Preparation of vanadium titano-magnetite slag waste derived composite carbon catalytic material and method for degrading sulfathiazole by activating peroxymonosulfate through vanadium titano-magnetite slag waste derived composite carbon catalytic material

Abstract

The invention relates to preparation of a vanadium titano-magnetite slag waste derived composite carbon catalytic material and a method for degrading sulfathiazole by activating peroxymonosulfate by using the vanadium titano-magnetite slag waste derived composite carbon catalytic material, and belongs to the technical field of oxidation catalytic materials and environments. The invention aims to solve the technical problem that the existing sulfathiazole widely exists in a water environment and forms a remarkable risk to the environment. The method comprises the following steps: grinding and sieving the vanadium titano-magnetite slag; pouring ammonium chloride, citric acid monohydrate, disodium ethylene diamine tetraacetate and the vanadium titano-magnetite slag sieved in the step 1 into an ethanol solution, and performing ultrasonic dispersion; heating and stirring in a water bath, then drying and grinding, and heating to obtain the powdery magnetic carbon-based material. The composite carbon catalytic material derived from the vanadium titano-magnetite slag is prepared by adopting a vacuum thermal synthesis method. The material can efficiently activate peroxymonosulfate to generate singlet oxygen non-free radical active species, and the degradation of a target pollutant sulfathiazole is accelerated through an efficient electron migration pathway. The catalytic material is applied to advanced oxidative degradation of high-concentration organic matters.

Description

Technical Field

[0001] The invention belongs to the field of oxidation catalytic materials and environmental technology, and particularly relates to a preparation method of a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste and a method for degrading sulfathiazole in water. Background Art

[0002] Water pollution is a global problem that poses a significant threat to human survival and safety, becoming a major obstacle to human health, economic and social sustainability. The widespread presence of sulfathiazole (STZ) in aquatic environments poses a significant risk. STZ concentrations in aquaculture wastewater are tens of thousands times higher than those in natural waters, with detected concentrations as high as 54.83 mg / L. PMS is relatively stable at room temperature. However, it requires specific conditions (such as acids, alkalis, high temperatures, ultraviolet light, ultrasound, metals, oxides, and carbon-based materials) to activate peroxymonosulfate (PMS) to generate ROS, which catalyzes the degradation of STZ. Therefore, advanced oxidation processes based on PMS activation are promising remediation methods. Summary of the Invention

[0003] In order to solve the technical problem that sulfathiazole is currently widely present in water environments and poses significant risks to the environment, the present invention provides a method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste and activating peroxymonosulfate to degrade sulfathiazole.

[0004] The preparation method of composite carbon catalytic material derived from vanadium-titanium magnetite slag waste is specifically carried out in the following steps:

[0005] 1. Grind and sieve the vanadium-titanium magnetite slag;

[0006] 2. Pour ammonium chloride, citric acid monohydrate, disodium ethylenediaminetetraacetic acid and the sieved vanadium-titanium magnetite slag in the step 1 into the ethanol solution and disperse them by ultrasonication to obtain a mixed solution;

[0007] 3. The mixed solution obtained in step 2 is heated and stirred in a water bath, then dried and ground, and then heated in a crucible under nitrogen conditions to obtain a powdered magnetic carbon-based material, namely, a vanadium-titanium magnetite slag waste-derived composite carbon catalytic material, thereby completing the preparation.

[0008] Furthermore, the particle size of the vanadium-titanium magnetite slag after screening in step 1 is less than 200 mesh.

[0009] Furthermore, the amount of vanadium-titanium magnetite slag added to the mixed solution in step 2 is 20-35 g / L.

[0010] Furthermore, the amount of citric acid monohydrate added to the mixed solution in step 2 is 15-30 g / L.

[0011] Furthermore, the dosage of disodium edetate in step 2 is 40-75 g / L.

[0012] Furthermore, the amount of the ammonium chloride solution in step 2 is 2.5-15 g / L.

[0013] Furthermore, the mass concentration of the ethanol solution in step 2 is 75-100%.

[0014] Furthermore, in step three, the vacuum heating temperature is controlled to be 700-1000° C. and the heating time is 1-3 hours.

[0015] Furthermore, in step three, the water bath heating temperature is 80° C., and the stirring time is 6 to 8 hours.

[0016] A method for activating peroxymonosulfate to degrade sulfathiazole using a prepared vanadium-titanium magnetite slag waste-derived composite carbon catalytic material, the method comprising:

[0017] Peroxymonosulfate was added to the wastewater containing sulfathiazole as the target antibiotic, and then the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste was added for treatment. The initial pH of the wastewater was 1-13, and the initial concentration of sulfathiazole in the wastewater was 1×10 -3 ~20 mg / L, the dosage of peroxymonosulfate is 1~20 mmol / L, the dosage of vanadium-titanium magnetite slag waste-derived composite carbon catalytic material is 0.01-0.5 g / L, the treatment temperature is 5~40℃, and the treatment time is controlled to be 5~100 min.

[0018] This invention combines vanadium-titanium magnetite slag, citric acid, disodium ethylenediaminetetraacetic acid (EDTA-2Na), and ammonium chloride (NH4Cl) to develop a targeted strategy for the design of high-performance composite catalytic materials. The key strategy lies in utilizing organic ligands (citric acid and EDTA-2Na) to achieve efficient dispersion and valence control of metal ions. Carbon sources (citric acid) and nitrogen sources (EDTA-2Na and NH4Cl) are used to construct a functionalized, highly conductive, nitrogen-doped carbon matrix to anchor active sites and promote electron transfer. A pore-forming agent (NH4Cl) is also used to create an optimized hierarchical pore structure to enhance mass transfer. The resulting WDM material combines the advantages of high catalytic activity (due to optimized multi-metal synergy and nitrogen-doped carbon), high stability (low metal leaching), excellent mass transfer performance (hierarchical pore structure), and low raw material cost (waste utilization). This strategy significantly differentiates it from, and outperforms, existing approaches that directly utilize natural iron-based minerals.

[0019] Coexisting ions and humic acid were used as the initial environmental factors of the system to analyze the advanced oxidation efficiency of vanadium-titanium magnetite slag waste-derived composite carbon catalytic materials (WDM); at the same time, tap water, surface water and secondary sedimentation tank effluent were selected as pollutant dispersion systems to verify the practical application potential of vanadium-titanium magnetite slag waste-derived composite carbon catalytic materials in activating PMS to degrade sulfathiazole.

[0020] The catalytic material of the present invention can be applied to the advanced oxidation degradation of high-concentration organic matter (antibiotics). Vanadium-titanium magnetite slag, citric acid monohydrate, disodium ethylenediaminetetraacetic acid, ammonium chloride and ethanol are added to simulated wastewater (sulfathiazole solution). After adsorption saturation under dark light conditions, the pollutants are degraded by visible light irradiation at room temperature.

[0021] Beneficial effects of the present invention:

[0022] 1. The present invention establishes a simple method for deriving composite carbon catalytic materials from vanadium-titanium magnetite slag waste, which is highly efficient, controllable and convenient;

[0023] 2. This method can achieve efficient reduction of sulfathiazole in water environment;

[0024] 3. This method also has a high reduction efficiency for low concentrations (ppm) of sulfathiazole in actual water bodies;

[0025] 4. This method also has a high reduction efficiency for sulfathiazole in low temperature (≤15°C) water environment;

[0026] 5. This method has a high degradation rate for sulfathiazole and can achieve large-scale degradation in a short time (10 min);

[0027] 6. This method can efficiently degrade sulfathiazole in actual water bodies, has a certain effect on the purification of surface water, can meet the country's major needs for efficient, economical, sustainable and green development, and provides technical and theoretical support for the management of antibiotics in the water environment.

[0028] This invention utilizes a vacuum thermal synthesis method to prepare a composite carbon catalytic material derived from vanadium-titanium magnetite slag. This material efficiently activates peroxymonosulfate (PMS), primarily producing singlet oxygen (¹O2) as a non-radical active species. It also accelerates the degradation of the target pollutant, sulfathiazole, via a highly efficient electron transfer pathway. By regulating the vacuum thermal synthesis temperature and using sulfathiazole degradation efficiency as a probe reaction, the composite material with a high catalytic activity doping ratio was optimized. A systematic investigation of the effects of key operating parameters on the material's performance confirmed its excellent treatment effect on antibiotic-containing wastewater, suggesting promising prospects for practical water applications.

[0029] The catalytic material prepared by the invention is used for treating antibiotics in water environments. BRIEF DESCRIPTION OF THE DRAWINGS

[0030] Figure 1 The X-ray diffraction patterns of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste before and after degradation of STZ were obtained in Example 1;

[0031] Figure 2 Fourier transform infrared spectra of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1 before and after degradation of STZ;

[0032] Figure 3 X-ray photoelectron spectra of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1 before and after degradation of STZ;

[0033] Figure 4 This is a hysteresis loop test diagram of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1;

[0034] Figure 5 The UV-visible-diffuse reflectance spectrum of NBT excited by the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1;

[0035] Figure 6 This is a diagram showing the effects of different factors on the degradation efficiency of composite carbon catalytic materials derived from vanadium-titanium magnetite slag waste;

[0036] Figure 7 This is the environmental characteristics diagram of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1;

[0037] Figure 8 This is the effect of coexisting ions and humic acid on the STZ degradation efficiency of WDM materials;

[0038] Figure 9 The figure shows the effect of different concentrations of coexisting substances on STZ removal efficiency;

[0039] Figure 10 This is the effect of actual water on the STZ degradation efficiency of WDM;

[0040] Figure 11 This is a graph showing the degradation efficiency of STZ in a homogeneous system;

[0041] Figure 12 This is a test chart of the recycling efficiency of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1;

[0042] Figure 13 This is a stability test chart of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1. DETAILED DESCRIPTION

[0043] Specific embodiment 1: The preparation method of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste in this embodiment is specifically carried out in the following steps:

[0044] 1. Grind and sieve the vanadium-titanium magnetite slag;

[0045] 2. Pour ammonium chloride, citric acid monohydrate, disodium ethylenediaminetetraacetic acid and the sieved vanadium-titanium magnetite slag in the step 1 into the ethanol solution and disperse them by ultrasonication to obtain a mixed solution;

[0046] 3. The mixed solution obtained in step 2 is heated and stirred in a water bath, then dried and ground, and then heated in a crucible under nitrogen conditions to obtain a powdered magnetic carbon-based material, namely, a vanadium-titanium magnetite slag waste-derived composite carbon catalytic material, thereby completing the preparation.

[0047] Specific embodiment 2: This embodiment differs from specific embodiment 1 in that the particle size of the vanadium-titanium magnetite slag after screening in step 1 is less than 200 meshes. Other steps are the same as those in specific embodiment 1.

[0048] Specific embodiment 3: This embodiment differs from specific embodiment 1 or 2 in that the amount of vanadium-titanium magnetite slag added to the mixed solution in step 2 is 20-35 g / L. Other aspects are the same as specific embodiment 1 or 2.

[0049] Specific embodiment 4: This embodiment differs from specific embodiments 1 to 3 in that the amount of citric acid monohydrate added to the mixed solution in step 2 is 15-30 g / L. Other aspects are the same as specific embodiments 1 to 3.

[0050] Specific embodiment 5: This embodiment differs from specific embodiments 1 to 4 in that the dosage of disodium EDTA in step 2 is 40-75 g / L. Other steps are the same as those of specific embodiments 1 to 4.

[0051] Specific embodiment 6: This embodiment differs from specific embodiments 1 to 5 in that the amount of the ammonium chloride solution in step 2 is 2.5-15 g / L. Other aspects are the same as specific embodiments 1 to 5.

[0052] Specific embodiment 7: This embodiment differs from Specific embodiments 1 to 6 in that the mass concentration of the ethanol solution in step 2 is 75-100%. Other aspects are the same as Specific embodiments 1 to 6.

[0053] Specific embodiment 8: This embodiment differs from specific embodiments 1 to 7 in that: in step 3, the vacuum heating temperature is controlled to be 700-1000° C. and the heating time is 1-3 hours. Other aspects are the same as specific embodiments 1 to 7.

[0054] Specific embodiment 9: This embodiment differs from specific embodiments 1 to 8 in that the water bath heating temperature in step 3 is 80° C. and the stirring time is 6 to 8 hours. Other aspects are the same as specific embodiments 1 to 8.

[0055] Specific embodiment 10: In this embodiment, a method for activating peroxymonosulfate to degrade sulfathiazole using a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste is as follows:

[0056] Peroxymonosulfate was added to the wastewater containing sulfathiazole as the target antibiotic, and then the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste was added for treatment. The initial pH of the wastewater was 1-13, and the initial concentration of sulfathiazole in the wastewater was 1×10 -3 ~20 mg / L, the dosage of peroxymonosulfate is 1~20 mmol / L, the dosage of vanadium-titanium magnetite slag waste-derived composite carbon catalytic material is 0.01-0.5 g / L, the treatment temperature is 5~40℃, and the treatment time is controlled to be 5~100 min.

[0057] The content of the present invention is not limited to the content of the above-mentioned embodiments. The combination of one or more specific embodiments can also achieve the purpose of the invention.

[0058] Example 1:

[0059] The preparation method of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste in this embodiment is specifically carried out according to the following steps:

[0060] 1. Grinding and screening the vanadium-titanium magnetite slag, wherein the particle size of the vanadium-titanium magnetite slag after screening is less than 200 mesh;

[0061] 2. Pour 1 g of ammonium chloride, 5 g of citric acid monohydrate, 10 g of disodium ethylenediaminetetraacetic acid, and 5 g of the sieved vanadium-titanium magnetite slag obtained in step 1 into 200 mL of an 80% ethanol solution, and perform ultrasonic dispersion to obtain a mixed solution;

[0062] 3. The mixed solution obtained in step 2 was stirred in an 80°C water bath for 6 h, then dried and ground, and then heated to 1000°C in a tube furnace under N2 atmosphere conditions (N2 flow rate of 100 mL / min) and maintained for 2 h, and then naturally cooled to room temperature to obtain a powdered magnetic carbon-based material, namely, vanadium-titanium magnetite slag waste-derived composite carbon catalytic material (WDM), completing the preparation.

[0063] Figure 1 The X-ray diffraction patterns (XRD) of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste before and after degradation of STZ were obtained in Example 1: The crystal structure of the catalytic material changed significantly before and after degradation of STZ: the intensity of the characteristic peak of Fe3O4 (such as 35.5°) decreased, indicating that the iron oxide underwent an oxidative phase transition (Fe2+ →Fe 3+ A new broad peak appeared at 28.5°, which was attributed to the amorphous carbon residues produced by STZ degradation covering the catalyst surface.

[0064] Figure 2 The Fourier transform infrared spectra (FT-IR) of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste before and after degradation of STZ prepared in Example 1: the OH / NH peak (3400 cm -1 ) weakened, indicating that hydroxyl / amino groups participated in the reaction; the C=O peak blue shifted (1630→1650 cm -1 ) suggests oxidation of the quinone group; 1384 cm -1 New peaks confirm the presence of -CH3 or NO3 - Adsorption of degradation intermediates.

[0065] Figure 3 X-ray photoelectron spectroscopy (XPS) of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1 before and after degradation of STZ: Fe 2p 3 / 2 The binding energy of the peak (710 eV) increases, confirming that Fe 2+ Fe 3+ The Ti / V peak shift reflects the change in metal valence state; the lattice oxygen ratio in the O 1s spectrum decreases, which proves that oxygen species participate in PMS activation.

[0066] Figure 4 The hysteresis loop test diagram (VSM) of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1: the hysteresis loop shows that the material has ferromagnetism (saturation magnetization intensity >20 emu / g), which supports magnetic recovery applications; the change in coercive force indicates that the grain size is reduced or the surface is chemically modified after the reaction.

[0067] Figure 5 The UV-visible diffuse reflectance spectrum (UV-vis-DRS) of NBT excited by the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1 is as follows: NBT-·O2 - The absorbance of the reaction product at 259 nm increased with time, confirming that the non-free radical pathway·O2 - Generation; Peak intensity change rate reflects O2 - The yield is regulated by the catalytic conditions.

[0068] The simulated antibiotic wastewater system uses sulfathiazole as a representative antibiotic. The concentration is higher than the actual environmental concentration. At the same time, 1 ppm is selected for environmental concentration simulation, and the simulation experiment is carried out with laboratory deionized water as the dispersion system.

[0069] Catalytic degradation experiments were conducted in a homogeneous mixing system simulating antibiotic wastewater. The reaction temperature was optimized in a water bath. Magnetic stirring was used to ensure thorough mixing. Samples were taken at specific intervals, filtered through a 0.22 μm filter membrane, and the filtrate was analyzed by high-performance liquid chromatography (HPLC) to determine the residual STZ concentration.

[0070] Catalytic materials WDM and PMS were added in the experiment, the simulated wastewater system was 100 mL, the simulated antibiotic wastewater was sulfathiazole solution, the reaction degradation time was 5-60 min, and the pH range of the simulated system was 1-13.

[0071] Figure 6 Figure 3 shows the effects of different factors on the degradation efficiency of composite carbon catalytic materials derived from vanadium-titanium magnetite slag waste. a is the effect of initial PMS concentration on STZ degradation efficiency, ■ represents 20 mM, ● represents 15 mM, ▲ represents 10 mM, ▼ represents 5 mM, and ◆ represents 1 mM; b is the effect of initial catalyst dosage on STZ degradation efficiency, ■ represents 20 mg / L, ● represents 10 mg / L, ▲ represents 2.5 mg / L, and ▼ represents 1 mg / L; c is the effect of system temperature on STZ degradation efficiency, ■ represents 35℃, ● represents 25℃, ▲ represents 15℃, ▼ represents 10℃, and ◆ represents 5℃; d is the effect of initial STZ concentration on its own degradation efficiency, ■ represents 20 mg / L, ● represents 10 mg / L, ▲ represents 1 mg / L, and ▼ represents 1×10 -3 mg / L;

[0072] Depend on Figure 6 It can be seen that under different initial PMS concentrations, the degradation rate of STZ by WDM within 10 minutes is above 80%, and it has the ability to completely remove STZ with different initial concentrations; and the catalytic material can also achieve efficient STZ removal efficiency at low temperature (10°C), which fully proves the prospect of this material in wastewater treatment in cold regions.

[0073] Figure 7 This is a graph showing the environmental characteristics of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1, where a is the STZ removal rate graph under different pH conditions, and b is the zeta potential graph. It can be seen that the degradation rate is highest at pH = 1 (■), and the STZ removal rate decreases in an alkaline environment (pH>11), but almost complete removal can still be achieved in the end. This result is positively correlated with the material's zeta potential (acidic positive charge facilitates adsorption). The acid buffer system (◆) behaves abnormally, indicating that the buffer ions may interfere with the reaction.

[0074] Figure 8 This is the effect of coexisting ions and humic acid on the STZ degradation efficiency of WDM materials;

[0075] Figure 9 The effect of different concentrations of coexisting substances on STZ removal efficiency is shown in the figure; a is SO4 2- , b is HCO3 - , c is HA, d is H2PO4 - , e is NO3 - , f is Cl - ;

[0076] It can be seen that H2PO4 - It has a certain inhibitory effect on degradation (especially >10 mM) due to quenching active oxygen or competitive adsorption. Humic acid (HA) reduces efficiency by shielding active sites or competing for light absorption.

[0077] Figure 10 Figure 3 is the effect of actual water on the STZ degradation efficiency of WDM (catalytic material dosage is 0.025 g / L, PMS concentration is 1 mM), where ■ represents deionized water, ● represents tap water, ▲ represents surface water, and ▼ represents effluent from the Second Sedimentation Tank. The results show that the efficiency is highest in deionized water (■), and tap water / surface water decreases by about 10% due to ion interference. The effluent from the Second Sedimentation Tank (▼) has the strongest inhibition, which is presumably related to the high concentration of organic matter and suspended solids contained therein.

[0078] Figure 11 This is a test chart of the degradation efficiency of STZ in a homogeneous system. It can be concluded that the degradation of STZ can be ignored when there is no catalyst (only PMS), and the contribution of homogeneous reaction is excluded. It verifies that heterogeneous catalysis is the dominant mechanism.

[0079] Figure 12 This is a test chart of the cycle efficiency of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste prepared in Example 1; after 5 cycles, the STZ removal rate remained >85%, demonstrating the stability of the material, and the slight decrease in STZ degradation efficiency was attributed to active site coverage or iron ion dissolution.

[0080] Figure 13 Figure 1 shows the stability test of the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste (ion leaching experiment) prepared in Example 1. The Fe / Ti / V leaching amounts were all <0.5 mg / L, far below environmental standards.

[0081] It is confirmed that the vanadium-titanium magnetite slag-derived composite carbon catalytic material can achieve efficient PMS activation through vacuum thermal synthesis regulation, and its core mechanism is: non-radical pathway ( 1 O2) dominated the degradation of sulfathiazole (STZ), and the Fe 2+ Oxidized to Fe3+ It triggers lattice reconstruction (XRD peak weakening / displacement) and simultaneously adsorbs carbon-containing intermediates on the surface (new FT-IR peaks); practical applications show that it maintains a degradation rate of >90% under acidic conditions (pH=3) and a wide temperature range (5-35°C), and has strong resistance to water interference (actual water efficiency decreases ≤20%), and a five-cycle stability of >85%. It has both magnetic recovery characteristics and low metal leaching risk (Fe dissolution <0.5 mg / L), providing a feasible solution for antibiotic wastewater treatment.

Claims

1. A method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste, characterized in that The method is specifically carried out in the following steps:

1. Grind and sieve the vanadium-titanium magnetite slag; 2. Pour ammonium chloride, citric acid monohydrate, disodium ethylenediaminetetraacetic acid and the sieved vanadium-titanium magnetite slag in the step 1 into the ethanol solution and disperse them by ultrasonication to obtain a mixed solution; 3. The mixed solution obtained in step 2 is heated and stirred in a water bath, then dried and ground, and then heated in a crucible under nitrogen conditions to obtain a powdered magnetic carbon-based material, namely, a vanadium-titanium magnetite slag waste-derived composite carbon catalytic material, thereby completing the preparation.

2. The method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste according to claim 1, characterized in that The particle size of the vanadium-titanium magnetite slag after screening in step 1 is less than 200 meshes.

3. The method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste according to claim 1, characterized in that The amount of vanadium-titanium magnetite slag added to the mixed solution in step 2 is 20-35 g / L.

4. The method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste according to claim 1, characterized in that The amount of citric acid monohydrate added to the mixed solution in step 2 is 15-30 g / L.

5. The method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste according to claim 1, characterized in that The dosage of disodium edetate in step 2 is 40-75 g / L.

6. The method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste according to claim 1, characterized in that The amount of ammonium chloride solution used in step 2 is 2.5-15 g / L.

7. The method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste according to claim 1, characterized in that The mass concentration of the ethanol solution in step 2 is 75-100%.

8. The method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste according to claim 1, characterized in that Step 3: Control the vacuum heating temperature to 700~1000℃ and the heating time to 1~3h.

9. The method for preparing a composite carbon catalytic material derived from vanadium-titanium magnetite slag waste according to claim 1, characterized in that Step 3: The water bath heating temperature is 80°C and the stirring time is 6 to 8 hours.

10. The method for degrading sulfathiazole by activating peroxymonosulfate using composite carbon catalytic materials derived from vanadium-titanium magnetite slag waste prepared as claimed in claim 1, characterized in that The method is: Peroxymonosulfate was added to the wastewater containing sulfathiazole as the target antibiotic, and then the composite carbon catalytic material derived from vanadium-titanium magnetite slag waste was added for treatment. The initial pH of the wastewater was 1-13, and the initial concentration of sulfathiazole in the wastewater was 1×10 -3 ~20 mg / L, the dosage of peroxymonosulfate is 1~20 mmol / L, the dosage of vanadium-titanium magnetite slag waste-derived composite carbon catalytic material is 0.01-0.5 g / L, the treatment temperature is 5~40℃, and the treatment time is controlled to be 5~100 min.

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