The existence of a humic substance in water causes the growth of microorganisms and reduces the quality of water; therefore, the removal of these materials is crucial. Here, the ZnO nanoparticles doped using transition metals, copper (Cu) and manganese (Mn), were used as an effective catalyst for photocatalytic removal of humic substances in an aqueous environment under ultraviolet, visible light, and light-emitting diode irradiations. Also, we study the effect of the sonocatalytic method. A solvothermal procedure is used for doping, and the Cu- and Mn-doped ZnO nanocatalyst were characterized by means of FTIR, XRD, AFM, SEM, and EDAX analyses. We investigate the effect of operational variables, including doping ratio, initial pH, catalyst dose, initial HS content, and illuminance on the removal efficiency of the processes. The findings of the analyses used for the characterization of the nanoparticles illustrate the appropriate synthesis of the Cu- and Mn-doped ZnO nanocatalysts. We observe the highest removal efficiency rate under acidic conditions and the process efficiency decreased with increasing solution pH, when we tested it in the range of 3–7. Photocatalytic decomposition of HS increases with a rise in catalyst dose, but an increase in initial HS content results in decreasing the removal efficiency. We observe the highest photocatalytic degradation of humic acid while using the visible light, and the highest removal efficiency is obtained using Cu.ZnO. The Cu.ZnO also shows better performance under ultraviolet irradiation compared to other agents.

1. Introduction

Degradation of plants and animals by microorganisms in water can mainly result in humic substances (HSs), which are the major part of natural organic matters (NOMs) [13]. These materials can decline the quality of drinking water as they cause color, taste, and odor [4]. Moreover, water treatment facilities can be influenced by HSs because they can lead to membrane fouling and the growth of microorganisms in distribution systems. However, the most important problem with the presence of HSs in water is the formation of disinfection byproducts (DBPs) as the water is chlorinated [5]. Two major compounds of DBPs are trihalomethanes (THMs) and haloacetic acids (HAAs) [6]; it has been documented that these compounds have carcinogenic and mutagenic properties [7]. Hence, it is of greatest importance to treat water containing HSs.

Several methods like the coagulation process [8], membrane technology [9], adsorption processes [10], and advanced oxidation processes (AOPs) have been employed to remove HSs from the aqueous solution. In AOPs, the hydroxyl radical of OH• as the strongest oxidizing agent is generated, which can degrade both organic and inorganic matters [11]. Recently, ultrasonic energy has been applied to generate the OH radicals to degrade refractory organic compounds. In aqueous solutions, ultrasonic irradiation can lead to producing cavitation bubbles because of acoustic cavitation. As a result, the produced bubbles generate severe heat and pressure in solution, called the “hot spots” phenomenon, because of which water molecules are pyrolyzed and OH• is generated [12, 13].

Photocatalytic methods have commonly been applied for the degradation of pollutants in water [14, 15]. The TiO2 and ZnO are two semiconductors, which have widely been used as a catalyst to decompose a huge number of resistant environmental contaminants in the presence of UV irradiation [16, 17]. In comparison with TiO2, the ZnO nanocatalyst has been introduced as a better photocatalyst because of its prominent advantages like wide bandgap, cheapness, high stability, and high adsorption capacity in UV irradiation [1821]. Although ZnO benefits from several plus factors, its photocatalytic activity is activated just under UV light (5 to 7% of solar energy), which makes it impossible to be used as the natural activation source [22]. In addition, another drawback to ZnO nanoparticles is a quick recombination of hole-electron pairs [23]. Therefore, in order to enhance the photocatalytic performance of ZnO nanoparticles, the mentioned problems should be solved. As a whole, irradiation via ultraviolet (UV) or visible light (VL) to the surface of semiconductors can trigger photocatalytic reactions, thereby exciting electrons from the valence band and transferring them to the conduction band [24]. As a result, the produced hole-electron (h/e) pair at the catalyst level can oxidize contaminant molecules through generating more OH•; this results in more oxidation and regeneration reactions [22].

Recently, the doping of the ZnO nanoparticles using transition metals like manganese (Mn), iron (Fe), copper (Cu), and so on has been introduced as a beneficial method [25]. It is worth noting that if a proper dopant is used, the bandgap energy of ZnO changes, thereby preventing the recombination of charge carriers. The doping of ZnO using a transition metal produces new electron levels; this makes it possible for ZnO to absorb visible light [26]. When ZnO is doped by a metal ion, the generated light electrons are trapped and penetrate to its structure, thereby increasing the photocatalytic performance of the doped ZnO nanoparticles. Chang et al. stated that the application of the Ce-doped ZnO photocatalyst could beneficially degrade dyes: direct blue 86, food black-2, and methyl orange under UV and visible light irradiation [27]. Also, the results reported by Subash et al. showed that the synthesized Ce codoped Ag–ZnO photocatalyst could effectively degrade Naphthol Blue Black (NBB) dye under natural sunlight illumination [28]. The application of ultrasonic irradiation generates microjets stemming from the collapse of cavitation bubbles in the solution; this causes the solution to be stirred well. Moreover, it can resolve the major downside of UV-light-based photocatalytic methods suffering from low penetration amount of UV light and shielding effects of nanoparticles [29].

Currently, there are a few research studies of copper-doped and manganese-doped ZnO nanocomposites for sonocatalytic and photocatalytic applications as well as HS decomposition by doped nanocatalysts in the aqueous environment. However, to the best of our knowledge, there are no reports on the sonocatalytic and photocatalytic decomposition of HS by manganese and copper doped ZnO nanocatalysts synthesized by the hydrothermal method. Therefore, in this study, two transition-metal ions, copper (Cu) and manganese (Mn), were selected because researchers have shown that copper is an inexpensive element that has physical and chemical properties similar to the properties of zinc. Therefore, due to the mismatch of the minimum size between zinc and copper, it is the best choice as an impurity for the realization of ZnO, which leads to the lowest formation energy. Also, due to its close size to zinc, it can be easily placed in the ZnO crystal lattice and change the microstructure and optical properties of ZnO. Also, due to its close size to zinc, it can be easily placed in the ZnO crystal lattice, altering the microstructure and optical properties of ZnO and showing a significant redshift in light absorption wavelength followed by an excellent catalytic activity [3032]. In the same way, it has been shown that the use of 3 d metal ions such as Mn with half-filled electronic configuration properties as dopants can increase the surface area and reduce the size of nanoparticles, including zinc oxide nanoparticles. This is why the use of Mn for ZnO doping is preferred because the d-manganese electron at the t2  level can easily overlap with the ZnO’s valence bond compared to other transition elements. In addition, manganese will not only act as a recombination center but also create more intermediate states. As a result, it shows a significant shift in the absorption and emission spectra to the visible light region [33, 34]. Therefore, according to the existing documents and the importance of the subject, this study was performed to synthesize zinc oxide by solvothermal method with the aim of improving its catalytic properties. Humic acids (HAs) as the target pollutant as well as an important chemical compound which is a pervasive substance in the environment, a natural refractory organic matter, and an important carcinogenic precursor in water supply was considered in this study and the efficiency of synthesized doped nanoparticles including ZnO, Cu.ZnO, Mn.ZnO, and Cu.Mn.ZnO in its catalytic degradation under ultraviolet irradiation, ultrasound radiation, LED, and visible light illumination was determined and evaluated. The effect of dopants concentration, solution pH, catalyst dosage, initial HAs concentration, and contact time on the degradation process of HAs and optical properties of nanoparticles was also investigated.

2. Materials and Methods

2.1. Chemicals

In the current research, the humic substance was purchased from Sigma-Aldrich Co. (Germany) and used as the model contaminant. The other materials used were of analytical grade and bought from Merck (Germany). Also, distilled water was applied for the preparation of synthetic solutions, as well as other experiments. Moreover, NaOH and H2SO4 were used to adjust the pH of the solutions.

2.2. Reactor

All the experiments were conducted by using a closed system, a 250 ml glassy reactor. Five 15 W UV lamps (Philips, Netherlands) were placed on the top part of the reactor to provide the UV region for the photocatalytic degradation runs. Meanwhile, to provide the visible region, natural sunlight (visible light (VL)) and light-emitting diode (LED) light (20-watt LED lamp) were applied as light sources. It should be noted that the visible light-based experiments were conducted in the peak hours of sunshine. Also, an Elema ultrasonic device (Germany) was utilized for the sonocatalytic process at 37 and 80 kHz frequency and 100% power. Furthermore, a magnetic stirrer was utilized in order to well mix the solution inside the reactor.

2.3. Photocatalyst Synthesis

In this study, a solvothermal procedure was exerted to dope the ZnO nanocatalysts with Cu and Mn. To prepare the undoped ZnO product, first, 119 g/l (0.4 M) hexahydrate zinc nitrate and 54.18 g/L (0.6 M) oxalic acid were dissolved separately in 100 ml deionized water and heated to the boiling point of the solutions. Next, the solution containing oxalic acid was added dropwise to the Zn (NO3) 2 solution. Then, the new solution was shaken and stirred well for 1 h, at 65°C; afterwards, it was cooled at room temperature. Then, the obtained homogeneous ZnO particles were washed a few times using distilled water; the mixture was then placed in an oven for 5 h (100°C) to dry it. In order to synthesize Cu-doped ZnO NPs and Mn-doped ZnO NPs (with a dopant concentration of 2%), 0.2 M Cu (CH3COO)2 and 0.24 M Mn (CH3COO)2·4H2O were added to the ZnO solution; in the next stage, oxalic acid was added, and the procedure for the synthesis was repeated like that for the undoped nanoparticles. To synthesize other percentages of the dopants: 1.5 and 2.5% for the two metals, 0.15 and 0.25 M Cu and 0.18 and 0.3 M Mn were applied according to the method explained above. And, for the synthesis of the codoped ZnO nanocatalyst, the aforementioned method was followed [28].

2.4. Characterization of Nanoparticles

In order to characterize the NPs synthesized in this study, scanning electron microscopy (SEM), X-ray diffraction (XRD), Fourier transform infrared (FTIR) spectroscopy, dynamic light scattering (DLS), atomic force microscopy (AFM), and zeta potential were used. To this end, a TESCAN microscope (model MIRA3, Czech Republic) was utilized to explain the shape and size of the ZnO NPs. In the present study, in order to obtain the information on the phase composition of the photocatalyst, especially the thin coating layer composited of ZnO, through an Inel instrument (EQUINOX 3000, France). Furthermore, a Bruker Tensor 27 instrument (Germany) was used for the FTIR spectroscopy of the synthesized NPs. And an AFM microscope (Advance model, Iran) was employed for the determination of the surface morphology of the NPs. Finally, the size of the NPs was determined via a DLS analyzer (NanoBrook model, USA).

2.5. Photocatalytic Experiments

The removal efficiency of the as-synthesized nanoparticles was examined by determining the degradation rate of humic acid. First, a 1,000 mg/L stock solution of humic acid was prepared by distilled water and then kept at 4°C. And the working solutions were made daily through diluting the stock solution in deionized water. In order to measure the content of humic acid before and after experiments, a UV-vis spectrophotometer was used at the maximum absorbance wavelength (λmax) of 254 nm. The number of samples was calculated according to the number of photocatalytic experiments, and the method of one factor at one time was used to optimize the parameters. The effect of the photocatalytic method on humic acid was measured in the presence of UV irradiation, sunlight, LED light, and ultrasound waves. Furthermore, the operating parameters: nanocatalyst type; dopant percentage, 1.5, 2, and 2.5%; initial humic acid content, 5, 10, 20, 30, 40, and 50 mg/L; pH value, 3, 5, 7, and 9; catalyst dosage, 0.4, 2, 4, 6, and 8 g/L; and reaction time, 15–180 min, were examined.

3. Results and Discussion

3.1. Cu.ZnO Nanoparticle Characterization

As previously mentioned, in the present study, the surface properties of the synthesized Cu.ZnO NPs were characterized by using the SEM analysis. Furthermore, Digimizer, which is an image analysis software, was used to determine the particle size distribution of the nanoparticles. Figure 1 shows the SEM image and particle size of the proposed photocatalyst. The SEM analysis shows a high and porous surface for the synthesized photocatalyst. As can be observed from the figure, the mean diameter of particle size distribution was 74.2 ± 21 nm. Therefore, it is illustrated that the synthesized nanoparticles had an approximately uniform spherical form with no agglomeration.

The chemical composition of the pure and Cu doped ZnO nanoparticles was performed using EDAX analysis and their results are displayed in Figure 2. The EDAX spectra of pure ZnO show Zn and O elements. The atomic ratio of Zn and O ions in the pure ZnO sample was 51.19 and 48.81 which is close to 1 : 1 ratio. In the 2% Cu-doped ZnO sample, the atomic concentrations of Cu, Zn, and O are 3.79, 76.59, and 19.62%, respectively. Therefore, EDAX analysis confirms the presence of Cu in the ZnO system and their weight percentage is approximately equal to their nominal stoichiometry under experimental conditions. These results also show that the zinc content in the undoped ZnO nanoparticles decreases simultaneously after doping with Cu, but the Cu content of Cu-doped ZnO increased significantly from 0 to 3.79 (wt%), indicating successful copper deposition in the structure of nanoparticles.

FTIR is a tool applied to attain information on the chemical bonding in a compound. Figure 3 presents the FTIR spectra of the synthesized nanoparticles. In all the samples studied, we observed broad absorption peaks at around 3700 and 1000 cm−1, which are attributed to normal polymeric O–H stretching vibration of H2O in Cu–Zn–O lattice [23], which may be because of moisture in solution and atmosphere. We also observed a sharp peak around 2750 cm1, which is ascribed to H–O–H bending vibration attributed to a small amount of H2O in the ZnO nanocrystals [25].

Figure 4 shows the XRD patterns of the synthesized nanoparticles. It has been reported that recrystallization and grain coarsening is formed because of the heat treatment process in amorphous materials. This phenomenon could lead to the emergence of peaks in the XRD pattern [35]. Apparently, the XRD patterns of all the synthesized nanoparticles: ZnO, Cu.ZnO, and Mn.ZnO had three major peaks: (100), (102), and (101), which are related to crystal planes (Figure 3). As can be seen, the three peaks accord with the pure ZnO nanoparticles’ peak (JCPDS stand card no. 800075), illustrating hexagonal crystal lattice. Furthermore, the patterns do not show an impurity phase, which accords with the two dopant metals. Nonetheless, the presence of the Cu and Mn leads to a shift of the three peaks because Zn2+ ions are substituted by these metals having larger effectual ionic radii and expansion of the lattice network.

Here, we applied the Dynamic light scattering as a physical method to determine the distribution of nanocatalyst particles in the solution and Figure 5(a) shows the results. We observed that the size of the most efficient synthesized nanoparticle is between 150 and 200 nm and also has a uniform distribution in this size range. In addition, the Zeta potential can be used as the main tool to study the electric charge at the interface of colloids. For this purpose, the zeta potential of the most efficient synthesized nanoparticle was also determined. Figure 5(b) shows that nanoparticle doping has increased the zeta potential compared to the undoped nanoparticle.

UV-vis spectra of the synthesized nanoparticles were performed to confirm the formation of ZnO NP and to compare the doped nanoparticles in terms of light absorption and its result is shown in Figure 6. As can be seen from this figure, a strong absorption band of about 371 nm can be seen, which confirms the formation of ZnO NPs. This sharp peak indicates that firstly, the particle size distribution is narrow and, secondly, the particle size is at the nanoscale [36, 37]. Zack et al. [37] obtained similar findings that confirm the formation of ZnO in this study. In the case of synthesized doped nanoparticles, it is also clear that all of them can effectively absorb light and develop the photocatalytic process under visible light. From these results, the absorption edge of Cu.ZnO and Mn.ZnO NPs are 390 and 383 nm, respectively, and it can be seen that the absorption peak is shifted to a longer wavelength. This slight redshift in the structure of Mn.ZnO and Cu.ZnO is due to the doping of Mn and Cu into the crystal lattice of Zn, which increases the absorption ability of the doped nanoparticles and then enhances better photoactivity. Comparing the data of UV-vis spectroscopy with the efficiency of different removal processes, as shown in Figure 6, it is clear that the photocatalytic efficiency of the doped nanoparticles is increased compared to pure ZnO, which indicates an improvement in visible light absorption due to the reduction of the ZnO bandgap.

The AFM analysis is applied to determine the size of NPs. This technique provides information regarding the roughness of ZnO NPs [38]. Roughness average, Ra, is the arithmetic average of the absolute values of the profile heights over the evaluation length. RMS roughness, Rq, is the root mean square average of the profile heights over the evaluation length. Here, we applied the AFM analysis to observe the shape of the ZnO NPs using tip-corrected AFM measurements (Figure 7). According to the results, the values of the Ra and Rq were 10.03 and 11.05 nm, respectively.

The effects of the different agents such as ZnO, Cu.ZnO, Mn.ZnO, and Mn.Cu.ZnO on the removal efficiency were investigated. Furthermore, we compared the removal efficiency of these agents with the process in which no catalyst was used. As Figure 8 shows, the highest efficiency is related to the Cu.ZnO catalyst in the presence of visible light, followed by UV irradiation. This shows the effect of visible light and UV on the synthesized catalyst for more production of hydroxyl radicals. The produced radicals can directly take part in the degradation of humic acid. In contrast, we observed the lowest efficiency in the case of lack of a catalyst in all the processes. In order to evaluate the effect of different nanocatalysts on the decomposition of HAs by using different catalytic processes, the results of this study are compared with other reported data and summarized in Table 1. This comparison shows that the metals-doped ZnO is an effective catalyst for the degradation of HAs compared to other photocatalysts.

3.2. Effect of Dopant Percentage and Irradiation Type Source

In the next step, we investigated the influences of ultrasonic, LED light, UV irradiation, and visible light on the removal of humic acid using the Cu.ZnO nanoparticles. It has been documented that, to enhance the performance of photocatalysts, semiconductors can be modified by a doping species (transitional metals). It is due to the fact that the optical response of the photocatalyst is shifted to higher wavelengths, which makes the photocatalyst active under visible irradiation. In this case, sunlight can be used as a cheap energy source for irradiation. In addition to optical absorption, some other characteristics of the photocatalyst like surface area, hydroxyl group density, adsorption/desorption, and so on can improve. It should be pointed out that the highest degradation rate of dyes happens at the optimum level of transition metals; this is because of the fact that the ions of copper deposit on the photocatalyst particles. As a result, oxygen vacancies are produced on the photocatalyst surface, thereby trapping the photogenerated electrons [47, 48]. On the other hand, when the content of dopant ions exceeds the optimum level, extra oxygen vacancies and Cu ions can recombine photoinduced electrons and holes; all this leads to decreasing the photocatalytic performance of the photocatalyst [47]. Moreover, when there are a higher number of dopants, extra ions of which deposit on the surface of photocatalyst particles instead of diffusing into photocatalyst lattice; this hinders the penetration of UV light and, in turn, active sites of the catalyst are blocked [48]. Of course, these changes depend on various factors, including the type of dopant and its concentration. In the case of manganese, it has been shown that, as the percentage of manganese increases, the particle size of ZnO nanoparticles also increases because the agglomeration of particles probably occurs. Therefore, at high concentrations of Mn, it is very difficult to incorporate into the crystal lattice of ZnO. Hence, it is recommended that the appropriate Mn concentration be accurately determined and that lower dopant concentration be used to create smaller particles and prevent particle aggregation [33].

Figure 9 shows the effect of the mentioned agents on the process efficiency. As can be seen, the visible light had the most effect on the photocatalysis of humic acid, and the highest removal efficiency was obtained using the ZnO doped by 2.5 and 2% Cu, respectively, in the presence of visible light. The single Cu.ZnO had the lowest performance under UV irradiation. We also observed the same trend for all the other activation agents, such as ultrasonic, LED, and visible light. Among the used activation agents, visible light had the highest effect on the process efficiency and provided more efficiency for the removal of humic acid. These differences in the effects of the used agents are associated with the absorbance edges of the prepared catalyst that can effectively activate the catalyst compared to the other agents. These results are consistent with the findings of previous studies. For example, Taufik et al. reported that ternary CuO/TiO2/ZnO nanocomposites offered a high performance (approximately 100%) under UV irradiation and visible light [49]. In general, in this study, the processes in which ultrasonic waves were utilized for the activation of the NPs had lower performance than the other methods. Geng et al. stated that the sole application of the ultrasonic irradiation process in contaminant removal needs long contact time and high energy consumption, which causes the performance to decline [50].

We have discussed and concluded that the synthesized Cu.ZnO nanoparticles showed the best performance in humic acid degradation. Next, the effects of various operational parameters such as solution pH, pollutant concentration, nanocatalyst dosage, and contact time on the process efficacy were investigated.

3.2.1. Effect of Solution pH

Figure 10(a) shows the influence of solution pH on performing the proposed process for the removal of HS at two different contact times. As observed, the highest removal efficiency was obtained under acidic conditions and the process efficiency decreased with increasing solution pH in the range of 3–7. We observed the lowest removal efficiency at pH values of 7 and 9.

The solution pH can affect photocatalyst removal efficiency by affecting the functional groups of humic acids and catalyst surface. Because humic acid contains both hydrophobic and hydrophilic functional groups, including carboxyl, phenolic hydroxyl, alcoholic hydroxyl, and carbonyl forms, under alkaline conditions, the adsorption of humic acid on the catalyst surface is very weak due to the high repulsion of carboxylate ions by negatively charged photocatalyst surface [51, 52].

In a previous study, it has been stated that the pHPZC of the ZnO NPs was 9.8, which makes its surface positively charged at pH values less than the PZC (acidic conditions) [53]. Thus, it is expected to attain a high catalytic performance for the photocatalytic degradation of humic acid. The results obtained in the current research are consistent with the findings reported by [54].

3.2.2. Humic Acid Concentration

Figure 10(b) demonstrates the effects of pollutant concentration on the photocatalytic removal of humic acid. As can be seen, the removal efficiency decreased with increasing the content of humic acid. We observed the highest removal efficiency at 5 mg/L of humic acid after 120 min of reaction time. Moreover, the lowest removal efficiency was obtained at 50 mg/L of the pollutant after 60 min of reaction, which shows that the high concentration of humic acid can obviously decrease the process efficiency. Each catalyst has a determined capacity for photocatalytic degradation of pollutant molecules on its surface; hence, a notable increase in the pollutant concentration can decrease their performance and efficiency [55].

3.2.3. Effect of Nanocatalyst Dosage

In the present study, we evaluated the effects of the nanocatalyst dosage on the photocatalysis of humic acid at different contact times (Figure 10(c)). We observed the lowest removal efficiency of humic acid at 0.4 g/L dosage of the ZnO nanoparticles. In contrast, we observed the highest removal efficiency of this organic matter in 8 g/L dosage of the proposed nanocatalyst. We conclude that a higher amount of nanocatalyst can increase the process capacity for the removal of a high concentration of humic acid.

3.2.4. Effect of Contact Time

Here, we have shown that increasing contact time from 60 to 120 min significantly improved the process performance for the removal and oxidation of humic acid during the proposed photocatalytic process. In addition, we separately evaluated the effect of different contact times on the process efficiency. Figure 10(d) shows the trends of performance changes of the proposed process by increasing contact time. As can be seen here, the efficiency of the proposed photocatalyst process continually increased with increasing contact time, which implied that we can achieve the desired performance for a high concentration of humic acid by using a high contact time. We can attribute this result to the effect of UV light during the proposed process that can further affect the catalyst surface by decreasing humic acid concentration during the reaction. We should point out that the findings obtained in this study are consistent with previous studies on the removal of various pollutants using photocatalytic processes [56, 57]. In agreement with our study, for example, Rashid Khan et al. stated that Cu-ZnO nanoparticle could reach a suitable performance in reactive red S3 B dye removal after a reaction time of 100 min and they concluded that the Cu-ZnO catalyst was entirely effective [58].

3.3. Mineralization of HAs

Regarding the HAs degradation, it is clear that the addition of dopants strongly enhances the degradation of HAs. In general, the photocatalytic oxidation process is based on the formation of reactive oxygen species (ROSs) including h+, •OH, and O2. ROS are very powerful oxidants that have the ability to degrade many organic compounds [59, 60]. Principally, if ZnO NPs are excited by exposure to an energy source such as visible light or ultraviolet light, h +VB and conduction band (CB) electron pairs are produced. Then, a set of reactions take place, resulting in the formation of the radicals of •OH and O2. The formed radicals can attack organic materials on the surface of ZnO [60, 61]. In fact, during the process, there are three distinct pathways for HA degradation, which generally include oxidation by hydroxyl radicals, reduction by superoxide radicals, and adsorption by the catalyst [60]. As a result, organic materials are degraded and final products including H2O and CO2 are produced. Of course, due to the incomplete mineralization process, it will usually be possible to produce intermediate products. Therefore, it was claimed that the reaction between HA and reactive oxygen species could produce carboxylic acids with low molecular weights such as oxalic, succinic, formic, acetic, and malonic acids [59, 60]. It should be noted that doping can help produce more OH radicals, therefore, leading to higher degradation efficiency of organic pollutants. This is because Cu and Mn act as electron scavengers and prevent the recombination of electron-hole pairs [61].

4. Conclusion

The characterization tests illustrated that the synthesized Cu.ZnO nanoparticles were well-crystalline and benefited from suitable optical properties. Also, we found out that the photocatalytic performance of the Cu.ZnO nanoparticles was better than that of the ZnO nanoparticles. The degradation rate raised with enhancing the concentration of Cu doping up to 2.5%. The photocatalytic processes exhibited better performance in HS removal than the sonocatalytic processes. And, among all methods examined in the current research, Cu.ZnO, Mn.ZnO, and Mn.Cu.ZnO in the presence of VL irradiation had the highest removal performance. In conclusion, Cu.ZnO nanoparticles under VL irradiation can be applied as an efficient nanocatalyst for the removal of humic substances.

Data Availability

The data used to support the findings of this study are included within the article.

Conflicts of Interest

The authors declare that they have no conflicts of interest.


The research reported in this publication was supported by Elite Researcher Grant Committee (Award no. 982747) from the National Institutes for Medical Research Development (NIMAD), Tehran, Iran.