CN114031167B - Method for synchronously removing microplastic and quinolone antibiotics in water - Google Patents

Method for synchronously removing microplastic and quinolone antibiotics in water Download PDF

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CN114031167B
CN114031167B CN202111305954.XA CN202111305954A CN114031167B CN 114031167 B CN114031167 B CN 114031167B CN 202111305954 A CN202111305954 A CN 202111305954A CN 114031167 B CN114031167 B CN 114031167B
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microplastic
water
feo
ferrate
quinolone antibiotics
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CN114031167A (en
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欧桦瑟
陈聿衡
张海璇
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Jinan University
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    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/72—Treatment of water, waste water, or sewage by oxidation
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/28—Treatment of water, waste water, or sewage by sorption
    • C02F1/281—Treatment of water, waste water, or sewage by sorption using inorganic sorbents
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2101/00—Nature of the contaminant
    • C02F2101/30—Organic compounds
    • C02F2101/34—Organic compounds containing oxygen

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  • Chemical & Material Sciences (AREA)
  • Life Sciences & Earth Sciences (AREA)
  • Hydrology & Water Resources (AREA)
  • Engineering & Computer Science (AREA)
  • Environmental & Geological Engineering (AREA)
  • Water Supply & Treatment (AREA)
  • Organic Chemistry (AREA)
  • Inorganic Chemistry (AREA)
  • Treatment Of Water By Oxidation Or Reduction (AREA)

Abstract

The invention discloses a method for synchronously removing microplastic and quinolone antibiotics in water. The invention adopts the ferrate pre-oxidation method, and generates nascent iron oxide (Fe) in the ferrate pre-oxidation process through specific condition regulation x O x ) The method takes the micro-plastic as a medium to improve the removal rate of the micro-plastic in the water in the pre-oxidation process, and synchronously adsorbs and removes the quinolone antibiotics in the water. Under the conditions of pH=6 and potassium ferrate adding concentration of 5mg/L, the PVC microplastic sinking rate in water exceeds 80%, and the ciprofloxacin removing rate exceeds 90%. The invention has low technical and economic cost, quick reaction of ferrate in water, no residual toxicity, no secondary pollution to water or other potential environmental risks, effective improvement of raw water treatment, even the removal efficiency of microplastic and quinolone antibiotics in the sewage treatment process, and wide application range.

Description

Method for synchronously removing microplastic and quinolone antibiotics in water
Technical Field
The invention belongs to the field of water supply and drainage engineering/environmental engineering, and mainly relates to a method for synchronously removing microplastic and quinolone antibiotics in water.
Background
Microplastic (MPs) is an emerging environmental contaminant, defined as plastic chips smaller than 5mm, having different shapes in the form of particles, flakes, filaments, etc. The microplastic sources are complex, including primary microplastics from personal care products and industrial processes, and secondary microplastics from the aging degradation of ordinary microplastics in the environment. Microplastic has strong stability to chemical and biological degradation, accumulates and persists in the environment after being released, and due to its tiny volume and stable nature, these waste polymer particles can migrate and transform continuously in aquatic or terrestrial ecosystems. In addition, the micro plastic can adsorb various organic pollutants, heavy metals, pathogenic bacteria and even resistance genes, so that the micro plastic can become an enrichment carrier of various environmental pollutants, thereby forming a potential threat to human beings at the top end of a food chain. Since the raw water is directly obtained from the freshwater ecosystem for the water treatment plant, the microplastic in the freshwater environment enters the daily water circulation of human beings.
Before the conventional treatment process of a water supply plant, a pre-oxidation technology is often adopted as an auxiliary method, and the auxiliary method generally comprises chlorine treatment, ozone oxidation, potassium permanganate oxidation and the like, so as to improve the removal rate of organic matters and microorganisms in raw water. At present, most of pre-oxidation technologies mainly aim at organic pollutants in water or improve the treatment effect of coagulating sedimentation in the subsequent process, and no technology for removing microplastic in raw water is available. If a proper pre-oxidation technology can be developed, the micro-plastics can be removed while the removal rate of organic matters in raw water is improved, so that the micro-plastics can be effectively intercepted at the front end of a water supply plant, and the potential risk of the micro-plastics on drinking water safety is reduced. Therefore, it is of great importance to develop a pre-oxidation technology capable of synchronously removing microplastic and organic pollutants in water.
Disclosure of Invention
In view of the shortcomings and drawbacks of the prior art, an object of the present invention is to provide a method for simultaneous removal of microplastic and quinolone antibiotics in water. The invention adopts the ferrate pre-oxidation method, and generates nascent iron oxide (Fe) in the ferrate pre-oxidation process through specific condition regulation x O x ) The method takes the micro-plastic as a medium to improve the removal rate of the micro-plastic in the water in the pre-oxidation process; the strong oxidizing property of ferrate can also degrade and remove quinolone antibiotics in water, and the nascent iron oxide compound generated on the surfaces of the micro-plastic particles has larger specific surface area, has adsorption effect on the quinolone antibiotics in water, can be used as an adsorbent to synergistically improve the removal rate of the quinolone antibiotics, and achieves the effect of synchronously removing the micro-plastic and the quinolone antibiotics in water.
The invention aims at realizing the following technical scheme:
a method for synchronously removing microplastic and quinolone antibiotics in water, comprising the following steps:
(1) Adding ferrate into a water body containing the microplastic and the quinolone antibiotics, and then carrying out oscillation reaction;
(2) And (3) standing the mixed solution after the oscillating reaction in the step (1), and synchronously removing the microplastic and the quinolone antibiotics.
Preferably, the pH of the water body in the step (1) is 3-11.
More preferably, the pH of the water body of step (1) is=6.
Preferably, the micro plastic in the step (1) is one or more than two of Polystyrene (PS), polyethylene terephthalate (PET) or polyvinyl chloride (PVC) with the size of 1-500 μm.
Preferably, the concentration of the microplastic in the water body in the step (1) is 5-250 mg/L, and the concentration of the quinolone antibiotics is 0.5-10 mg/L.
Preferably, the quinolone antibiotic of step (1) is Ciprofloxacin (CPFX).
Preferably, the ferrate of step (1) is K 2 FeO 4 Or Na (or) 2 FeO 4 One or a combination of both.
Preferably, the amount of ferrate added in step (1) is 5-40 mg/L.
More preferably, the amount of ferrate added in step (1) is 5mg/L.
Preferably, the rotational speed of the shaking reaction in the step (1) is 300-500 rpm, and the time is 0.5-2 h.
More preferably, the time of the shaking reaction in step (1) is 2 hours.
Preferably, the standing in the step (2) is specifically carried out for more than 30 minutes until the micro plastic is free to settle to a stable state.
Compared with the prior art, the invention has the following advantages:
(1) The invention adopts ferrate pre-oxidation technology to improve the sinking rate of the microplastic, and obtains the optimal reaction condition through condition control, thereby realizing the rapid sedimentation removal of the microplastic in water.
(2) The invention is based on ferrate pre-oxidation technology, and performs condition control to improve the generation efficiency of the nascent iron oxide in the system, thereby improving the adsorption effect of the nascent iron oxide on the quinolone antibiotics in the system and realizing synchronous and efficient removal of the microplastic and the quinolone antibiotics in the water.
(3) The invention has low technical and economic cost, quick reaction of ferrate in water, no residual toxicity, no secondary pollution to water or other potential environmental risks, effective improvement of raw water treatment, even the removal efficiency of microplastic and quinolone antibiotics in the sewage treatment process, and wide application range.
Drawings
FIG. 1 is an SEM image of an untreated 100 μm PVC microplastic as received in simulation experiment 1.
FIG. 2 is a graph of the K-th curve of 100 μm PVC microplastic at pH=3 in simulation experiment 1 2 FeO 4 SEM image after oxidation.
FIG. 3 is a graph of the K-th curve of 100 μm PVC microplastic at pH=6 in simulation experiment 1 2 FeO 4 SEM image after oxidation.
FIG. 4 is a graph of the K-th curve of 100 μm PVC microplastic at pH=8 in simulation experiment 1 2 FeO 4 SEM image after oxidation.
FIG. 5 is a graph of the K-th curve of 100 μm PVC microplastic at pH=11 in simulation experiment 1 2 FeO 4 SEM image after oxidation.
FIG. 6 is a graph showing the K-exposure of 100 μm PVC microplastic in simulation experiment 1 at different pH values 2 FeO 4 XPS graph after oxidation (O1 s).
FIG. 7 is a graph showing the K-exposure of 100 μm PVC microplastic in simulation experiment 1 at different pH values 2 FeO 4 XPS graph after oxidation (Fe 2 p).
FIG. 8 shows the 6.5 μm microplastic in simulation experiment 1 at different K 2 FeO 4 Dip rate at concentration.
FIG. 9 shows K-exposure of 6.5 μm microplastic in simulation experiment 1 at different pH values 2 FeO 4 Sinking rate after oxidation.
FIG. 10 shows the CPFX removal rate in simulation experiment 2.
FIG. 11 shows CPFX concentration standard curves.
FIG. 12 shows the sinking rate of PET and PVC microplastic in example 1 under different pH conditions.
FIG. 13 shows the removal rate of CPFX in example 1 at different pH conditions.
FIG. 14 shows the PET and PVC microplastics of example 2 at different K 2 FeO 4 Dip rate at concentration.
FIG. 15 shows CPFX at different K in example 2 2 FeO 4 Removal rate at concentration.
FIG. 16 is K in comparative example 1 2 FeO 4 The effect of CPFX alone was removed.
Detailed Description
The present invention will be described in further detail with reference to examples, but embodiments of the present invention are not limited thereto. The simulation experiments and examples, comparative examples were carried out at room temperature using K 2 FeO 4 The purity was 99% (CAS#: 39469-86-8). For process parameters not specifically noted, reference may be made to conventional techniques.
The invention firstly carries out experiment research by simulating water body to synchronously remove the optimal reaction condition of the microplastic and the quinolone antibiotics in the water.
The filtration device in the simulation experiments and examples consisted of a 10mL syringe and hydrophilic PTFE needle filter (0.45 μm), and the specific filtration steps were:
(1) Weigh mass M of each group of filter devices before filtration 1 ；
(2) After the reaction device is kept stand for 30min, micro-plastic particles floating on the surface of the liquid are transferred into a 10mL syringe by using a 5mL liquid-transferring gun, the solution is separated from the micro-plastic particles by a hydrophilic PTFE needle filter (0.45 mu m), and a 9.8% sulfuric acid solution is used for washing a filtering device to remove Fe which can affect the whole quality of the micro-plastic 2 O 3 Particles;
(3) Using ultrapure water (resistivity 18.2MΩ, soluble organic carbon DOC)<5. Mu.g/L) was washed three times with the filter device (for the purpose of removing residual K 2 FeO 4 And H 2 SO 4 Solution) was used in an amount of 10mL per time of ultrapure water; 10mL absolute ethyl alcohol (99%) is used for washing once again, so that the drying time is shortened; placing the filter device with the micro plastic particles in a 50 ℃ oven, and weighing the whole mass after dryingM 2 。
The calculation mode of the microplastic sinking rate in the simulation experiment and the embodiment is as follows: mass M of microplastic contained in filter device Float upwards ＝M 2 -M 1 The sinking rate of the microplastic in each group of reaction devices is the sinking mass and the total mass M of the microplastic Total (S) Ratio of:
the concentration of CPFX in the simulation experiment and examples and comparative examples was measured by spectrophotometry, the sampled solution was detected at 276nm wavelength using an ultraviolet spectrophotometer, and the measured absorbance was converted to the concentration of CPFX in the solution by a CPFX concentration standard curve (FIG. 11).
The solutions of ph=3, 6,8,11 in the simulation experiments consisted of 42.5wt% H 3 PO 4 Solution, 0.2mol/L Na 2 HPO 4 Solution, 0.2mol/L NaH 2 PO 4 The solution, 0.2mol/L NaOH solution and ultrapure water are mixed according to different proportions to prepare the water-based paint.
In the examples and comparative examples, a water sample obtained from a river in the vicinity of which a medical wastewater discharge port was present was used as a water body to be treated, solids and a solution in the water body were separated by using a vacuum filtration device (0.45 μm), and the types and concentrations of microplastic particles in the solids and the average concentration of CPFX in the solution were measured from a plurality of samples, respectively. The water sample detects the existence of PET and PVC microplastic particles, the concentration is 11.32mg/L and 14.43mg/L respectively, and the original CPFX concentration in the water sample is about 562 mug/L.
The pH of the water in the examples and comparative examples was 42.5wt% H 3 PO 4 Solution, 0.2mol/L Na 2 HPO 4 Solution, 0.2mol/L NaH 2 PO 4 The solution and 0.2mol/L NaOH solution were adjusted to 3,6,8 and 11.
Simulation experiment 1: influence of different reaction conditions on microplastic sedimentation effect
The experiment is carried out by using PS, PET, PVC microplastic with 6.5 μm, 100 μm and 500 μmA subject, in a solution with pH of 3,6,8,11, at a concentration of 5mg/L, 10mg/L, 20mg/L, 30mg/L, 40mg/L K 2 FeO 4 The optimal reaction condition for removing the microplastic by preoxidation of ferrate is explored by the solid particle adding concentration.
The experimental steps are as follows:
(1) Adding 50mg of microplastic into a beaker filled with 200mL of solution to oscillate to form a mixed solution, and simultaneously setting a beaker filled with 200mL of ultrapure water as a control group;
(2) Adding K into the beaker in the step (1) 2 FeO 4 And (3) continuously oscillating the solid particles at a rotating speed of 500rpm for reaction for 0.5h, standing the reaction device for 0.5h, enabling the micro-plastic particles to freely settle to a stable state, and calculating the sinking rate of the micro-plastic after filtering.
The results of this experiment are shown in FIGS. 1-9 and tables 1-3:
as can be seen from FIGS. 1, 2, 3, 4, 5, the micro-plastic material is subjected to K 2 FeO 4 The surfaces of the pre-oxidized micro plastic particles are adhered with a large amount of fine particles which are nascent iron oxide mixture generated in the oxidation process. The degree of iron oxide adhesion on the surface of the microplastic is different under different pH conditions. Wherein, when the pH value is=3, the surface of the microplastic has less attached iron oxide, and the pH value of the solution moves towards the neutral and alkaline directions, and K in the solution 2 FeO 4 The reaction mechanism of (c) is changed, the generated iron oxide is increased, and when the pH=6, the surface of the microplastic is covered with the most nascent iron oxide.
As can be seen from FIGS. 6 and 7, the microplastic warp K 2 FeO 4 The spectrum intensities of Fe2p and O1s on the oxidized surface are higher, which indicates that the surface has iron oxide compound, possibly Fe 2 O 3 FeOOH, etc.
As can be seen from Table 1, warp K 2 FeO 4 The sinking rate of the oxidized PVC microplastic is improved, wherein the sinking rate of PVC particles with the smallest particle diameter (6.5 mu m) is improved from 56.3% to 96.4% and is close to 100%.
As can be seen from Table 2, the PVC has an initial density of 1.42g/cm 3 Greater than the density of water, at different pH conditionsK 2 FeO 4 After the pre-oxidation treatment, the density of the PVC microplastic increases to some extent, especially at ph=6. For example, a PVC density of 6.5 μm is from 1.42g/cm 3 Increased to 1.69g/cm 3 And the degree of increase in density is proportional to the degree of increase in the sinking rate.
As can be seen from Table 3, warp K 2 FeO 4 The contact angle of the oxidized PVC microplastic is obviously reduced from 94.1 ° to 35.9 ° at ph=6, which indicates that the surface of the PVC microplastic changes from hydrophobic to hydrophilic, which is favorable for infiltration of water, thereby improving the sinking rate thereof.
As can be seen from FIG. 8, the microplastic dip rate is subjected to K 2 FeO 4 The effect of concentration variation is weak, when K 2 FeO 4 When the adding concentration is 5mg/L, the sinking rate of PET and PVC microplastic is raised to more than 80%, the sinking rate of PS is raised to more than 60%, and then the PET and PVC microplastic enter a platform stage and do not follow K 2 FeO 4 The increase in concentration was increased, which indicates that 5mg/L K was administered 2 FeO 4 The good sedimentation effect can be achieved by adding the concentration.
As can be seen from fig. 9, compared with the control group, the microplastic sinking rate is obviously improved under different pH conditions, and when the ph=6, the sinking rate is obviously higher than other pH conditions, which is consistent with the microscopic characterization results of the microplastic particles in table 2 and table 3, namely, under the oxidation condition of the solution ph=6, the surface of the microplastic has more nascent iron oxide, the surface hydrophilicity is stronger, and the density change of the microplastic particles is obvious.
Table 1 PVC warp K in simulation experiment 1 2 FeO 4 Change in the sinking rate after oxidation
TABLE 2 PVC warp K in simulation experiment 1 2 FeO 4 Density change after oxidation (g/cm) 3 )
TABLE 3 PVC K-passage of 500 μm in simulation experiment 1 2 FeO 4 Surface contact angle variation after oxidation
Simulation experiment 2: k (K) 2 FeO 4 Synchronous removal of microplastic and CPFX
In the experiment, 6.5 mu m PVC microplastic and CPFX are taken as experimental objects to explore K 2 FeO 4 Synchronous removal effect on microplastic particles and CPFX.
The experimental steps are as follows:
(1) 50mg of PVC microplastic with the thickness of 6.5 mu m and 2mg of CPFX are added into 200mL of solution with the pH of 3,6,8 and 11 to oscillate to form a mixed solution; (A beaker containing 200mL of ultrapure water was set simultaneously as a control group)
(2) Charging 1mg K into each of the four beakers in the step (1) 2 FeO 4 The solid particles continue to react for 2 hours at the rotating speed of 500rpm, and the removal rate of CPFX is detected by sampling at 0.5 hour, 1 hour, 1.5 hour and 2 hours respectively; closing the oscillator to stand the reaction device for 0.5h, enabling the micro plastic particles to be free to settle to a stable state, and calculating the sinking rate of the micro plastic after filtering.
The results of this experiment are shown in fig. 10 and table 4:
as can be seen from FIG. 10, effective CPFX removal was achieved at pH=3, 6,8, with a removal rate of up to 100% after 2h reaction due to K 2 FeO 4 And the adsorption of the nascent iron oxide produced, which together produce a significant removal effect on CPFX.
As can be seen from Table 4, the sinking rate of the PVC microplastic of 6.5 μm is obviously improved compared with that of the control group. As can be seen in combination with FIG. 10 and Table 4, K is carried out under the reaction conditions proposed in the present invention 2 FeO 4 The oxidation can realize the synchronous removal of the microplastic and the quinolone antibiotics in the water.
Table 4 PVC warp K in simulation experiment 2 2 FeO 4 Change in the sinking rate after oxidation
Example 1
(1) 1mg (i.e. 5 mg/L) K is respectively added into the beakers of 4 water bodies to be treated with 200mL pH=3, 6,8 and 11 2 FeO 4 The solid particles are subjected to oscillation reaction for 2 hours at a rotating speed of 500rpm, and sampling and detecting the removal rate of CPFX are respectively carried out at 0.5 hour, 1 hour, 1.5 hours and 2 hours;
(2) Closing the oscillator to stand the reaction device for 0.5h, enabling the micro plastic particles to be free to settle to a stable state, and calculating the sinking rate of the micro plastic after filtering. Three replicates were set for each set of experiments and the results averaged.
The results of this example are shown in fig. 12 and 13:
as can be seen from fig. 12, when ph=6, the microplastic sinking rate is significantly higher than other pH conditions, and according to the experimental results in the simulation experiment, the surface hydrophilicity of the microplastic is stronger due to more nascent iron oxide on the surface, and the density change of the particles is more obvious.
As can be seen from fig. 13, in the actual water body, the effective removal of CPFX can be achieved when ph=3, 6,8, and the removal rate exceeds 90% after 2 hours of reaction, which is consistent with the experimental results in the simulation experiment: k (K) 2 FeO 4 Together, the nascent iron oxide produced produces a significant removal effect on CPFX.
Example 2
(1) 1mg, 2mg, 4mg, 6mg and 8mg (corresponding to 5mg/L, 10mg/L, 20mg/L, 30mg/L and 40mg/L of the added concentration respectively) K are respectively added into 5 beakers filled with 200mL of water to be treated with pH=6 2 FeO 4 The solid particles are subjected to oscillation reaction for 2 hours at a rotating speed of 500rpm, and sampling and detecting the removal rate of CPFX are respectively carried out at 0.5 hour, 1 hour, 1.5 hours and 2 hours;
(2) Closing the oscillator to stand the reaction device for 0.5h, enabling the micro plastic particles to be free to settle to a stable state, and calculating the sinking rate of the micro plastic after filtering. Three replicates were set for each set of experiments and the results averaged.
The results of this example are shown in fig. 14 and 15:
as can be seen from FIG. 14, when K 2 FeO 4 When the adding concentration is 5mg/L, the sinking rate of the PET and PVC microplastic in the actual water body is raised to more than 75%, and the sinking rate is not along with K 2 FeO 4 The increase in concentration increases, which indicates 5mg/L K 2 FeO 4 The good sedimentation effect can be achieved by adding the concentration.
As can be seen from FIG. 15, K 2 FeO 4 When the concentration of the added solution was 5mg/L, the CPFX removal rate after 2 hours of reaction exceeded 90%, indicating that the concentration of K was 5mg/L 2 FeO 4 The good removing effect can be achieved by adding the concentration.
Comparative example 1
In this comparative example, a solution obtained by separating and removing a water body to be treated by vacuum filtration (i.e., a filtrate from which only CPFX is remained by removing microplastic) was used as an experimental object.
To 200mL of the filtrate at ph=6, 1mg K was added 2 FeO 4 (namely, the adding concentration is 5 mg/L), solid particles are subjected to oscillation reaction for 2 hours at a rotating speed of 500rpm, and sampling and detecting the removal rate of CPFX at 0.5 hour, 1 hour, 1.5 hour and 2 hours respectively.
The results of this comparative example are shown in fig. 16:
as can be seen from fig. 16, at ph=6, K 2 FeO 4 Under the condition of 5mg/L of adding concentration, after 2 hours of reaction, the CPFX removal rate is less than 70 percent and is far lower than the CPFX removal efficiency in the synchronous removal experiment of the microplastic and the CPFX. Therefore, the reaction condition provided by the invention can realize the synchronous removal of the microplastic and the quinolone antibiotics in the actual water body, and K 2 FeO 4 The oxidation reaction of (2) and the nascent iron oxide produced have a synergistic effect on the removal of CPFX.
The above examples are preferred embodiments of the present invention, but the embodiments of the present invention are not limited to the above examples, and any other changes, modifications, substitutions, combinations, and simplifications that do not depart from the spirit and principle of the present invention should be made in the equivalent manner, and the embodiments are included in the protection scope of the present invention.

Claims (5)

1. A method for synchronously removing microplastic and quinolone antibiotics in water, which is characterized by comprising the following steps:
(1) Adding ferrate into a water body containing the microplastic and the quinolone antibiotics, and then carrying out oscillation reaction; the pH of the water body is 6; the micro plastic is one or more than two of polystyrene, polyethylene terephthalate or polyvinyl chloride with the size of 6.5-500 mu m; the concentration of the microplastic in the water body is 5-250 mg/L, and the concentration of the quinolone antibiotics is 0.5-10 mg/L; the addition amount of ferrate is 5-40 mg/L; the rotation speed of the oscillating reaction is 300-500 rpm, and the time is 0.5-2 h;
(2) And (3) standing the mixed solution after the oscillating reaction in the step (1), and synchronously removing the microplastic and the quinolone antibiotics.
2. The method of claim 1, wherein the quinolone antibiotic in step (1) is ciprofloxacin.
3. The method of claim 1, wherein the ferrate of step (1) is K 2 FeO 4 Or Na (or) 2 FeO 4 One or a combination of both.
4. The method of claim 1, wherein the time of the shaking reaction in step (1) is 2 hours, and the amount of ferrate added in step (1) is 5mg/L.
5. The method according to claim 1, wherein the standing in step (2) is specifically for more than 30 min.
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Citations (2)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN111117814A (en) * 2019-12-30 2020-05-08 湖南大学 Magnetic carbon material for treating plastic surface pollutants and treatment method thereof
CN112892550A (en) * 2021-01-26 2021-06-04 暨南大学 Lanthanum-manganese double-doped bismuth ferrite nano material and preparation method and application thereof

Family Cites Families (1)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
JP5876476B2 (en) * 2010-06-11 2016-03-02 モリーコープ ミネラルズ エルエルシーＭｏｌｙｃｏｒｐ Ｍｉｎｅｒａｌｓ Ｌｌｃ Improvement of bioactive compounds from wastewater

Patent Citations (2)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN111117814A (en) * 2019-12-30 2020-05-08 湖南大学 Magnetic carbon material for treating plastic surface pollutants and treatment method thereof
CN112892550A (en) * 2021-01-26 2021-06-04 暨南大学 Lanthanum-manganese double-doped bismuth ferrite nano material and preparation method and application thereof

Non-Patent Citations (2)

* Cited by examiner, † Cited by third party
Title
Xianshi Wang et al..Quantitively Analyzing the Variation of Micrometer-Sized Microplastic during Water Treatment with the Flow Cytometry-Fluorescent Beads Method.《ACS Environmental Science and Technology Engineering》.2021,第1卷第1668-1677页. *
李进军等编著.绿色化学导论.武汉大学出版社,2015,(第2版),第45页. *

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