CN110508613B - Remediation method for polycyclic aromatic hydrocarbon contaminated soil - Google Patents
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Abstract
The invention provides a remediation method of polycyclic aromatic hydrocarbon contaminated soil, and belongs to the technical field of soil remediation. According to the invention, the soil polluted by the polycyclic aromatic hydrocarbon is made into the soil slurry by utilizing the bioactive water, so that the polycyclic aromatic hydrocarbon in the soil polluted by the polycyclic aromatic hydrocarbon has a lower distribution coefficient in a soil slurry sample, and particularly, the bioactive water has stronger desorption capacity on the polycyclic aromatic hydrocarbon and can increase the amount of solute in a water phase, so that more polycyclic aromatic hydrocarbon can be dissolved in the bioactive water, and the subsequent biodegradation is convenient; moreover, the bioactive water is non-toxic, unlike organic solvents or surfactants and the like which may cause secondary pollution; in addition, the bioactive water can activate the metabolism of microorganisms and enhance the availability of the microorganisms, and the soil slurry is biodegraded by polycyclic aromatic hydrocarbon degrading bacteria on the basis of the bioactive water, so that the bioremediation efficiency is enhanced.
Description
Technical Field
The invention relates to the technical field of soil remediation, in particular to a remediation method of polycyclic aromatic hydrocarbon contaminated soil.
Background
With the development of society and the acceleration of industrialization process, the variety and the quantity of industrial three wastes are increased greatly, and the organic pollutants entering the soil are increased. Polycyclic Aromatic Hydrocarbons (PAHs) are a class of Persistent Organic Pollutants (POPs) commonly existing in soil (including saline-alkali soil and general soil), and have strong teratogenic, carcinogenic and mutagenic effects on human bodies and other organisms. Therefore, how to effectively repair PAHs contaminated soil becomes a great problem which is concerned about and needs to be solved in the field of domestic and foreign environmental protection in recent years.
Through research and application for more than 30 years, a PAHs polluted soil remediation technology system mainly comprising three remediation technologies of physical remediation, chemical-biological combined remediation and biological remediation is formed at present. Early bioremediation mainly refers to microbial remediation and is also one of the earliest, deepest and currently most widely applied bioremediation methods. The environmental system for repairing the pollution by using the microorganisms is more effective and economical, and becomes an important clean environment-friendly technology. Microorganisms are the subject of bioremediation and play an important role in the process of migratory transformation and even eventual removal of contaminants. Microbial remediation essentially exploits the metabolic capacity and genetic diversity of microorganisms to convert pollutants into non-polluting end products that can re-enter the earth's biochemical cycle.
Currently, the remediation of PAHs contaminated soil by microbial remediation technology should consider the bioavailability (bioavailabilty), wherein the microorganisms utilize several possible mechanisms of organic compounds, including: first, microorganisms metabolize organic compounds dissolved in an aqueous phase; secondly, the microorganisms directly contact with the absorbed organic compounds in the soil particles to consume the matrix; and thirdly, the microorganism secretes extracellular enzymes or extracellular polymers such as EPS and the like for biodegradation or biodegrades after adsorbing pollutants. In order to improve or enhance the efficiency of microbial remediation techniques, surfactants and the like are generally added to enhance desorption of organic contaminants, increase water solubility, and improve bioavailability. However, this easily causes a problem of secondary pollution, and the bioremediation efficiency is to be improved.
Disclosure of Invention
The invention aims to provide a remediation method of polycyclic aromatic hydrocarbon contaminated soil, which is green and environment-friendly and has a good remediation effect.
In order to achieve the above object, the present invention provides the following technical solutions:
the invention provides a remediation method of polycyclic aromatic hydrocarbon contaminated soil, which comprises the following steps:
mixing the polycyclic aromatic hydrocarbon polluted soil with bioactive water to obtain soil slurry;
and (3) inoculating polycyclic aromatic hydrocarbon degrading bacteria to the soil slurry and then performing biodegradation.
Preferably, the raw material for preparing the soil slurry also comprises a nutrient substrate.
Preferably, the content of salt in the polycyclic aromatic hydrocarbon-polluted soil is less than or equal to 15 percent.
Preferably, the soil species of the polycyclic aromatic hydrocarbon-contaminated soil include loess, black soil or sandy soil.
Preferably, the salt content in the soil mud is less than or equal to 12 percent.
Preferably, the salt content in the soil mud is less than or equal to 6 percent.
Preferably, the inoculation amount of the polycyclic aromatic hydrocarbon degrading bacteria is 1-10%.
Preferably, the temperature of biodegradation is 15-45 ℃ and the time is 1-15 d.
The invention provides a remediation method of polycyclic aromatic hydrocarbon contaminated soil, which comprises the following steps: mixing the polycyclic aromatic hydrocarbon polluted soil with bioactive water to obtain soil slurry; and (3) inoculating polycyclic aromatic hydrocarbon degrading bacteria to the soil slurry and then performing biodegradation. According to the invention, the soil polluted by the polycyclic aromatic hydrocarbon is made into the soil slurry by utilizing the bioactive water, so that the polycyclic aromatic hydrocarbon in the soil polluted by the polycyclic aromatic hydrocarbon has a lower distribution coefficient in a soil slurry sample, and particularly, the bioactive water has stronger desorption capacity on the polycyclic aromatic hydrocarbon and can increase the amount of solute in a water phase, so that more polycyclic aromatic hydrocarbon can be dissolved in the bioactive water, and the subsequent biodegradation is convenient; moreover, the bioactive water is non-toxic, unlike organic solvents or surfactants and the like which may cause secondary pollution; in addition, the bioactive water can activate the metabolism of microorganisms and enhance the availability of the microorganisms, and the soil slurry is biodegraded by polycyclic aromatic hydrocarbon degrading bacteria on the basis of the bioactive water, so that the bioremediation efficiency is enhanced.
Drawings
FIG. 1 is a graph comparing the solubility of NaCl in bioactive water and distilled water;
FIG. 2 is a graph comparing distribution coefficients in a fluoranthene gradient contaminated soil mud sample;
FIG. 3 is a graph showing the bioremediation effect of soil contaminated by 6 PAHs;
FIG. 4 is a graph of the growth of degrading bacteria YN1 under different salt content conditions.
Biological preservation description:
classification and naming of degrading bacteria YN 1: bacillus parasuis; latin literature name: bacillus paramycoides; the preservation date is as follows: year 2019, month 06, day 10; the preservation unit: china general microbiological culture Collection center (CGMCC), national institute of sciences, No. 3, Xilu-1, Beijing, Chaoyang, North Chen, China; the preservation number is: CGMCC No.: 17911.
Detailed Description
The invention provides a remediation method of polycyclic aromatic hydrocarbon contaminated soil, which comprises the following steps:
mixing the polycyclic aromatic hydrocarbon polluted soil with bioactive water to obtain soil slurry;
and (3) inoculating polycyclic aromatic hydrocarbon degrading bacteria to the soil slurry and then performing biodegradation.
The soil mud is obtained by mixing the polycyclic aromatic hydrocarbon polluted soil and bioactive water. In the invention, the polycyclic aromatic hydrocarbon-polluted soil specifically refers to any soil polluted by polycyclic aromatic hydrocarbon and needing to be repaired; the salt content in the polycyclic aromatic hydrocarbon-polluted soil is not specially limited, the saline-alkali soil (the salt content is more than or equal to 0.7%) or the common soil (the salt content is less than 0.7%) can be adopted, and particularly, the salt content in the polycyclic aromatic hydrocarbon-polluted soil is preferably less than or equal to 15%. The soil type of the polycyclic aromatic hydrocarbon-polluted soil is not particularly limited, and the soil can be any soil, specifically, loess, black soil or sandy soil. The invention has no special limitation on the types of the polycyclic aromatic hydrocarbons in the polycyclic aromatic hydrocarbon polluted soil, such as naphthalene, fluorene, phenanthrene, anthracene, fluoranthene, pyrene and the like. In the invention, the polycyclic aromatic hydrocarbon polluted soil is preferably screened by a pharmacopoeia sieve with the aperture of 2mm, and the part under the sieve is taken for use.
In the present invention, the method for preparing the biologically active water (BW) preferably comprises the steps of:
mixing turfy soil, bentonite, calcium alginate, cement and water, and curing and molding the obtained mixed slurry to obtain a molded mixture;
and placing the molding mixture and the pumice in water for aeration to obtain the bioactive water.
The turfy soil, the bentonite, the calcium alginate, the cement and the water are preferably mixed, and the obtained mixed slurry is solidified and formed to obtain a forming mixture. The invention has no special limitation on the types and sources of the turfy soil, the bentonite, the calcium alginate and the cement, and can adopt commercial products well known by the technicians in the field; wherein the pH value of the turfy soil is preferably 5.47.
In the invention, the mass ratio of the turfy soil, the bentonite, the calcium alginate and the cement is preferably (30-50): (10-30): (0.2-1): (10-20), more preferably (35-45): (15-25): (0.5-0.8): (12-17), more preferably 40: 20: 0.6: 15. the amount of water used in the preparation of the molding mixture is not particularly limited, and the turfy soil, the bentonite, the calcium alginate and the cement can be mixed together to form slurry with proper hardness, so that the molding mixture can be prepared by further curing molding.
In the embodiment of the invention, turfy soil, bentonite, calcium alginate and cement are mixed, then a proper amount of water is sprayed under the stirring condition to form mixed slurry with proper hardness, and the mixed slurry is added into a mold to be cured and molded to obtain a molding mixture. The stirring speed is not specially limited, and all the materials can be uniformly mixed. The shape and size of the molding compound are not particularly limited, but preferably the molding compound is a cylindrical shape having a length of 10cm and a diameter of 2.5 cm. The invention has no special limitation on the curing and molding operation parameters, and can ensure that the turfy soil, the bentonite and the calcium alginate are bonded together after the cement is cured to obtain the molding mixture.
After the forming mixture is obtained, the forming mixture and the pumice are placed in water for aeration to obtain the bioactive water. In the present invention, the mass ratio of the molding compound to pumice is preferably 1: (1.5-2.5), more preferably 1: 2. in the invention, the size of the pumice is preferably 2-10 cm. When the aeration is carried out, the volume ratio of the total mass of the forming mixture and the pumice to the water is preferably (30-40) g: 1000mL, more preferably 36 g: 1000 mL. The invention preferably uses an air pump for aeration, and the flow rate of the air is preferably more than 0.5L/min, more preferably 0.55-0.60L/min; the time of aeration is preferably 4-7 d, and more preferably 4-5 d.
After the aeration is finished, the forming mixture and the pumice in the system are preferably filtered and removed, and the obtained water is the bioactive water.
After the bioactive water is obtained, the soil polluted by the polycyclic aromatic hydrocarbon and the bioactive water are mixed to obtain soil slurry. In the invention, the content of salt in the soil slurry is preferably less than or equal to 12%, more preferably less than or equal to 6%, even more preferably 2-6%, and even more preferably 4%. Specifically, when the salt content of the polycyclic aromatic hydrocarbon-polluted soil is less than or equal to 8%, the polycyclic aromatic hydrocarbon-polluted soil and the bioactive water are preferably mixed according to the weight ratio of 1 g: (0.5-2) mL (NaCl or other salts can be properly added to ensure that the salt content in the soil slurry is 2-4%) to obtain soil slurry; when the salt content of the polycyclic aromatic hydrocarbon-polluted soil is more than 8%, the polycyclic aromatic hydrocarbon-polluted soil is preferably diluted by water until the salt concentration is 8-12%, and then the obtained diluted soil and bioactive water are mixed according to the weight ratio of 1 g: (0.5-2) mL to obtain soil slurry, wherein the water used for diluting the polycyclic aromatic hydrocarbon-polluted soil is not particularly limited, and the water well known to a person skilled in the art can be used, and the underground water can be used in actual production.
In the invention, the raw materials for preparing the soil mud preferably also comprise a nutrient substrate, and specifically, the soil polluted by the polycyclic aromatic hydrocarbon, the bioactive water and the nutrient substrate are mixed to obtain the soil mud; the invention has no special limit on the type and the dosage of the nutrient medium, and can be obtained by adopting a conventional inorganic salt culture medium; the present invention utilizes a nutrient medium to provide conditions for the growth of microorganisms.
In the invention, the temperature of mixing the materials is preferably 15-45 ℃ and the time is preferably 24-48 h when the soil slurry is prepared. According to the invention, the components are preferably mixed under a bottle rolling condition, and specifically, a mixed material obtained by mixing the components is placed on a table type bottle rolling device for balance treatment; in the balance treatment process, all the components are fully mixed, and under the action of bioactive water, part of polycyclic aromatic hydrocarbon in the polycyclic aromatic hydrocarbon polluted soil is desorbed into a water phase, so that subsequent biodegradation is facilitated.
After soil slurry is obtained, the soil slurry is inoculated with polycyclic aromatic hydrocarbon degrading bacteria and then is subjected to biodegradation. The specific types of the polycyclic aromatic hydrocarbon degrading bacteria are not particularly limited, and the degradation of polycyclic aromatic hydrocarbons can be realized. In the invention, the inoculation amount of the polycyclic aromatic hydrocarbon degrading bacteria is preferably 0.5-10% (v/v). In the embodiment of the invention, in order to verify the effectiveness of the method provided by the invention, the soil slurry prepared from the polycyclic aromatic hydrocarbon-polluted soil is biodegraded by using degrading bacteria YN 1; the preservation number of the degrading bacteria YN1 is CGMCC No.: 17911.
in the invention, the temperature of biodegradation is preferably 15-45 ℃; in the examples of the present invention, the biodegradation is carried out in particular under room temperature conditions; the time for biodegradation is preferably 1-15 d, and more preferably 2-10 d. The invention preferably performs biodegradation under the condition of roller bottle, and specifically, soil slurry is inoculated with polycyclic aromatic hydrocarbon degrading bacteria and then placed on a table type roller bottle device for biodegradation; in the biodegradation process, polycyclic aromatic hydrocarbon in the system is degraded by polycyclic aromatic hydrocarbon degrading bacteria, and the amount of solute in the water phase can be increased due to the strong desorption capacity of the bioactive water on the polycyclic aromatic hydrocarbon, so that more polycyclic aromatic hydrocarbon is dissolved in the bioactive water, the polycyclic aromatic hydrocarbon degrading bacteria can be conveniently biodegraded, and the bioremediation efficiency can be enhanced.
The technical solution of the present invention will be clearly and completely described below with reference to the embodiments of the present invention. It is to be understood that the described embodiments are merely exemplary of the invention, and not restrictive of the full scope of the invention. All other embodiments, which can be derived by a person skilled in the art from the embodiments given herein without making any creative effort, shall fall within the protection scope of the present invention.
Example 1
1. Preparation of bioactive water
Mixing 40g of turfy soil (pH value is 5.47), 20g of bentonite, 0.6g of calcium alginate and 15g of cement, then spraying a proper amount of distilled water under the stirring condition to form mixed slurry with proper hardness, and adding the mixed slurry into a mold for curing molding to obtain a molding mixture; and (3) putting 12g of the forming mixture and 24g of pumice into 1000mL of distilled water, aerating for 4d by using an air pump under the condition that the flow is 0.55L/min, and filtering to remove the forming mixture and the pumice to obtain the Bioactive Water (BW).
2. NaCl solubility analysis
Taking 100mL of bioactive water for useFiltering with GF/C filter paper (Whatman 1822-047), taking 25mL of the obtained filtrate into 3 100mL beakers respectively, placing the beakers on a heatable magnetic stirrer for stirring, keeping the temperature of the bioactive water at 30 ℃, slowly adding NaCl solid until the NaCl solid can not be dissolved, placing the beakers in a refrigerator at 4 ℃ for cooling, observing once every 5min, if NaCl crystals are separated out, keeping the solution in a saturated state, and standing the saturated solution at 30 ℃ for 10 min. 5mL of supernatant from each of the three beakers was pipetted into 3 known masses (m)1G) in a constant temperature oven at 100 deg.C, drying for 45min in a drier, and weighing2In g), the solubility of NaCl in bioactive water at 30 ℃ can be calculated from formula I:
S＝(m2-m1) V × n is formula I;
in the formula I, S is solubility and the unit is g/100 mL;
m1weighing the mass of the bottle, wherein the unit is g;
m2the total mass of NaCl and the weighing bottle is g;
v is the volume of the supernatant, and is specifically 5 mL;
n is a reduced dilution factor, specifically 20.
The solubility of NaCl in Distilled Water (DW) at 30 ℃ was determined as described above.
FIG. 1 is a comparison graph of the solubility of NaCl in bioactive water and distilled water (error bars in the graph are standard deviations), and it can be seen from FIG. 1 that the solubility of NaCl in bioactive water is 34g/100mLBW, the solubility of NaCl in distilled water is 32g/100mL DW, and the solubility of NaCl in bioactive water is higher than that of distilled water, which indicates that the solubility of NaCl in bioactive water is increased, and further, the utilization of NaCl by microorganisms is more facilitated.
3. Analysis of the contaminant washing action of biologically active water and determination of the partition coefficient
The ratio of the concentration of the compound adsorbed in the soil to the concentration of the compound in the water, i.e., the distribution coefficient, is expressed by Kd, which is expressed by the formula II:
kd ═ Cs/Cc formula II;
in formula II, Cs and Cc are equilibrium concentrations of organic compounds in soil and water, respectively.
Respectively weighing 5g of loess, black soil and sandy soil (respectively collected in a later mountain of Yanbian university, a black land of Heilongjiang and a 29682g; Chun Fangchuan dune; passing through a pharmacopoeia sieve with the aperture of 2mm, and taking the part under the sieve for use) into 20mL of sample bottles, respectively and sequentially adding 2.5 muL, 5 muL, 10 muL, 16.25 muL, 20 muL and 25 muL of fluoranthene standard solution (2.0000mg/mL), 1-10 mg/kg of gradient pollution, respectively adding 5mL of Bioactive Water (BW), ultra-pure water (UPW), Distilled Water (DW), mineral water (obtained from spring) and tap water into each sample bottle, and placing the obtained soil slurry sample on a table type bottle rolling device for balance treatment for 48 hours; and then carrying out solid-liquid separation on the obtained system to obtain an aqueous phase and a solid phase, and analyzing the concentration of fluoranthene in the aqueous phase and the solid phase by using HPLC (high performance liquid chromatography), wherein the HPLC analysis conditions comprise:
liquid chromatography column: ZORBAX Eclipse PAH (4.6 mm. times.250 mm, 5 μm);
column temperature: 35 ℃;
mobile phase: the volume ratio of the acetonitrile to the ultrapure water is 9: 1;
flow rate: 1.0 mL/min;
UV detection wavelength: 220 nm;
sample introduction amount: 10 μ L.
Fig. 2 is a distribution coefficient comparison graph in a fluoranthene gradient contaminated soil slurry sample, and as can be seen from fig. 2, the distribution coefficient (Kd) of fluoranthene in a soil slurry sample prepared from 5 kinds of water is as follows: BW < UP < DW < mineral water < tap water, which shows that the Kd value of fluoranthene in the bioactive water is minimum, the desorption capacity to organic matters is strong, the availability of microorganisms can be enhanced, and the degradation of the microorganisms is promoted.
4. Bioremediation of polycyclic aromatic hydrocarbon polluted general soil by utilizing bioactive water
Experimental groups: respectively weighing 5g of loess, black soil and sandy soil (respectively collected in the rear mountain, the black Longjiang black land and the 29682;, Chun Fang Chuan sand dune; passing through a pharmacopoeia sieve with the aperture of 2mm, and taking the part under the sieve for use) into a 20mL sample bottle, respectively adding 5 muL of fluoranthene standard solution (2.0000mg/mL) to ensure that the fluoranthene pollution concentration in the soil is 2mg/kg, and taking the soil as the soil to be repaired for later use;
mixing the soil to be repaired, 5mL of bioactive water and a nutrient medium (MSM), placing the obtained mixed material on a table type roller bottle device, and carrying out balance treatment for 48 hours at room temperature to obtain soil slurry;
the soil slurry is inoculated with degrading bacteria YN1 (preservation number CGMCC No.: 17911, inoculum size is 2%, v/v), and then placed on a bench roller bottle device for biodegradation for 48h at room temperature.
Setting a control group: distilled water is adopted to replace bioactive water to prepare soil slurry, and other conditions are consistent with the experimental formula method.
The concentrations of fluoranthene remaining in the systems obtained after biodegradation in the experimental group and the control group were analyzed by HPLC to obtain the biodegradation rates of fluoranthene in different soil samples, which is specifically shown in table 1.
TABLE 1 biodegradation rates of fluoranthene in different soils
As can be seen from Table 1, compared with the control group (soil + DW), the three soil muds all show the phenomenon of improved degradation rate in the experimental group (soil + BW), which indicates that the bioactive water plays a role in promoting the bioremediation of the soil polluted by the polycyclic aromatic hydrocarbon. In the three soil slurry tests, compared with a control group, the bioactive water of the experimental group plays the highest role in the loess sample test, and the degradation rate is improved by more than 70%.
5. Bioremediation of 6 PAHs (naphthalene, fluorene, phenanthrene, anthracene, fluoranthene and pyrene respectively) polluted soil by using degrading bacteria YN1
According to the above experimental method, loess is contaminated by 6 kinds of PAHs, and prepared into soil slurry for biodegradation experiment, and the specific result is shown in FIG. 3. As can be seen from FIG. 3, the degrading bacteria YN1 all had degrading activity on 6 PAHs such as naphthalene, fluorene and anthracene, and the degrading bacteria BW all had an improved effect on the degradation of PAHs.
6. Influence of different salt concentration conditions on growth of degrading bacteria YN1
Adding NaCl into a nutrient medium (MSM) to prepare culture media with different salt concentrations of 0-15%, adding 0.1% (w/v) fluoranthene as a carbon source, inoculating 1% (v/v) of degrading bacteria YN1, shake culturing for 36h at 37 ℃ and 120r/min by using a shaking table, measuring OD600The specific results are shown in FIG. 4. As can be seen from FIG. 4, the range of suitable salt concentration for growth of the degrading bacterium YN1 is 2-6%, the optimum salt concentration condition is 4%, and the degrading bacterium YN1 can survive under the condition that the salt concentration is 0-15%.
7. Bioremediation of saline-alkali soil polluted by polycyclic aromatic hydrocarbon by utilizing bioactive water
Taking a certain amount of saline-alkali soil (the salt concentration is 10%) in a certain saline-alkali soil, respectively diluting the saline-alkali soil to 2.5 times and 1.5 times of the original saline-alkali soil by using DW to prepare quicksand-shaped saline-alkali soil, then taking the saline-alkali soil diluted by 2.5 times, diluted by 1.5 times and undiluted as a soil sample, and adopting fluoranthene for pollution according to a method in '4, carrying out bioremediation on general soil polluted by polycyclic aromatic hydrocarbon by using bioactive water' to obtain saline-alkali soil to be restored;
mixing a soil sample and bioactive water in a proportion of 1 g: 1mL of bioactive water is respectively added, the soil slurry is obtained after balanced treatment is carried out for 48 hours at room temperature, namely the salt concentration in the obtained soil slurry is respectively 2%, 4% and 5% (without dilution), then degradation bacteria YN1 are inoculated for carrying out biodegradation experiments, control experiments adopting distilled water, ultrapure water and added nutrient substrates are set according to the experimental grouping conditions in the table 2, and the results are specifically shown in the table 2.
TABLE 2 biodegradation rates of fluoranthene in saline-alkaline earths of different salt concentrations
As can be seen from Table 2, under the soil slurry conditions of 3 different diluted saline-alkali soils, the fluoranthene degradation rates are BW & gt BW + MSM & gt UPW + MSM & gt DW + MSM & gt UPW & gt DW, which shows that the Bioactive Water (BW) can effectively improve the degradation efficiency of fluoranthene in the saline-alkali soil.
The foregoing is only a preferred embodiment of the present invention, and it should be noted that, for those skilled in the art, various modifications and decorations can be made without departing from the principle of the present invention, and these modifications and decorations should also be regarded as the protection scope of the present invention.
Claims (8)
1. A remediation method of polycyclic aromatic hydrocarbon contaminated soil is characterized by comprising the following steps:
mixing the polycyclic aromatic hydrocarbon polluted soil with bioactive water to obtain soil slurry;
inoculating polycyclic aromatic hydrocarbon degrading bacteria to the soil slurry and then performing biodegradation;
the polycyclic aromatic hydrocarbon degrading bacteria are degrading bacteria YN1, and the preservation number of the degrading bacteria YN1 is as follows: CGMCC No.: 17911;
the preparation method of the bioactive water comprises the following steps:
mixing turfy soil, bentonite, calcium alginate, cement and water, and curing and molding the obtained mixed slurry to obtain a molded mixture; the mass ratio of the turfy soil to the bentonite to the calcium alginate to the cement is (30-50): (10-30): (0.2-1): (10-20);
placing the molding mixture and pumice in water for aeration to obtain bioactive water; the mass ratio of the molding mixture to the pumice stone is 1: (1.5-2.5), wherein the volume ratio of the total mass of the forming mixture and the pumice to the water is (30-40) g: 1000 mL; and the flow rate of air during aeration is more than 0.5L/min, and the aeration time is 4-7 d.
2. The remediation method of claim 1 wherein the feedstock from which the soil slurry is prepared further comprises a nutrient substrate.
3. The remediation method of claim 1, wherein the polycyclic aromatic hydrocarbon-contaminated soil has a salt content of 15% or less.
4. The remediation method of claim 3, wherein the soil species of the polycyclic aromatic hydrocarbon-contaminated soil comprises loess, black soil, or sandy soil.
5. The remediation method of any one of claims 1 to 4 wherein the soil slurry has a salt content of 12% or less.
6. The remediation method of claim 5 wherein the soil slurry has a salt content of 6% or less.
7. The method for repairing according to claim 1 or 2, wherein the amount of the polycyclic aromatic hydrocarbon-degrading bacteria inoculated is 1 to 10%.
8. The repair method according to claim 1 or 2, wherein the temperature of biodegradation is 15 to 45 ℃ for 1 to 15 days.
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| CN107746104A (en) * | 2017-09-30 | 2018-03-02 | 延边大学 | A kind of bioactive water and preparation method thereof |
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