyst was redistributed in fresh NOFX solution for the degradation experiments under optimized conditions. The degradation efficiency decreases from 86% to 65% after the 3rd repeated cycle of photocatalysis, which may be attributed to the loss of a small amount of catalyst after every run.

Conclusions
In this study, Mn:ZnS QDs were prepared by a facile and rapid chemical precipitation method and the photocatalytic degradation of NOFX in the presence and absence of pure ZnS and Mn:ZnS QDs was investigated. In the photocatalytic degradation, the optimal parameters involved (substrate concentration, loading of catalyst, and solution pH) were identified. The synthesized Mn doped

Conclusions
In this study, Mn:ZnS QDs were prepared by a facile and rapid chemical precipitation method and the photocatalytic degradation of NOFX in the presence and absence of pure ZnS and Mn:ZnS QDs was investigated. In the photocatalytic degradation, the optimal parameters involved (substrate concentration, loading of catalyst, and solution pH) were identified. The synthesized Mn doped photocatalyst was much more efficient for the degradation of NOFX than the undoped material. This can be explained by the enhanced e − −h + separation at the hetero interface, by the production of highly reactive radicals and by an enlarged active surface area. The photocatalytic drug removal process followed first-order kinetics. Thus, Mn:ZnS QDs mediated the efficient degradation of NOFX, suggesting that the process is highly efficient, very simple, and can potentially be used for the remediation of organic pollutants from waste waters.