Preparation and Modification of Biochar Materials and their Application in Soil Remediation
Abstract
:1. Introduction
2. Preparation and Modification of Biochar
2.1. Preparation of Biochar
2.1.1. Pyrolysis
2.1.2. Factors Affecting the Pyrolysis Process
2.1.3. Other New Methods
2.2. Modification of Biochar
2.2.1. Chemical Oxidation
2.2.2. Chemical Reduction
2.2.3. Metal Impregnation
2.2.4. Other Modification Methods
3. Removal Mechanism of Major Pollutants by Biochar
3.1. Ion Exchange
3.2. Physical Adsorption
3.3. Electrostatic Interaction
3.4. Precipitation
3.5. Complexation
4. Application of Biochar in Soil Remediation
4.1. Removal of Heavy Metals
4.2. Removal of Persistent Organic Pollutants (POPs)
4.3. Amelioration of Soil
4.4. Potential Risk of Biochar
5. Conclusions
Author Contributions
Funding
Acknowledgments
Conflicts of Interest
References
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Raw Material | Atmosphere | Temperature (°C) | Heating Rate (°C/min) | Residence Time (h) | Yield (%) | pH | Ash Content (%) | Surface Area (m2·g−1) | Total Pore Volume (cm3·g−1) | Pore Diameter (nm) | Reference |
---|---|---|---|---|---|---|---|---|---|---|---|
Herb residue | N2 | 400 | 10 | 3 | 37.9 | 10.2 | 28.3 | 49.2 | 0.042 | 3.39 | [38] |
600 | 31.2 | 10.1 | 31.1 | 51.3 | 0.051 | 3.99 | |||||
800 | 29.1 | 10.6 | 37.1 | 70.3 | 0.068 | 3.87 | |||||
Sesame straw | oxygen-limited | 400 | 5 | 2 | 35.6 | 30.77 | 37.2 | 0.0542 | [24] | ||
500 | 28.2 | 28.54 | 46.9 | 0.0716 | |||||||
600 | 22.9 | 21.98 | 289.2 | 0.1433 | |||||||
Corn straw | N2 | 600 | 3 | 10.0 | 5.02 | 61.0 | 0.036 | 23.7 | [39] | ||
Pine cone | N2 | 500 | 1 | 4.66 | 2.13 | 6.6 | 0.016 | [40] | |||
Rice-husk | 450–500 | 7.0 | 42.2 | 34.4 | 0.028 | [41] | |||||
Hickory wood | N2 | 450 | 10 | 2 | 28.5 | 7.9 | 6.47 | 12.9 | [42] | ||
600 | 22.7 | 8.4 | 4.18 | 401.0 | |||||||
Bagasse | N2 | 450 | 10 | 2 | 28.0 | 7.5 | 13.68 | 13.6 | |||
600 | 26.5 | 7.5 | 15.36 | 388.3 | |||||||
Bamboo | N2 | 450 | 10 | 2 | 26.3 | 8.5 | 8.83 | 10.2 | |||
600 | 24.0 | 9.2 | 11.86 | 375.5 | |||||||
Poplar chips | N2 | 550 | 5 | 2 | 23.18 | 7.56 | 212.58 | 0.356 | 6.70 | [43] | |
Burcucumber plants | oxygen-limited | 700 | 7 | 2 | 27.52 | 12.23 | 43.72 | 2.31 | 0.008 | 6.780 | [44] |
Pine wood | N2 | 600 | 10 | 1 | 4.02 | 209.6 | 0.003 | [45] | |||
Orange peel | oxygen-limited | 400 | 5 | 6 | 11.3 | 6.93 | 28.1 | 0.0409 | 2.9 | [29] | |
700 | 5 | 6 | 5.93 | 14.9 | 501 | 0.390 | 1.6 | ||||
Marine macroalgae | N2 | 450 | 5 | 2 | 1.05 | 0.007 | 30.41 | [46] | |||
Municipal solid waste | N2 | 400 | 0.5 | 8.0 | 6.1 | 20.7 | 0.027 | [47] | |||
500 | 0.5 | 8.5 | 9.2 | 29.1 | 0.039 | ||||||
600 | 0.5 | 9.0 | 6.2 | 29.8 | 0.038 | ||||||
Rice straw | oxygen-limited | 700 | 2 | 58.97 | 369.26 | 0.23 | [48] | ||||
Swine manure | oxygen-limited | 700 | 2 | 60.73 | 227.56 | 0.14 | |||||
Auricularia auricula dreg | 400 | 2 | 0.55 | 77.64 | 0.0612 | 4.837 | [49] | ||||
Thalia dealbata | N2 | 500 | 4 | 10.09 | 22.0 | 7.1 | [50] | ||||
Corn straw | N2 | 500 | 1.5 | 41.0 | 32.85 | 0.0148 | 5.01 | [51] | |||
Pitch pine | oxygen-free | 400 | 2 s | 33.5 | 7.9 | 4.8 | [52] | ||||
500 | 2 s | 14.4 | 7.7 | 175.4 | |||||||
Wheat straw | N2 | 600 | 10 | 3 | 5.65 | 38.1 | 0.051 | 19.9 | [53] | ||
Rice straw | N2 | 600 | 10 | 3 | 0.03 | 27.4 | 0.040 | 15.8 | |||
Digested sugar beet tailing | N2 | 600 | 10 | 2 | 45.5 | 9.95 | 336.0 | [54] | |||
Raw sugar beet tailing | N2 | 600 | 10 | 2 | 36.3 | 9.45 | 2.6 | ||||
tea waste | oxygen-limited | 700 | 7 | 2 | 28.35 | 10.87 | 342.22 | 0.0219 | 1.756 | [55] | |
N2 | 700 | 7 | 2 | 22.35 | 11.60 | 421.31 | 0.0576 | 1.904 |
Raw Material | Reagent | Pollutant | Modification Method | Modification Effects | Reference |
---|---|---|---|---|---|
Bamboo hardwoods | NaOH, CS2 | Cd | The composition of sulfur modified mixture solution was obtained by stirring NaOH and CS2. Biochar and sulfur modified mixture solution stirred at 45 °C for 8 h. | Sulfur-modified biochar (S-BC) has more roughness, with a more granular massive structure than that seen on the pristine biochar. | [76] |
FeSO4 | S-BC was added to FeSO4 solution and then stirred for 16 h with magnetic stirrer at 40 °C, and cooled slowly to room temperature and filtered through 0.45 μm filters. The feedstock was oven-dried at 40 °C. | Successful impregnation of sulfur and iron onto the SF-BC surface, and it showed various atomic proportions of sulfur and iron, with biochar ranging from 0.48% to 4.66% and 0.44% to 22.25%, respectively. | |||
Poplar chips | AlCl3 | NO3−, PO43− | The poplar pieces were impregnated into AlCl3 solutions with different concentrations for 6 h. The mixtures were dried at 80 °C for 48 h. The pretreated pristine poplars were pyrolyzed under the N2 atmosphere at 550 °C with a heating rate of 5 °C/min, and the peak temperature was maintained for 2 h. | The biochar yield increased after modification with Al. The carbon content of the Al-modified biochar significantly decreased compared with the pristine biochar. The BET surface area significantly increased with the Al content of the biochar. NO3− and PO43− adsorptions significantly improved on the Al-modified biochar. | [43] |
Rice straw, swine manure | H3PO4 | Tetracycline (TC) | Biochars were immersed in H3PO4 solution for 24 h at 25 °C. Then, the H3PO4 modified biochars were washed by distilled water until the pH of supernatants was stable. Finally, the supernatants were discarded and the biochars were oven-dried overnight at 105 °C. | The H3PO4 modification enhanced the surface area of biochars produced from rice straw biochar (RC) and swine manure biochar (SC). Compared with SC, modified SC presented higher total pore, micropore and mesopore volume by 0.25 to 0.14, 0.09 to 0.07, 0.17 to 0.07cm3·g−1), but there was no change between RC and RCA modification. | [48] |
Wheat straw, cow manure | HNO3 | U(VI) | Biochar powders were treated with 300 mL 25% HNO3 solution at 90 °C for 4 h. The excess acid was removed by centrifugation. All oxidized biochar samples were washed with deionized distilled water, freeze-dried, and milled to <0.25 mm. | Owing to the higher contents of surface COO groups and more negative surface charge, the modified biochar showed enhanced U(VI) adsorption ability than the unmodified biochar. The maximum adsorption capacity of U(VI) by the oxidized wheat straw biochar showed an improvement of 40 times relative to the untreated biochar. | [77] |
Auricularia auricular dreg (AAD) | cetyltrimethyl ammonium bromide (CTAB) | Cr(VI) | Mixed 5 g of dried AAD biochar with 250 mL of 3.0% CTAB solution in 25 °C for 2 h. Residual CTAB rinsed with deionized water and the material was dried at 70 °C until the weight remained constant. | After modification, the surface area increased 6.1% and the average pore diameter increased 16.5% (77.64 m2/g and 48.37 Å). Moreover, the number of mesoporous and micropores in unit area increased obviously. The adsorption rate and quantity of modified AAD biochar were 6.4% and 8.0% higher than those of AAD biochar, respectively. | [49] |
Thalia dealbata | MgCl2 | sulfamethoxazole (SMX), Cd | Thalia dealbata were soaked in 100 mL 1 M MgCl2 solution, after 0.5 h mixing under magnetic stirring, the pre-treated biomass was then separated from the solution and pyrolyzed at 500 °C. | The surface area of MgCl2 modified biochar (BCM, 110.6 m2·g−1) was higher than untreated biochar (BC, 7.1 m2·g−1). The addition of BCM increased the sorption of SMX (by 50.8–58.6%) and Cd (by 24.2–25.6%) as compared with BC. In situ remediation with BCM decreased the mobility and bioavailability of SMX and Cd in sediments. | [50] |
Corn straw | Na2S and KOH | Hg(II), atrazine | Biochar were mixed with 500 mL of 2 M Na2S or 2 M KOH solution and stirred for 4 h. The suspension was then filtered and washed with deionized water for several times until the pH of the filtrate was nearly 7. The washed biochar was dried overnight in an oven at 105 °C. | Sulfur content significantly increased by 101.29% under Na2S modification. Compared to untreated biochar (BC, 32.85 m2·g−1), chemical modification increased the BET surface area which was 55.58 and 59.23 m2·g−1 for Na2S modified biochar (BS), KOH modified biochar (BK), respectively. In comparison to BC, the sorption capacity of BS and BK for Hg (II) increased by 76.95%, 32.12%, while that for atrazine increased by 38.66%, 46.39%, respectively. | [51] |
Coconut shell | HCl+ultrasonication | Cd, Ni and Zn | 5 g of CS biochar and 250 mL of 1 M HCl were mixed in beaker and ultrasonicated for 3 h with interval stirring. Then, the material was filtered, washed, and dried to constant weight. | Modified coconut shell biochar (MCSB) improved surface functional groups and microcosmic pore structure of pristine biochar (CSB). | [78] |
Dairy manure | NaOH | Pb and Cd | Biochar and 2 M NaOH were thoroughly mixed with a solid–liquid ratio of 1:5 and then were re-suspended for 12 h with a speed of 30 r min−1 at 65 °C. After that, the mixture was filtered, and the precipitate was collected and rinsed with deionized. Finally, material was dried at 105 °C. | The NaOH treatment increased the specific surface area, ion-exchange capacity, and the number of oxygen-containing functional groups of biochar. The adsorption capacities of biochar for Pb and Cd increased after modification. The highest sorption capacities were 175.53 and 68.08 mg·g−1, for Pb and Cd, respectively. | [79] |
Raw Material | Pollutant | Mechanism | Reference |
---|---|---|---|
Municipal sewage sludge | Cd | Surface precipitation under alkaline conditions and exchange of exchangeable cations with Cd. | [95] |
Fertilizer | Cu, Zn and Cd | Precipitate from CO32−, PO43− on the surface of the biochar, partially by surface complexing with -OH group or delocalized π electron. | [92] |
Rice husk loaded with manganese oxide | Pb | Oxide spherical complexes and biochar surface oxygen complexes; the π-band electron density of graphene-based carbon in the π-electron cloud system reduces vacancies on the surface of biochar, thereby adsorbing Pb2+. | [96] |
Wheat straw, pine needles | Zn | The components of -OH, CO32-, and Si in biochar can form precipitates with Zn2+. | [97] |
Bamboo, eucalyptus | chloramphenicol | Electron-donor-acceptor (EDA) interaction with pH < 2.0, also forms charge-assisted hydrogen bonds (CAHB) and hydrogen bonds at pH 4.0–4.5, and interaction with CAHB and EDA at pH > 7.0. | [98] |
Corn straw | Hg(II), atrazine | After Na2S modification, sulfur impregnated onto the biochar reacted with Hg(II) to form HgS, which greatly facilitated the sorption of Hg(II). Formation of surface complexes between Hg(II) and the functional groups of sorbent, such as phenolic hydroxyl, carboxylic groups. These oxygen-containing functional groups exchanged ion with Hg(II). The electrostatic and EDA interaction also participated in Hg(II) sorption. | [51] |
Dairy manure | Pb and Cd | Because of the easy hydrolysis of Pb at low pH, biochar has a higher affinity for Pb than Cd. Besides, precipitation as carbonate minerals (2PbCO3·Pb(OH)2 and CdCO3) and complexation with functional groups such as carboxyl and hydroxyl, were also important for adsorption of Pb and Cd by biochar. | [79] |
Rice straw, swine manure | Tetracycline (TC) | The H-bonding, electrostatic attraction and EDA interaction might be the primary mechanism during adsorption process. | [48] |
Sugar beet tailing (SBT) | Cr(VI) | First, SBT biochar reduced Cr(VI) to Cr(III) by electrostatic adsorption. Second, with the participation of hydrogen ions and the electron donors from SBT biochar, Cr(VI) was reduced to Cr(III). Then, the function groups on the SBT biochar complexed with Cr(III). | [99] |
Empty fruit bunch, rice husk | As(III), As(V) | Surface complexes were formed between As(III) and As(V) and the functional groups (hydroxyl, carboxyl, and C–O ester of alcohols) of the two biochars. | [100,101] |
Bamboo biomass | Sulfathiazole, sulfamethoxazole, sulfamethazine | The sorption of neutral sulfonamide species occurred mainly due to H-bonds followed by EDA, and by Lewis acid-base interaction. EDA was the main mechanism for the sorption of positive sulfonamides species. The sorption of negative species was mainly due to proton exchange with water forming negative CAHB, followed by the neutralization of -OH groups by H+ released from functionalized biochar surface, and π–π electron-acceptor–acceptor (EAA) interaction. | [102] |
Raw Material | Tested Soil | Pollutant | Remediation Effect | Reference |
---|---|---|---|---|
Bamboo, rice straw, and Chinese walnut shell | industrial contaminated soil | Cu | Cu uptake in roots was reduced by 15%, 35%, and 26%, respectively. Rice straw biochar reduced solubility of Cu and Pb. | [107] |
Sewage sludge | Brazil soil | Cd, Pb, and Zn | Biochar reduced the concentration and bioavailable levels of Cd, Pb, and Zn of in the leachates. | [108] |
Poultry litter | paddy soil near Zn and Pb mines | Cd, Cu, Zn, Pb | Acid-soluble Cd in soils amended with poultry litter biochar was 8% to 10% lower than in the control polluted soil. | [109] |
Wheat straw | acid soil | Cd and Cu | Cu concentration in wheat roots was reduced most efficiently to 40.9% by biochar. Available Cd and Cu in soil added biochar decreased 18.8% and 18.6%. | [110] |
Rice husk | saturated soil, dryland soil | Cd | The adsorption of Cd on saturated soil increased by 21–41%, and that on dryland soil increased by 38–54%. | [111] |
Gliricidia sepium | shooting range soil | Pb, Cu | The addition of biochar to the soil reduced the dissolution rates of Pb and Cu by 10.0–99.5% and 15.6–99.5%, respectively, and was able to fix Pb and Cu released by protons and ligands in the soil. | [112] |
Poultry manure, cow manure, and sheep manure | farmland soil | Cr(VI) | Poultry manure decreased61.54 mg·kg−1 Cr(VI) in acidic soil and 73.93 mg·kg−1 Cr(VI) in alkaline soil. Cow and Sheep manure decreased by 66.61, 58.67, and 57.81, 68.15 mg·kg−1 Cr(VI) in acidic and alkaline soil, respectively. | [113] |
Raw Material | Modification | Pollutant | Tested Soil | Remediation Effect | Reference |
---|---|---|---|---|---|
Bamboo hardwoods | sulfur-iron | Cr | plant farmland | Sulfur-modified biochar (S-BC) and sulfur-iron modified biochar (SF-BC) addition increased the content of soil organic matter, alpha diversity indices, and changed soil bacterial community structure. The exchangeable Cd in soil was decreased by 12.54%, 29.71%, 18.53% under the treatments of BC, S-BC, SF-BC, respectively. | [76] |
Poultry, cow, sheep manure | Chitosan, ZVI | Cr | uncontaminated surface soil | Modified sheep manure biochar reduced Cr(VI) by 55%, and poultry manure modified biochar reduced Cr(VI) by 48%. | [113] |
corn straw | Fe-Mn | As | paddy soil | Modified biochar decreased the content of available As, increased the residual, amorphous hydrous oxide-bound, and crystalline hydrous oxide-bound As forms. | [115] |
Eucalyptus wood and poultry litter | iron | Cd, Cu, Zn, Pb | paddy soil near Zn and Pb mines | Acid-soluble Cd, Zn, Cu in soils amended with poultry litter biochar (PLB) was 8% to 10%, 27% to 29%, 59% to 63%, respectively, lower than in the control polluted soil. Plant biomass increased by 32% in the treatments containing magnetic PLB. | [109] |
Coconut shell | HCl + ultrasonication | Cd, Ni, and Zn | topsoil of paddy fields | In groups with 5% MCSB addition, the acid soluble Cd, Ni and Zn decreased by 30.1%, 57.2%, and 12.7%, respectively. | [78] |
Rice husk | Sulfur | Hg | Hg contaminated soil | Modification increased the Hg2+ adsorptive capacity of biochar by 73%, to 67.11 mg·g−1. And freely available Hg in TCLP (toxicity characterization leaching procedure) leachates by 95.4%, 97.4%, and 99.3%, respectively, compared to untreated soil. | [116] |
Corn straw | MnO | As | red soil | Modified biochar (MBC) in red soil had a much greater sorption capacity for As(III) than pristine biochar, although both enhanced the sorption of As(III) in red soil. | [117] |
Raw Material | Tested Soil | Pollutants | Remediation Effect | Reference |
---|---|---|---|---|
Fir wood chips | rice soil | 2,4-dichlorophenol, phenanthrene | Reduced the degradation and mineralization of both pollutants. Increased the accumulation of their metabolites in soil. | [118] |
Mixed wood shavingsRice husk | loamy agricultural soil | Pyrene, polychlorinated biphenyl and dichlorodiphenyldichloroethylene (DDE) | At the biochar dose of 10%, bioavailability and accessibility by 37% and 41%, respectively, compared to unamended soil. | [119] |
Rice hull | loamy clay, sandy loam, clay loam | oxyfluorfen | Oxyfluorfen degraded faster in biochar amended soil than in unamended soil. Biochar decreased the oxyfluorfen uptake by soybean plants by 18–63%, and the adsorption capacity of oxyfluorfen by soybean decreased. | [120] |
Orchard pruning biomass | vineyard | PAHs | During the investigated period, PAH concentrations decreased with time and the change resulted more intense for light PAHs. The soil properties (TOC, pH, CEC, bulk density) were modified after two consecutive applications | [121] |
Corn straw and bamboo | soil contaminated with PAHs | PAHs | The bioaccumulation of PAHs in rice roots was reduced, especially high molecular weight PAHs. The total and bioavailable concentration of PAHs in the soil treated with corn straw biochar were both lower than that of the control group. | [100] |
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Yang, X.; Zhang, S.; Ju, M.; Liu, L. Preparation and Modification of Biochar Materials and their Application in Soil Remediation. Appl. Sci. 2019, 9, 1365. https://doi.org/10.3390/app9071365
Yang X, Zhang S, Ju M, Liu L. Preparation and Modification of Biochar Materials and their Application in Soil Remediation. Applied Sciences. 2019; 9(7):1365. https://doi.org/10.3390/app9071365
Chicago/Turabian StyleYang, Xue, Shiqiu Zhang, Meiting Ju, and Le Liu. 2019. "Preparation and Modification of Biochar Materials and their Application in Soil Remediation" Applied Sciences 9, no. 7: 1365. https://doi.org/10.3390/app9071365