Next Article in Journal
One-Pot Preparation of Layered Double Hydroxide-Engineered Boric Acid Root and Application in Wastewater
Next Article in Special Issue
Enhancing Performance of Organic Pollutant Degradation via Building Heterojunctions with ZnO Nanowires and Na Doped Conjugated 2,4,6-Triaminopyrimidin-g-C3N4
Previous Article in Journal
Surface Functionalization of Bamboo via Photo-Grafting Tannic Acid for Enhanced Silver Ion Loading Properties
Previous Article in Special Issue
Effect of Ag Modification on the Structure and Photocatalytic Performance of TiO2/Muscovite Composites
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Molecules
Volume 29
Issue 13
10.3390/molecules29133202
molecules-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

High-Efficiency Photo-Fenton-like Catalyst of FeOOH/g-C3N4 for the Degradation of PNP: Characterization, Catalytic Performance and Mechanism Exploration

by
Rongjun Su
1,*,
Junhao Wang
1,
Hao Jiang
1,
Lan Wei
1,
Deying Mu
1 and
Chunyan Yang
2,*
1
School of Food Engineering, Harbin University of Commerce, Harbin 150076, China
2
College of Architecture and Environment, Institute of New Energy and Low-Carbon Technology, Sichuan University, Chengdu 610207, China
*
Authors to whom correspondence should be addressed.
Molecules 2024, 29(13), 3202; https://doi.org/10.3390/molecules29133202
Submission received: 28 May 2024 / Revised: 21 June 2024 / Accepted: 27 June 2024 / Published: 5 July 2024
(This article belongs to the Special Issue Heterogeneous Catalysis in Environmental Application)
Browse Figures
Review Reports Versions Notes

Abstract

:
The composite photocatalyst FeOOH/g-C3N4 was prepared through thermal polycondensation and co-precipitation methods, followed by XRD, SEM and UV-vis characterization. The stability of FeOOH/g-C3N4 was explored by the recycling test. The active species in the reaction system were investigated by the capture experiment. The results indicated that the optimal preparation condition for g-C3N4 involved calcination at 600 °C for 4 h. XRD analysis revealed that g-C3N4 exhibits a high-purity phase, and Fe in FeOOH/g-C3N4 exists in a highly dispersed amorphous state. SEM analysis showed that FeOOH/g-C3N4 has a rough surface with an irregular layered structure. Element composition analysis confirmed that the content of elements in the prepared catalyst is consistent with the theoretical calculation. FeOOH/g-C3N4 possesses the largest specific surface area of 143.2 m2/g and a suitable pore distribution. UV-vis DRS analysis showed that the absorption intensity of FeOOH/g-C3N4 is stronger than that of g-C3N4. When the catalyst dosage was 1.0 g/L, the H2O2 dosage was 4 mmol/L, the PNP initial concentration was 10 mg/L and the initial pH value was 5, the PNP removal could reach 92% in 120 min. Even after 5 cycles, the efficiency of PNP removal by FeOOH/g-C3N4 remains nearly 80%. The capture experiment indicated that both •OH and •O2− play roles in the photocatalytic degradation of PNP, with •OH being more significant. These findings affirm that FeOOH has been successfully incorporated into g-C3N4, resulting in a conspicuous catalytic effect on the degradation of PNP in the visible light-assisted Fenton-like reaction.

1. Introduction

Advanced oxidation processes (AOPs) have valuable practical applications because of their strong mineralization ability, fast reaction speed, easy operation and simple process and equipment [1]. What is more, Fenton-like advanced oxidation processes have been widely used due to their advantages of high natural abundance, cost-effectiveness, low toxicity and environmental friendliness [2,3,4,5]. This process has been proven to be efficient in the degradation of organics with iron-based multiphase catalysts such as Fe3O4 and α-FeOOH in wastewater [6,7]. Among them, hydroxyl iron oxide (FeOOH) has the advantages of stable chemical properties, high specific surface area, wide pH range and controllable iron solution, which has been reported in many studies [8,9,10,11,12].
Traditional semiconductor photocatalysts, such as TiO2- [13,14] and ZnO-based [15,16] catalytic materials, have high photocatalytic activity. However, they have a low utilization ratio of sunlight in the reaction process because they had wide band gaps and can only respond to UV energy, which is less than 5% of the total energy of sunlight. As a metal-free semiconductor with a layered structure, g-C3N4 has a band gap of about 2.7 eV and a strong visible light-absorption capacity [17]. Since its discovery in 2009, g-C3N4 has gradually become a research hotspot [18]. However, g-C3N4 has a narrow band gap and photogenerated electron–hole pairs are easy to recombine, which limits its application in the field of photocatalysis [19,20]. Introducing element doping [21,22] and heterojunction construction [23,24] can make the catalyst structure form defects, which can act as a trap for photogenerated electrons and promote the separation of photoexcited carriers [25]. Simultaneously, impurity energy levels can be generated in the energy gap to change the band gap structure of semiconductor materials, so as to improve the redox ability of the valence band (VB) and conduction band (CB), making the band gap structure more suitable for photocatalytic reaction [26,27]. FeOOH, with the advantages of a narrow band gap and a broad visible absorption region, has been used for coupling with other semiconductors for applications such as direct photocatalytic degradation of organic matter [28]. In addition, the band gap of amorphous FeOOH is much smaller than that of the corresponding crystalline materials, which results in a broader visible absorption region and excellent photocatalytic performance [29]. However, there are few reports on amorphous FeOOH as a photocatalyst modifier.
P-nitrophenol (PNP) usually exists in sewage, natural water bodies and soil. It can enter the human body through oral, respiratory and skin contact. Additionally, PNP has the potential to accumulate in animal and human bodies through the food chain. PNP structure is relatively stable and widely used as a raw chemical material, such as medicine, dyes and pesticides [30]. Due to the presence of nitro in its molecular structure, it is difficult to biodegrade in nature, so it is extremely stable in the environment [31]. Prolonged exposure to drinking water contaminated with PNP may lead to adverse health effects, including dizziness, memory loss and neurological diseases [32]. Therefore, it is very important to remove PNP from water by efficient and cost-effective means. Many researchers have focused on the development of novel catalysts with high degradation efficiency for PNP.
Based on the above research basis, FeOOH/g-C3N4 composite visible light catalyst was prepared by thermal polycondensation and co-precipitation method in this project. With PNP in water as the main target pollutant, the photo-assisted Fenton oxidation system was established to study the visible light catalytic performance, and the mechanism of FeOOH/g-C3N4 visible light catalytic on the degradation of PNP was discussed.

2. Experimental

2.1. Materials

All reagents used in the experiment are analytically pure, including urea, ferric chloride hexahydrate, ammonium bicarbonate, anhydrous ethanol, sodium hydroxide, hydrochloric acid (Xilong Scientific Co., Ltd., Shantou, China), 30% hydrogen peroxide (Tianjin Continental Chemical Reagent Factory, Tianjin, China), etc.

2.2. Preparation of FeOOH/g-C3N4

Preparation of g-C3N4: 10 g of urea was put into a crucible, which was then fully covered and wrapped with aluminum foil. Subsequently, the crucible was placed in a muffle furnace. The initial temperature was set at 20 °C. The crucible was heated to different preset temperatures and was maintained at each temperature for 4 h, and then cooled to room temperature.
The preparation of FeOOH/g-C3N4: 0.3 g of g-C3N4 was taken into 40 mL anhydrous ethanol, and subjected to ultrasonic treatment (Type KQ5200B ultrasonic cleaner, Kunshan ultrasonic instrument Co., Ltd., Shanghai, China) for 1 h. Subsequently, 0.39 g of FeCl3·6H2O was added with ultrasonic treatment for 10 min. Following this, 0.343 g of NH4HCO3 was added, and then the mixture underwent magnetic stirring for 8 h. The resulting mixture was subjected to centrifugal washing three times and then dried at 50 °C. The resulting catalyst is denoted as x-FeOOH/g-C3N4 (x represents the mass fraction of FeOOH). As a control, pure FeOOH without g-C3N4 was synthesized in the same procedure.

2.3. Characterization

Phase analysis of the catalyst was carried out by X-ray diffraction (XRD, D/Max-RB). The micromorphology of the catalyst was analyzed by scanning electron microscope (SEM, Sigma 500, Sigma America, Ronkonkoma, NY, USA). The X-ray energy dispersive spectrometer (EDS) was used to analyze the composition of elements in the micro-structure of catalysts. The Brunauer–Emmett–Teller method (BET, ASAP2460, Micromeritics, Norcross, GA, USA) was used to analyze the specific surface area and pore distribution of the catalysts. Ultraviolet-visible diffuse reflection spectroscopy (UV–Vis DRS, Lambda 950, PerkinElmer, Waltham, MA, USA) was applied to probe the optical performance of the catalysts.

2.4. Experimental Procedures

The reaction device used in the photocatalytic degradation experiment is shown in Figure 1. The optimization of single photocatalyst preparation conditions was achieved by assessing RhB removal. A 0.25 g amount of photocatalysts and 250 mL of RhB solution (10 mg/L) were placed in a photocatalytic reactor and stirred for 30 min under dark conditions to reach an equilibrium of adsorption and desorption. Then, a 500 W xenon lamp (type GXH500 long arc xenon lamp, Shanghai Jiguang Special Lighting electric appliance factory, Shanghai, China) was turned on to radiate the reaction system. Samples of the reaction solution (2–3 mL) were taken out every 30 min, and the clear solution was filtered out through a 0.22 µm membrane. The optimization of composite catalyst-preparation conditions was conducted using PNP as the target pollutant, and the effects of different degradation processes were analyzed using the same method as described above. In addition, 3 mmol/L H2O2 was added immediately after the light source was turned on to construct the photo-Fenton system, and the concentration of the PNP in the reaction solution was determined at 400 nm at different time intervals.
After the photocatalytic degradation experiment was completed, the remaining reaction liquid was centrifuged in a centrifugal tube to separate solids, washed with deionized water and anhydrous ethanol, and dried for later use. The recovered catalyst was reused in the photocatalytic degradation experiment.

2.5. Analytical Methods

UV-vis (Type 722N visible spectrophotometer, Shanghai Yuanxi Instrument Co., Ltd., Shanghai, China) was used to determine the concentration of target pollutants in the reaction solution, and the RhB maximum absorption wavelength of 554 nm.
Isopropanol (IPA), ethylenediamine tetraacetic acid disodium (EDTA-2Na) and p-benzoquinone (BQ) were selected as the capture agents of •OH, h+ and•O2−, respectively. The experimental procedure was the same as in Section 2.4. After the system reached the adsorption and desorption equilibrium, a certain amount of the aforementioned trapping agent is added into the system to continue the photocatalytic degradation experiment.

3. Results and Discussion

3.1. Evaluation of FeOOH/g-C3N4 Catalytic Performance in Different Preparation Conditions

Figure 2a shows the effect of calcination temperature on the photocatalytic degradation of RhB by g-C3N4. The results show that the degradation rate of RhB was about 95% when the calcination temperature was 600 °C. This result is because the C/N ratio of g-C3N4 increases with the increase in temperature, and the band gap decreases according to other references [33,34]. Generally, the narrower the band gap, the larger the corresponding light absorption range. But an excessively narrow band gap may facilitate the recombination of photogenerated electron–hole pairs, resulting in low light quantum utilization and a weakened redox capacity. The catalyst prepared at 600 °C may combine these two effects to achieve the most suitable catalytic performance. Therefore, 600 °C was chosen as the optimal calcination temperature.
As shown in Figure 2b, the degradation efficiency of RhB was about 95% when the calcination time was 4 h. This phenomenon can be attributed to the increase in the specific surface area and pore volume of g-C3N4 with prolonged calcination time [35]. However, once the calcination time surpasses a certain threshold, the structure tends to stabilize, leading to no significant alteration in the photocatalytic capability of g-C3N4. Therefore, 4 h was chosen as the optimal calcination time.
The FeOOH/g-C3N4 photocatalyst prepared with different mass fractions of FeOOH was used in photocatalytic degradation of PNP for 120 min. The total removal was calculated and the dark adsorption curve was plotted with the results illustrated in Figure 3a,b. Figure 3a shows that the prepared 0.3FeOOH/g-C3N4 composite photocatalyst has the highest efficiency in PNP degradation, achieving a degradation rate of approximately 82% under visible light for 120 min. This may be because a mass fraction of 0.3FeOOH is the ideal doping amount, resulting in the optimal specific surface area and pore size, thereby enhancing photocatalytic efficacy. Figure 3b shows that all three photocatalysts can reach adsorption equilibrium after a dark reaction for 30 min. Notably, the 0.3FeOOH/g-C3N4 photocatalyst exhibits the highest adsorption capacity for PNP, with an adsorption ratio of 7.6% after 30 min. This heightened adsorption is likely due to its high specific surface area. In the photocatalytic system, catalysts with large specific surface areas can adsorb more target pollutants, which is conducive to the subsequent photocatalytic reaction. Thus, FeOOH doping enhances the PNP degradation rate of g-C3N4, and 0.3FeOOH/g-C3N4 demonstrates superior photocatalytic performance. Therefore, the 0.3FeOOH/g-C3N4 composite photocatalyst was used in subsequent photocatalytic performance tests and the influence of experimental parameters was assessed.
In conclusion, the optimal preparation conditions of g-C3N4 were calcination at 600 °C for 4 h. Similarly, for the FeOOH/g-C3N4 composite photocatalyst, the optimal conditions were determined by adding FeOOH with a mass fraction of 0.3.

3.2. Characterizations of FeOOH/g-C3N4

3.2.1. Crystal Structure Analysis

XRD was used to characterize the crystal structure of the catalysis. As shown in Figure 4, there are two distinct characteristic peaks located at 12.8° and 27.2°, which belong to the (100) and (002) surfaces of g-C3N4, respectively, indicating that g-C3N4 has a high purity phase (JCPDS No. 87-1526). There is no obvious FeOOH diffraction peak in the figure for FeOOH/g-C3N4 and FeOOH, which may be due to the synthesized FeOOH being amorphous.
EDS analysis was performed on the sample of the 0.3FeOOH/g-C3N4 photocatalyst, and the results are shown in Figure 5. The results show that the prepared catalyst contains 41.9% N, 30.9% C, 15.2% O and 7.0% Fe, which is consistent with the theoretical calculation results.

3.2.2. Microtopography Analysis

Figure 6 displays the SEM microscopic morphology analysis results. The sample of g-C3N4 presents an irregular layered structure, which corresponds to the traditional two-dimensional layered structure of g-C3N4. The nanosheets in g-C3N4 have a smooth surface, while the FeOOH/g-C3N4 composite photocatalyst has a rough surface. This can be attributed to the generation of granular FeOOH during the co-precipitation process, which uniformly adheres to the surface of g-C3N4. This phenomenon contributes to an increase in the specific surface area, enhancing the number of active sites on the catalyst surface.

3.2.3. Analysis of Specific Surface Area and Aperture Structure

Brunauer–Emmett–Teller (BET) and Barrett–Joyner–Halenda (BJH) methods were used to analyze the specific surface area and pore distribution of the prepared photocatalysts, respectively, with the results shown in Figure 7. As can be seen from Figure 7a, N2 adsorption–desorption isotherms of g-C3N4 and FeOOH/g-C3N4 samples are consistent with the hysteresis characteristic curves of mesoporous materials with a type IV isotherm and a type H3 adsorption hysteresis loop in the high P/P0 range. This aligns with the pore size distribution curve in Figure 7b, indicating a mesoporous structure in the catalysts. This indicates that the introduction of FeOOH has no significant effect on pore structure. BET model analysis showed that the specific surface areas of FeOOH, g-C3N4 and FeOOH/g-C3N4 were 62.5, 96.9 and 143.2 m2/g, respectively. The composite catalyst demonstrated a substantial increase in specific surface area compared to individual FeOOH and g-C3N4. According to the BJH model, the average pore sizes of FeOOH, g-C3N4 and FeOOH/g-C3N4 were 3.406, 3.053 and 3.823 nm, respectively, with corresponding pore volumes of 0.086, 0.214 and 0.849 cm3/g. Higher specific surface area enhances adsorption capacity, while a rich pore structure exposes more active sites, thereby improving catalytic activity. In summary, FeOOH/g-C3N4 with its largest specific surface area and suitable pore distribution combines the advantages of the two single catalysts, exhibiting significant photocatalytic potential.

3.2.4. Optical Property Analysis

The optical properties of the prepared FeOOH/g-C3N4 photocatalyst were analyzed by UV-Vis DRS. As shown in Figure 8a, both g-C3N4 and FeOOH/g-C3N4 can absorb visible light. The absorption edge of pure g-C3N4 is about 430 nm, while that of FeOOH/g-C3N4 is extended to about 480 nm, which means it red-shifted and has a wide range; thus, the absorption intensity is strengthened. This indicates that the prepared FeOOH/g-C3N4 photocatalyst demonstrates efficient utilization of visible light. For semiconductor materials, the band gap (Eg) is calculated as αhν = A(hν − Eg)n/2, where α is the absorption coefficient, h is Planck’s constant, ν is the optical frequency, and A is a constant. n value is determined by the type of semiconductor leap. Since g-C3N4 is an indirect semiconductor, n is taken as 4, while FeOOH is a direct semiconductor, so n is 1. Figure 8b,c display band gaps of 2.53 eV and 1.90 eV for g-C3N4 and FeOOH, respectively. The charge transportation between the FeOOH/g-C3N4 heterojunction follows a Z-scheme according to references [36,37]. Hence, electron–hole (e−-h+) pairs were generated on the surface of FeOOH and g-C3N4 photocatalysts under visible light irradiation. Briefly, the electrons are excited into the CB while the holes remain in the VB. Due to the formation of a heterojunction, the FeOOH holes migrate downward. Conversely, the electrons of g-C3N4 will migrate to the more positively charged CB of FeOOH. As a result, the electrons gather on the CB of FeOOH and the holes gather on the VB of g-C3N4 for the purpose of photogenerated charge separation.

3.3. Catalytic Performance of Different Degradation Processes

The degradation effects of PNP under different degradation processes were analyzed and measured, as shown in Figure 9. As can be seen from the figure, the removal of PNP by light alone is only about 10%, because the structure of PNP is stable under visible light and is difficult to degrade through this process. The addition of H2O2 to this system enhances the removal of PNP to approximately 43%, indicating that H2O2 has a certain oxidation effect, but cannot reach the ideal efficiency, because the amount of •OH generated by H2O2 decomposition under light is still small, thus the oxidation effect on PNP is limited. Based on light, H2O2 and FeOOH/g-C3N4, the removal of PNP sharply rises to about 82%, indicating that most organic matter can be rapidly oxidized and decomposed. This indicates that FeOOH/g-C3N4 has an obvious effect on PNP degradation in the photo-Fenton-like reaction system. The catalytic performance of FeOOH/g-C3N4 under visible light, combined with the strong oxidation of the Fenton system, achieves an ideal synergistic effect in PNP degradation.

3.4. Effect of Reaction Conditions on the Decomposition of PNP

3.4.1. Effect of H2O2 Dosage

A 1.0 g/L FeOOH/g-C3N4 photocatalyst was placed into a 250 mL PNP solution with a concentration of 10 mg/L. The system underwent dark adsorption for 30 min until the adsorption equilibrium was reached, and then different concentrations of H2O2 (2 mmol/L, 3 mmol/L, 4 mmol/L, 5 mmol/L) were added. The influence of catalyst dosage on PNP degradation was studied under simulated visible light radiation for 120 min. The degradation curve is shown in Figure 10a. The pseudo-first-order reaction kinetics was fitted, with the results shown in Figure 10b and Table 1.
As shown in Figure 10a, the degradation rate of PNP in the reaction increases with the increase in H2O2 dosage. However, when the concentration increases above 4 mmol/L, the PNP removal exhibits marginal improvement, which is mainly because excessive H2O2 will capture •OH instead and increase side reactions in the system. As a result, the utilization rate of •OH in the system is reduced, which affects the effect of PNP removal. Thus, the optimal concentration is identified as 4 mmol/L. Figure 10b and Table 1 show that the photocatalytic reaction rate enhanced with the increase in H2O2 dosage, and the pseudo-first-order reaction rate constant is the maximum and remains nearly the same at 4 mmol/L and 5 mmol/L. Therefore, the optimal dosage of 4 mmol/L is selected for further study on the influence of photocatalytic parameters.

3.4.2. Effect of Catalyst Dosage

The influence of catalyst dosage on PNP degradation was studied with various dosages of FeOOH/g-C3N4 catalyst (0.6 g/L, 0.8 g/L, 1.0 g/L and 1.2 g/L), and other conditions were the same as in Section 3.4.1. The degradation curves are shown in Figure 11a. The quasi-first-order reaction kinetics was fitted, and the results are shown in Figure 11b and Table 2.
As shown in Figure 11a, when the dosage of the catalyst increased from 0.6 g/L to 1.0 g/L, the degradation rate of PNP also increased. This is mainly attributed to the enlarged number of active sites on the catalyst surface and the increased concentration of Fe3+. For the constant amount of pollutants, the enhanced catalyst dosage leads to more significant participation of PNP in catalytic oxidation reactions, consequently improving its degradation rate. However, when the dosage of the catalyst continues to increase to 1.2 g/L, the removal rate decreases. The reason is that the excessive catalyst amount could lead to a decrease in light transmittance in the reaction system, thus resulting in insufficient light intensity and inhibitory effects on the photocatalytic effect. When the dosage is 1.0 g/L, the degradation rate of PNP is up to 91% after 120 min. Figure 11b and Table 2 show that a higher dosage of catalyst results in an increased photocatalytic reaction rate with the maximum quasi-first-order reaction rate constant at 1.0 g/L. Therefore, the optimal FeOOH/g-C3N4 dosage of 1.0 g/L is selected to proceed with the subsequent investigation of the influence of photocatalytic parameters.

3.4.3. Effect of Initial pH Value

NaOH and HCl solution were used to adjust the initial pH value of the reaction system to 3, 5, 7, 9, and other conditions were the same as in Section 3.4.1. The influence of the initial pH value on the degradation of PNP was studied. Figure 12a illustrates the degradation curves. The quasi-first-order reaction kinetics was fitted, and the results are shown in Figure 12b and Table 3.
In Figure 12a, the initial pH value greatly affects the PNP removal, showing a gradual decrease with rising pH value. This indicates that the system has better catalytic activity in an acidic environment, which is the same as the conclusion of other studies in the general heterogeneous Fenton system. Under acidic conditions, Fe3+ can participate in the reaction in the form of ions without facile hydrolysis, increasing the utilization rate of •OH in the system, thus improving the PNP removal. In addition, under acidic conditions, H+ can promote the decomposition of H2O2 to produce •OH, which improves the ability of catalytic oxidation of organic pollutants. Conversely, under alkaline conditions, Fe3+ is prone to hydrolysis, resulting in a decrease in catalytic activity, and H2O2 easily loses its activity in alkaline conditions, which reduces the generation of •OH and inhibits the effective degradation of PNP. In addition, it can be seen from the figure that when the pH value is 3 and 5, the final PNP removal is relatively close, which can reach more than 92%. Given the cost-effectiveness and proximity to typical water pH, the optimal pH value of 5 is selected for this experiment. As shown in Figure 12b and Table 3, different initial pH values in reaction systems exhibit a consistent trend in influencing the photocatalytic reaction rate.

3.4.4. Effect of PNP Initial Concentration

The concentration of PNP solution was different (5 mg/L, 10 mg/L, 15 mg/L and 20 mg/L), and other conditions were the same as in Section 3.4.1. The effect of the initial concentration of target substance PNP on its degradation was studied. The degradation curve is illustrated in Figure 13a. The quasi-first-order reaction kinetics was fitted, and the results are shown in Figure 13b and Table 4. As shown in Figure 13a, the total degradation rate decreases with the increase in the initial concentration of PNP. When the concentration of PNP is 5 mg/L, the removal is close to 98% at 120 min, but when the concentration increases to 20 mg/L, the removal rate is only about 63% at 120 min. This is because in high concentrations of PNP, more intermediate products are produced in the photocatalytic reaction process, and these substances will also react with •OH. At the same time, when the dosage of the catalyst is fixed, the number of active sites provided and the number of active groups that can participate in the photocatalytic reaction are limited, which also limits the number of PNP molecules that can participate in the photocatalytic reaction. Therefore, when the concentration of PNP increases, the limited catalyst cannot provide enough reaction sites, and the overall degradation rate will decrease correspondingly. Figure 13b and Table 4 further demonstrate that the photocatalytic reaction rate also decreases with the gradual increase in the initial concentration of PNP.

3.4.5. Stability of FeOOH/g-C3N4

The FeOOH/g-C3N4 involved in the photocatalytic reaction was centrifuged, washed, recovered and dried, and its visible light catalytic performance for PNP was tested again to evaluate its recycling performance. As shown in Figure 14, the degradation rate of PNP by FeOOH/g-C3N4 was nearly 80% even when it was reused five times, which indicates that the FeOOH/g-C3N4 photocatalyst prepared in this paper has better recycling performance and good stability.

3.5. Identification of Active Species in the Photo-Fenton-like Process

In the process of photocatalytic degradation, three active substances, namely •OH, h+ and •O2−, typically play crucial roles. In this paper, isopropyl alcohol (IPA), EDTA-2Na and p-benzoquinone (BQ) were selected as the capture agents of •OH, h+ and •O2−, respectively. The effect of PNP degradation in each capture experiment was compared with a system without adding a capture agent. The results are illustrated in Figure 15. The degradation rate of PNP is 92% when there is no trapping agent in the system. When the capture agent EDTA-2Na was added to the system, the degradation rate of PNP was unchanged, indicating that there is no significant role of h+ in the photocatalytic system. The degradation rate of PNP decreased significantly with the addition of IPA and BQ, and the inhibition effect of IPA was greater. Therefore, the capture experiment showed that both •OH and •O2− in the FeOOH/g-C3N4 photo-Fenton-like system played roles in PNP degradation, with •OH having a more significant impact.

3.6. Comparison with Other Results about Modification of g-C3N4

The comparison of photocatalytic efficiency of other modified g-C3N4 is shown in Table 5. It can be seen that g-C3N4 is commonly modified by non-metals, metals and their oxides. The catalyst used in this experiment has a great advantage in time and degradation rate.

4. Conclusions

In summary, FeOOH/g-C3N4 was successfully prepared by thermal polycondensation and coprecipitation, serving as a highly effective heterogeneous Fenton photocatalyst for the removal of PNP from water. The optimum preparation conditions were obtained as follows: g-C3N4 calcined at 600 °C for 4 h, with a mass fraction of FeOOH of 0.3. Single-factor experiments were conducted to establish the optimal process conditions for PNP degradation: H2O2 dosage of 4 mmol/L, catalyst dosage of 1 g/L, PNP initial concentration of 10 mg/L and pH value of 5. Under these conditions, the degradation efficiency of PNP by FeOOH/g-C3N4 reaches 92% within 120 min. Characterization techniques including SEM, XRD and UV-vis proved that FeOOH was successfully loaded on the surface of g-C3N4 without affecting the crystal structure of g-C3N4. After five cycles of photocatalytic degradation of PNP by FeOOH/g-C3N4, the degradation efficiency remained nearly 80%, which proves that the FeOOH/g-C3N4 photocatalyst prepared in this paper has good recycling and stability. Moreover, capture experiments revealed that both •OH and •O2− play roles in the photocatalytic degradation of PNP by FeOOH/g-C3N4, while •OH plays a more significant role.

Author Contributions

Conceptualization, D.M.; Methodology, J.W.; Software, J.W.; Validation, L.W.; Investigation, J.W. and D.M.; Data curation, H.J.; Writing—original draft, J.W.; Writing—review & editing, R.S., H.J. and C.Y.; Supervision, R.S. and C.Y.; Funding acquisition, R.S. All authors have read and agreed to the published version of the manuscript.

Funding

This work was financially supported by the National Natural Science Foundation (52370174) and High-tech Venture Capital Co., Ltd. of Hefei, China (No. HSDHX202110181).

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

The data presented in this study are available in article.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Ding, Z.; Zhang, H. Research and application of advanced oxidation technology in refractory organic wastewater. Chem. Adhes. 2010, 32, 72–75. [Google Scholar]
  2. Raha, S.; Ahmaruzzaman, M. Facile fabrication of g-C3N4 supported Fe3O4 nanoparticles/ZnO nanorods: A superlative visible light responsive architecture for express degradation of pantoprazole. Chem. Eng. J. 2020, 387, 123766. [Google Scholar] [CrossRef]
  3. Zapata, A.; Malato, S.; Sanchez-Perez, J.A.; Oller, I.; Maldonado, M.I. Scale-up strategy for a combined solar photo-Fenton/biological system for remediation of pesticide-contaminated water. Catal. Today 2010, 151, 100–106. [Google Scholar] [CrossRef]
  4. De Torres-Socias, E.; Prieto-Rodriguez, L.; Zapata, A.; Fernandez-Calderero, I.; Oller, I.; Malato, S. Detailed treatment line for a specific landfill leachate remediation. Brief economic assessment. Chem. Eng. J. 2015, 261, 60–66. [Google Scholar] [CrossRef]
  5. Silva, T.F.; Fonseca, A.; Saraiva, I.; Boaventura, R.A.; Vilar, V.J. Scale-up and cost analysis of a photo-Fenton system for sanitary landfill leachate treatment. Chem. Eng. J. 2016, 283, 76–88. [Google Scholar] [CrossRef]
  6. Lin, Z.; Zhao, L.; Dong, Y.; Xu, J. Degradation of PCB28 by hydrogen peroxide catalyzed by goebite. Acta Sci. Circumstafica Sin. 2011, 31, 2043–2048. [Google Scholar]
  7. Qian, X.; Wu, Y.; Kan, M.; Fang, M.; Yue, D.; Zeng, J.; Zhao, Y. FeOOH quantum dots coupled g-C3N4 for visible light driving photo- Fenton degradation of organic pollutants. Appl. Catal. B Environ. 2018, 237, 513–520. [Google Scholar] [CrossRef]
  8. Xu, J.; Li, Y.; Yuan, B.; Cui, H.; Fu, M. Degradation of dichlofenac sodium by visible light catalyzed by α-FeOOH and H2O2. Environ. Sci. 2015, 36, 2122–2128. [Google Scholar]
  9. Huang, Z.; Han, F.; Li, M.; Zhou, Z.; Guan, X.; Guo, L. Which phase of iron oxyhydroxides (FeOOH) is more competent in overall water splitting as a photocatalyst, goethite, akaganeite or lepidocrocite? A DFT-based investigation. Comput. Mater. Sci. 2019, 169, 109110. [Google Scholar] [CrossRef]
  10. Wang, C.; Li, A.; Shuang, C. The effect on ozone catalytic performance of prepared-FeOOH by different precursors. J. Environ. Manag. 2018, 228, 158–164. [Google Scholar] [CrossRef]
  11. Wu, P.; Zhou, C.; Li, Y.; Zhang, M.; Tao, P.; Liu, Q.; Cui, W. Flower-like FeOOH hybridized with carbon quantum dots for efficient photo-Fenton degradation of organic pollutants. Appl. Surf. Sci. 2021, 540, 148362, (prepublish). [Google Scholar] [CrossRef]
  12. Guo, L.; Zhang, K.; Han, X.; Zhao, Q.; Wang, D.; Fu, F.; Liang, Y. Highly efficient visible-light-driven photo-Fenton catalytic performance over FeOOH/Bi2WO6 composite for organic pollutant degradation. J. Alloys Compd. 2020, 816, 152560. [Google Scholar] [CrossRef]
  13. Zhang, Y.; Pang, S.; Yu, L.; Liu, L. Research progress of photocatalytic degradation of phenol by modified TiO2. Environ. Dev. 2020, 32, 112–113. [Google Scholar]
  14. Sim, L.C.; Koh, K.S.; Leong, K.H.; Chin, Y.H.; Abd Aziz, A.; Saravanan, P. In situ growth of g-C3N4 on TiO2 nanotube arrays: Construction of heterostructures for improved photocatalysis properties. J. Environ. Chem. Eng. 2020, 8, 103611. [Google Scholar] [CrossRef]
  15. Tan, C.; Li, Y.; Liu, H.; Li, J.; Xia, Z.; Zuo, J.; Zhao, L. AgBr/ZnO composite photocatalyst and Its photocatalytic performance. J. Chin. Ceram. Soc. 2021, 49, 202–210. [Google Scholar]
  16. Ravichandran, K.; Kalpana, K.; Uma, R.; Sindhuja, E. Cost-effective fabrication of ZnO/g-C3N4 composite film coated stainless steel meshes for visible light responsive photocatalysis. Mater. Res. Bull. 2018, 99, 268–280. [Google Scholar] [CrossRef]
  17. Mamba, G.; Mishra, A.K. Graphitic carbon nitride (g-C3N4) nanocomposites: A new and exciting generation of visible light driven photocatalysts for environmental pollution remediation. Appl. Catal. B Environ. 2016, 198, 347–377. [Google Scholar] [CrossRef]
  18. Wang, X.; Maeda, K.; Thomas, A.; Takanabe, K.; Xin, G.; Carlsson, J.M.; Domen, K.; Antonietti, M. A metal-free polymeric photocatalyst for hydrogen production from water under visible light. Nat. Mater. 2009, 8, 76–80. [Google Scholar] [CrossRef] [PubMed]
  19. Ismael, M. A review on graphitic carbon nitride (g-C3N4) based nanocomposites: Synthesis, categories, and their application in photocatalysis. J. Alloys Compd. 2020, 846, 156446. [Google Scholar] [CrossRef]
  20. Ma, T.; Shen, Q.; Zhao, B.; Xue, J.; Guan, R.; Liu, X.; Jia, H.; Xu, B. Facile synthesis of Fe-doped g-C3N4 for enhanced visible-light photocatalytic activity. Inorg. Chem. Commun. 2019, 107, 107451. [Google Scholar] [CrossRef]
  21. Patnaik, S.; Dipti, P.S.; Parida, K. Recent advances in anion doped g-C3N4 photocatalysts: A review. Carbon 2021, 172, 682–711. [Google Scholar] [CrossRef]
  22. Liu, S.; Zhu, H.; Yao, W.; Chen, K.; Chen, D. One step synthesis of P-doped g-C3N4 with the enhanced visible light photocatalytic activity. Appl. Surf. Sci. 2018, 430, 309–315. [Google Scholar] [CrossRef]
  23. Chen, X.; Hu, T.; Zhang, J.; Yang, C.; Dai, K.; Pam, C. Diethylenetriamine synergistic boosting photocatalytic performance with porous g-C3N4/CdS-diethylenetriamine 2D/2D S-scheme heterojunction. J. Alloys Compd. 2021, 863, 158068. [Google Scholar] [CrossRef]
  24. She, X.; Wu, J.; Xu, H.; Zhong, J.; Wang, Y.; Song, Y.; Nie, K.; Liu, Y.; Yang, Y. High efficiency photocatalytic water splitting using 2D alpha- Fe2O3/g-C3N4 Z-scheme catalysts. Adv. Energy Mater. 2017, 7, 1700025. [Google Scholar] [CrossRef]
  25. Sun, S.; Liang, S. Recent advances in functional mesoporous graphitic carbon nitride (mpg-C3N4) polymers. Nanoscale 2017, 9, 10544–10578. [Google Scholar] [CrossRef] [PubMed]
  26. Jiang, L.; Yuan, X.; Pan, Y.; Liang, J.; Zeng, G.; Wu, Z.; Wang, H. Doping of graphitic carbon nitride for photocatalysis: A review. Appl. Catal. B Environ. 2017, 217, 388–406. [Google Scholar] [CrossRef]
  27. Hu, J.; Zhang, P.; An, W.; Liu, L.; Liang, Y.; Wang, H. In-situ Fe-doped g-C3N4 heterogeneous catalyst via photocatalysis-Fenton reaction with enriched photocatalytic performance for removal of complex wastewater. Appl. Catal. B Environ. 2019, 245, 130–142. [Google Scholar] [CrossRef]
  28. Luo, J.; Lin, P.; Zheng, P.; Zhou, X.; Ning, X.; Zhan, L.; Wu, Z.; Liu, X.; Zhou, X. In suit constructing S-scheme FeOOH/MgIn2S4 heterojunction with boosted interfacial charge separation and redox activity for efficiently eliminating antibiotic pollutant. Chemosphere 2022, 298, 134297. [Google Scholar] [CrossRef] [PubMed]
  29. Zhang, Y.; Shi, L.; Geng, Z.; Ren, T.; Yang, Z. The improvement of photocatalysis O2 production over BiVO4 with amorphous FeOOH shell modification. Sci. Rep. 2019, 9, 19090. [Google Scholar] [CrossRef]
  30. Yehia, F.Z.; Eshaq, G.; Elmetwally, A.E. Enhancement of the working pH range for degradation of p-nitrophenol using Fe2+-aspartate and Fe2+-glutamate complexes as modified Fenton reagents. Egypt. J. Pet. 2016, 25, 239–245. [Google Scholar] [CrossRef]
  31. Xu, R. Research progress of catalytic degradation of p-nitrophenol in water. Guangdong Chem. Ind. 2019, 46, 64–65+75. [Google Scholar]
  32. Bekena, F.T.; Abdullah, H.; Kuo, D.H.; Zeleke, M.A. Photocatalytic reduction of 4-nitrophenol using effective hole scavenger over novel Mg-doped Zn(O,S) nanoparticles. J. Ind. Eng. Chem. 2019, 78, 116–124. [Google Scholar] [CrossRef]
  33. Xiao, H.; Wang, W.; Liu, G.; Chen, Z.; Lv, K.; Zhu, J. Photocatalytic performances of g-C3N4 based catalysts for RhB degradation: Effect of preparation conditions. Appl. Surf. Sci. 2015, 358, 313–318. [Google Scholar] [CrossRef]
  34. Ismael, M. The photocatalytic performance of the ZnO/g-C3N4 composite photocatalyst toward degradation of organic pollutants and its inactivity toward hydrogen evolution: The influence of light irradiation and charge transfer. Chem. Phys. Lett. 2020, 739, 136992. [Google Scholar] [CrossRef]
  35. Wang, Y.; Wang, H.; Chen, F.; Cao, F.; Zhao, X.; Meng, S.; Cui, Y. Facile synthesis of oxygen doped carbon nitride hollow microsphere for photocatalysis. Appl. Catal. B Environ. 2017, 206, 417–425. [Google Scholar] [CrossRef]
  36. Wu, X.; Zhao, Q.; Guo, F.; Xia, G.; Tan, X.; Lv, H.; Feng, Z.; Wu, W.; Zheng, J.; Wu, M. Porous g-C3N4 and α-FeOOH bridged by carbon dots as synergetic visible-light-driven photo-fenton catalysts for contaminated water remediation. Carbon 2021, 183, 628–640. [Google Scholar] [CrossRef]
  37. Sun, Y.; Wang, Y.; Chen, Y.; Qian, J.; Chen, F.; Zhou, Z.; Han, C.; Shi, Y.; Lu, X.; Ni, C. In-situ construction of 1D β-FeOOH nanobelts/2D porous g-C3N4 heterojunction for enhanced “signal-on” photoelectrochemical aptasensing. J. Alloys Compd. 2024, 990, 174383. [Google Scholar] [CrossRef]
  38. Wang, Q.; Xu, P.; Zhang, G.; Hu, L.; Wang, P. Visible-light responsive g-C3N4 coupled with ZnS nanoparticles via a rapid microwave route: Characterization and enhanced photocatalytic activity. Appl. Surf. Sci. 2019, 488, 360–369. [Google Scholar] [CrossRef]
  39. Yan, S.; Li, Z.; Zou, Z. Photodegradation Performance of g-C3N4 Fabricated by Directly Heating Melamine. Langmuir 2009, 25, 10397–10401. [Google Scholar] [CrossRef]
  40. Dong, F.; Wang, Z.; Sun, Y.; Ho, W.K.; Zhang, H. Engineering the nanoarchitecture and texture of polymeric carbon nitride semiconductor for enhanced visible light photocatalytic activity. J. Colloid Interface Sci. 2013, 401, 70–79. [Google Scholar] [CrossRef]
  41. Xiao, D.; Dai, K.; Qu, Y.; Yin, Y.; Chen, H. Hydrothermal synthesis of α-Fe2O3/g-C3N4 composite and its efficient photocatalytic reduction of Cr(VI) under visible light. Appl. Surf. Sci. 2015, 358, 181–187. [Google Scholar] [CrossRef]
  42. Zhang, B.; Wang, Q.; Zhuang, J.; Guan, S.; Li, B. Molten salt assisted in-situ synthesis of TiO2/g-C3N4 composites with enhanced visible-light-driven photocatalytic activity and adsorption ability. J. Photochem. Photobiol. A Chem. 2018, 362, 1–13. [Google Scholar] [CrossRef]
Molecules 29 03202 g001
Figure 1. Equipment: (a) picture of real products and (b) schematic diagram.
Figure 1. Equipment: (a) picture of real products and (b) schematic diagram.
Molecules 29 03202 g001
Molecules 29 03202 g002
Figure 2. Effect of (a) calcination temperature and (b) calcination time on photocatalytic degradation of RhB by g-C3N4.
Figure 2. Effect of (a) calcination temperature and (b) calcination time on photocatalytic degradation of RhB by g-C3N4.
Molecules 29 03202 g002
Molecules 29 03202 g003
Figure 3. Effect of FeOOH mass fraction on photocatalytic degradation of PNP by FeOOH/g-C3N4: (a) total degradation rate and (b) dark adsorption curve.
Figure 3. Effect of FeOOH mass fraction on photocatalytic degradation of PNP by FeOOH/g-C3N4: (a) total degradation rate and (b) dark adsorption curve.
Molecules 29 03202 g003
Molecules 29 03202 g004
Figure 4. XRD patterns of g-C3N4, FeOOH/g-C3N4 and FeOOH.
Figure 4. XRD patterns of g-C3N4, FeOOH/g-C3N4 and FeOOH.
Molecules 29 03202 g004
Molecules 29 03202 g005
Figure 5. EDS diagram of FeOOH/g-C3N4.
Figure 5. EDS diagram of FeOOH/g-C3N4.
Molecules 29 03202 g005
Molecules 29 03202 g006
Figure 6. SEM of (a) g-C3N4 and (b) FeOOH/g-C3N4.
Figure 6. SEM of (a) g-C3N4 and (b) FeOOH/g-C3N4.
Molecules 29 03202 g006
Molecules 29 03202 g007
Figure 7. N2 adsorption–desorption curves (a) and pore size distribution curves (b) for g-C3N4 and FeOOH/g-C3N4 catalysts.
Figure 7. N2 adsorption–desorption curves (a) and pore size distribution curves (b) for g-C3N4 and FeOOH/g-C3N4 catalysts.
Molecules 29 03202 g007
Molecules 29 03202 g008
Figure 8. (a) UV-Vis DRS of g-C3N4, FeOOH and FeOOH/g-C3N4; the Tauc plots of (b) g-C3N4 and (c) FeOOH.
Figure 8. (a) UV-Vis DRS of g-C3N4, FeOOH and FeOOH/g-C3N4; the Tauc plots of (b) g-C3N4 and (c) FeOOH.
Molecules 29 03202 g008
Molecules 29 03202 g009
Figure 9. Effects of different degradation processes on PNP treatment.
Figure 9. Effects of different degradation processes on PNP treatment.
Molecules 29 03202 g009
Molecules 29 03202 g010
Figure 10. Effect of H2O2 concentration on PNP degradation efficiency: (a) photocatalytic degradation curve and (b) quasi-first-order kinetic fitting curve of photocatalytic reaction.
Figure 10. Effect of H2O2 concentration on PNP degradation efficiency: (a) photocatalytic degradation curve and (b) quasi-first-order kinetic fitting curve of photocatalytic reaction.
Molecules 29 03202 g010
Molecules 29 03202 g011
Figure 11. Effect of catalyst dosage on PNP degradation efficiency: (a) photocatalytic degradation curve and (b) quasi-first-order kinetic fitting curve of photocatalytic reaction.
Figure 11. Effect of catalyst dosage on PNP degradation efficiency: (a) photocatalytic degradation curve and (b) quasi-first-order kinetic fitting curve of photocatalytic reaction.
Molecules 29 03202 g011
Molecules 29 03202 g012
Figure 12. Effect of initial pH value of the reaction system on PNP degradation efficiency: (a) photocatalytic degradation curve and (b) quasi-first-order kinetic fitting curve of photocatalytic reaction.
Figure 12. Effect of initial pH value of the reaction system on PNP degradation efficiency: (a) photocatalytic degradation curve and (b) quasi-first-order kinetic fitting curve of photocatalytic reaction.
Molecules 29 03202 g012
Molecules 29 03202 g013
Figure 13. Effect of initial concentration of PNP on its degradation efficiency: (a) photocatalytic degradation curve and (b) quasi-first-order kinetic fitting curve of photocatalytic reaction.
Figure 13. Effect of initial concentration of PNP on its degradation efficiency: (a) photocatalytic degradation curve and (b) quasi-first-order kinetic fitting curve of photocatalytic reaction.
Molecules 29 03202 g013
Molecules 29 03202 g014
Figure 14. Recycling test of FeOOH/g-C3N4 photocatalyst for PNP degradation.
Figure 14. Recycling test of FeOOH/g-C3N4 photocatalyst for PNP degradation.
Molecules 29 03202 g014
Molecules 29 03202 g015
Figure 15. Active species capture experiment of PNP degradation by FeOOH/g-C3N4.
Figure 15. Active species capture experiment of PNP degradation by FeOOH/g-C3N4.
Molecules 29 03202 g015
Table 1. Effect of H2O2 dosage on PNP degradation: quasi-first order kinetic analysis.
Table 1. Effect of H2O2 dosage on PNP degradation: quasi-first order kinetic analysis.
H2O2 Dosage
(mmol L−1)		Kinetic EquationSpeed Constant k
(min−1)		R2
2.0y = 0.00863x0.008630.99412
3.0y = 0.0145x0.01450.99379
4.0y = 0.01992x0.019920.99543
5.0y = 0.02161x0.021610.99293
Table 2. Effect of catalyst dosage on PNP degradation: quasi-first order kinetic analysis.
Table 2. Effect of catalyst dosage on PNP degradation: quasi-first order kinetic analysis.
Catalyst Dosage
(mg L−1)		Kinetic EquationSpeed Constant k (min−1)R2
0.6y = 0.00616x0.006160.99924
0.8y = 0.00952x0.009520.99085
1.0y = 0.01992x0.019920.99543
1.2y = 0.01674x0.016740.99574
Table 3. Effect of initial pH on PNP degradation: quasi-first order kinetic analysis.
Table 3. Effect of initial pH on PNP degradation: quasi-first order kinetic analysis.
Initial pH ValueKinetic EquationKinetic Equation k (min−1)R2
3y = 0.02469x0.024690.99628
5y = 0.02079x0.020790.99916
7y = 0.01441x0.014410.99292
9y = 0.01098x0.010980.9901
Table 4. Effects of PNP initial concentration on its degradation: quasi-first order kinetic analysis.
Table 4. Effects of PNP initial concentration on its degradation: quasi-first order kinetic analysis.
Initial Conc. of PNP
(mg L−1)		Kinetic EquationKinetic Equation k (min−1)R2
5y = 0.02712x0.027120.99774
10y = 0.02079x0.020790.99916
15y = 0.01011x0.010110.99701
20y = 0.00781x0.007810.99443
Table 5. Comparison of degradation results of organic pollutants by different catalysts.
Table 5. Comparison of degradation results of organic pollutants by different catalysts.
CatalystsTarget PollutantLight SourcesDegradation Time (min)Degradation Rate (%)Refs
Al2O3/g-C3N4RhB300 W Xe lamp12083[38]
ZnO/g-C3N4MO150 W Xe lamp30065[39]
O-g-C3N4Cr(VI)300 W Xe lamp6080[40]
α-Fe2O3/g-C3N4Cr(VI)300 W Xe lamp15098[41]
TiO2/g-C3N4RhB300 W Xe lamp18080[42]
FeOOH/g-C3N4brilliant blue500 W Xe lamp3099Present work
Disclaimer/Publisher’s Note: The statements, opinions and data contained in all publications are solely those of the individual author(s) and contributor(s) and not of MDPI and/or the editor(s). MDPI and/or the editor(s) disclaim responsibility for any injury to people or property resulting from any ideas, methods, instructions or products referred to in the content.

Share and Cite

MDPI and ACS Style

Su, R.; Wang, J.; Jiang, H.; Wei, L.; Mu, D.; Yang, C. High-Efficiency Photo-Fenton-like Catalyst of FeOOH/g-C3N4 for the Degradation of PNP: Characterization, Catalytic Performance and Mechanism Exploration. Molecules 2024, 29, 3202. https://doi.org/10.3390/molecules29133202

AMA Style

Su R, Wang J, Jiang H, Wei L, Mu D, Yang C. High-Efficiency Photo-Fenton-like Catalyst of FeOOH/g-C3N4 for the Degradation of PNP: Characterization, Catalytic Performance and Mechanism Exploration. Molecules. 2024; 29(13):3202. https://doi.org/10.3390/molecules29133202

Chicago/Turabian Style

Su, Rongjun, Junhao Wang, Hao Jiang, Lan Wei, Deying Mu, and Chunyan Yang. 2024. "High-Efficiency Photo-Fenton-like Catalyst of FeOOH/g-C3N4 for the Degradation of PNP: Characterization, Catalytic Performance and Mechanism Exploration" Molecules 29, no. 13: 3202. https://doi.org/10.3390/molecules29133202

Article Metrics

Back to TopTop