Engineered Biochar for Metal Recycling and Repurposed Applications
Abstract
:1. Introduction
2. Preparation and Characterization of Engineered Biochar
2.1. Feedstock Selection
2.2. Thermochemical Conversion Processes for Biochar Production
2.3. Surface Modification and Functionalization Methods
2.4. Characterization Techniques of Biochar Materials
3. Mechanisms of Metal Adsorption on Biochar
3.1. Physical Adsorption
3.2. Chemical Adsorption
3.2.1. Ion Exchange
3.2.2. Complexation
3.2.3. Electrostatic Attraction
3.2.4. Precipitation
3.2.5. Other Mechanisms
4. Factors Influencing Metal Adsorption Capacity of Biochar
4.1. Effect of Biochar Properties on Metal Adsorption
4.1.1. Surface Area and Porosity
4.1.2. Surface Functional Groups
4.2. Effect of Metal Characteristics
4.3. Environmental Conditions
4.3.1. Effect of pH
4.3.2. Effect of Temperature
4.3.3. Effect of Competing Ions
Factors | Description | Impact on Metal Adsorption | Example | Reference |
---|---|---|---|---|
Surface area | Total area available for metal ion binding on the BC surface | A larger surface area increases the number of active sites, enhancing adsorption | Increased surface area from 273.26 to 2372.51 m2/g improved Hg adsorption capacity | [85] |
Porosity | Micropores and mesopores in BC affect the accessibility of adsorption sites | Higher porosity improves accessibility and adsorption capacity | Alkali treatment of BC from Douglas fir enlarged micropores to mesopores, enhancing adsorption The KOH-activated BC effectively adsorbed Cr(VI), Pb(II), and Cd(II) with capacities of 127.2, 140.0, and 29.0 mg/g, respectively | [126] |
Functional groups | The chemical groups on BC that interact with metal ions | Different functional groups enhance interaction with specific metals | Cr(III) immobilized through complexation with the -COOH group of the modified BC | [127] |
Cation exchange capacity (CEC) | BC’s ability to exchange cations with metal ions | Higher CEC improves the BC’s ability to adsorb metal ions | CEC of all BC samples increased by 1.33 to 2.40 times post-modification, enhancing the immobilization efficiency for Cd(II) and Cu(II) | [59] |
Ionic radius | The size of the metal ion affects how easily it can fit into adsorption sites on BC | Smaller ionic radius may enhance adsorption due to better site fit | Cr(III) exhibited higher adsorption efficiency due to its smaller ionic radius (0.0615 nm) compared to Cu(II) (0.073 nm) and Zn(II) (0.074 nm) | [102] |
Charge | The electrical charge of metal ions influencing electrostatic interactions with BC | A higher charge can lead to stronger electrostatic attraction | The crayfish shell BC possessed a higher positive charge, resulting in stronger electrostatic interactions with As | [128] |
Speciation | The chemical form of the metal ion in solution, which affects its interaction with BC | Different species may have varying adsorption efficiencies | The speciation of arsenic significantly influences its removal efficiency; As(V) is more readily adsorbed compared to As(III) due to its greater stability and inertness | [100] |
Oxidation state | The oxidation state of the metal ion, which affects its reactivity and interaction with functional groups on BC | Different oxidation states influence the adsorption mechanisms | Cr(VI) reduction to Cr(III) impacts its adsorption on BC | [113] |
pH of the medium | The acidity or alkalinity of the solution affects the ionization of functional groups and metal speciation | pH changes can enhance or reduce adsorption depending on the metal type | Cationic metals such as Cu2+ increase with higher pH, while Cr(VI) adsorption decreases | [114,115] |
Temperature | The thermal condition of the environment affecting adsorption kinetics and capacity | Increased temperature can enhance or reduce adsorption depending on the process | Higher temperatures improved the adsorption capacity (160 mg/g) of U(VI) by BC | [117] |
Competing ions | The presence of other ions in the solution that can compete with metal ions for adsorption sites | A high concentration of competing ions can decrease metal adsorption | Anions (Cl−, SO42−, PO43−, and NO3−) in wastewater competed with Cr(VI) for adsorption sites, leading to a reduction in adsorption capacity | [127] |
5. Engineered Biochar for the Adsorption of Specific Types of Metals
5.1. Adsorption of Heavy Metals
Biochar Sources | Temperature (°C) | Procedure | Pollutant | Adsorption Capacity (mg/g) | Sorption Mechanism | Reference |
---|---|---|---|---|---|---|
Rice straw | 100–700 | Stepwise pyrolysis, including drying, grinding, and slow pyrolysis under anaerobic conditions. The BC was sonicated to form colloids | Cr(III) | 2.4–14.1 | Physical adsorption due to high specific surface area and functional groups | [136] |
Eupatorium adenophorum | 500 | Mixed with magnesium nitrate and ferric chloride, dried, and then pyrolyzed in an oxygen-free environment | Pb(II) | 252.70 | Precipitation and cation exchange | [137] |
Eupatorium adenophorumj | 500 | Mixed with magnesium nitrate and ferric chloride, dried, and then pyrolyzed in an oxygen-free environment | Cd(II) | 156.60 | Precipitation and cation exchange | [137] |
Sargassum hemiphyllum | 700 | Dried, ground, sieved, pyrolyzed in muffle furnace 10 °C·min−1 | Cu(II) | 75–120 | Physical sorption, ion exchange, surface complexation, surface precipitation, electrostatic interaction, metal–π interaction | [138] |
HFO-BC (BC with Fe(III) and NaOH treatment) | - | Treated with 1 mol/L FeCl3 solution, stirred in 5% NaOH solution, washed, dried | Cd(II), Cu(II) | 29.9, 34.1 | Inner-sphere complexation, migration from solution to adsorbent surface, pore diffusion | [139] |
Sulfonated BC (SBC) | 180 | Carbonization and sulfonation with A. compressus, H2SO4 treatment, washing, and drying | Pb(II), Cd(II) | 191.07, 85.76 | Complexation, ion exchange, electrostatic interaction | [90] |
Nix-MnO2/BC | - | Hybrid BC precursor from CS and RH biomasses pyrolysis; surface-functionalized with Ni-MnO2 nanorods via ultrasonication, hydrothermal treatment, and calcination | Li+ | 89.2 | Physisorption via electrostatic attractive forces; monolayer adsorption according to Langmuir model | [140] |
Magnetic EP BC | 400, 800 | Enteromorpha prolifera biomass (126 g) treated with 120 mL FeCl3 (2 mol/L) solution, stirred at 80 °C for 2 h. Ferric hydroxide-coated biomass separated via centrifugation, dried at 80 °C overnight. Pyrolysis at 400 or 800 °C under N2 with heating rate of 5 °C/min and N2 flow rate of 300 mL/min. Washed with 1 M HCl and distilled water, dried at 80 °C | Cr(VI) | 95.23 | Enhanced adsorption due to increased surface polarity and specific surface; likely includes physical adsorption due to magnetic modification | [141] |
Coffee ground | 650 | SCG/FO mixtures pyrolyzed in a quartz tube furnace with CO2 atmosphere. Mixtures of SCG and FO in mass ratios SCG1/FO0.33, SCG1/FO0.5, SCG1/FO1, and SCG1/FO2. Pyrolysis at 10 °C/min heating rate to 650 °C, held for 60 min, cooled to 25 ± 2 °C | Sb(V), Cd(II), Ni(II) | Sb(V): 7.0 (single mode), 9.3 (multiple mode); Cd(II): 12.7; Ni(II): 16.8 | Ternary complexation on iron oxides surface; competition for adsorption sites in multiple mode reduces Cd(II) and Ni(II) uptake but enhances Sb(V) removal | [142] |
Porous BC | 600 | Corn straw powder soaked in 25% ZnCl2 for 20 h, dried, pyrolyzed at 600 °C for 1.5 h with N2, mixed with Fe(NO3) and Zn(NO3)2, pH adjusted to 11, stirred, red-brown precipitate formed | Ce(IV) | 453.518 | Chemisorption via surface active sites fits quasisecondary kinetic model better; adsorption influenced by temperature and is heat absorbing | [143] |
Palm tree fronds | 650 | Carbonization at 650 °C under inert N2 atmosphere. Oxidation with 8 M HNO3 | Eu3+ | 123 | Reaction equation: Proposed two-step mechanism: Cation exchange of carboxylic protons with Eu3+, followed by complexation of Eu3+ with carboxylate groups | [144] |
Orange peel | 600 | Orange peel cut, washed, oven-dried at 60 °C, heated at 600 °C under oxygen-limited conditions for 2 h, ground and sieved to <0.15 mm | La(III) | 55.57 | High adsorption capacity; mesoporous structure with well-developed porosity and surface functional groups | [145] |
Corn cob | 600 | A mixture of 6.5 g KCl/NaCl (1:1) and 3 g corncob powder was dissolved in 30 mL DI water and soaked for 12 h at 50 °C. In the final hour, 1 g of Na2S, Na2S2O3, Na2SO3, or Na2SO4 was added. The precursors were then filtered, dried at 80 °C for 12 h | Pb(II), Cu(II) | 421.8 for Pb(II), 185 for Cu | Ion exchange, electrostatic interaction, cation–π interaction | [146] |
Apple wood | 700 | - | Cr(VI) | 5 | Electrostatic interactions, ion exchange, complexation | [147] |
Food waste | 300 | Food waste was mixed, oven-dried (105 °C), ground (10-mesh sieve), and stored in a sealed container at room temperature | Cd(II), Pb(II) | Cd 16.86, Pb 12.41 | Surface complexation, cation–π interaction, precipitation, electrostatic interaction | [148] |
Sewage sludge–coconut fiber | 600 | Copyrolysis | Cu(II), Zn(II), Ni(II), Cd(II) | - | Electrostatic interaction, complexation, π–π interaction, H-bond, pore filling, crystal lattices | [149] |
Modified pineapple pulp | 400 | - | Cu(II) | 41.9 | Ion exchange, complexation, electrostatic attraction | [150] |
5.2. Adsorption of Transition Metals
5.3. Adsorption of Rare Earth Metals
6. Recycling and Regeneration of Metal-Loaded Biochar
6.1. Chemical Regeneration Techniques
6.2. Thermochemical Recycling Techniques
6.3. Limitations in Recycling and Environmental Considerations
7. Applications of Metal-Loaded Biochar
7.1. Soil Amendment and Fertilization
7.2. Catalytic Applications
7.2.1. Application for Wastewater Treatment
Raw Materials | Metal Compounds | Process | Remarks | References |
---|---|---|---|---|
Calamus | MoO2-enhanced Fe2+/Fe3+ | Impregnation and followed by pyrolysis, 600 °C | Degradation of tetracycline, 90.9% | [188] |
Rice straw | MoO2-enhanced Fe2+/Fe3+ | Impregnation and followed by pyrolysis, 800 °C | Degradation of BPA, >96% | [191] |
Cherry kernel | CoCl2·6H2O | Impregnation and followed by pyrolysis, 800 °C | Degradation of BPA, ~100% | [186] |
Rice straw | CuCl2·2H2O | Impregnation and followed by pyrolysis, 800 °C | Degradation of ciprofloxacin, ~100% | [180] |
Rice straw | FeCl3·6H2O/LaCl3·7H2O | Pyrolysis, 450 °C | Adsorption of phosphorus, 52 mg P/g | [182] |
Corn stalks | KOH, FeCl3·6H2O | Autoclave at 200 °C, Copyrolysis (800 °C) with KOH and impregnation in FeCl3·6H2O solution | 480.9 mg g−1 of Pb2+adsorption capacity | [193] |
Sewage sludge | Zero valent iron | Copyrolysis 500 °C | 83.4% degradation of sulfamethoxazole | [194] |
Municipal sludge | FeCl3·6H2O | Impregnation and followed by pyrolysis, 400 °C | 99.8% degradation of thiamethoxam | [195] |
7.2.2. Applications for Catalytic Bio-Oil Production
Feedstock for BC | Process for BC Catalyst | Metal Ion Sources | Feedstock for Biofuel | Process for Biofuel | Remarks | References |
---|---|---|---|---|---|---|
Rice husk | Microwave-assisted catalytic pyrolysis, 550 °C | Fe(NO3)3, impregnation and calcined with BC | Corn cob | MW-assisted torrefaction | Increased phenol compounds in bio-oil up to 60% | [200] |
Cellulose powder | Pyrolysis, 600 °C | Ni(NO3)2·6H2O, impregnation and calcined with cellulose powder BC (CPB) | Lignin model compounds | Hydrogenolysis, 140 °C | Increased yield of phenol (12.5%) and cyclohexanol (80.7%) | [199] |
Peanut shell | Microwave-assisted Pyrolysis, 550 °C | FeCl2·4H2O and FeCl3 (1:1 ratio), impregnation and calcined, 450 °C | Peanut shell | Pyrolysis | Total bio-oil 24.3% where 27% aliphatic and 18% aromatic hydrocarbon selectivity | [201] |
Rice husk | Pyrolysis, 700 °C | CaO (30 wt%), impregnation and calcined (700 °C) with rice husk BC | Palm oil | Transesterification reaction, 65 °C | Biodiesel yields up to 93.4% | [209] |
Municipal sludge | Pyrolysis, 800 °C | CaO (20 wt%), impregnation and calcined (700 °C) with the BC | Palm oil | Transesterification reaction, 65 °C | Biodiesel yields up to 93.8% | [207] |
Peanut shell | Pyrolysis, 700 °C | FeCl3·4H2O, MnCl2·4H2O, NaCl; impregnation and calcined with BC | Peanut shell | Pyrolysis, 440–660 °C | 8% phenolic selectivity over Fe3+ | [202] |
Pine tree needles | Impregnation with ZnCl2 (1:1 biomass to ZnCl2 weight ratio) and Pyrolysis, 700 °C | Ni(NO3)2·6H2O, Impregnation and calcined with the modified BC, 500 °C | Pine tree needles | Pyrolysis, 550 °C | Increased the aromatic selectivity to ~36% | [197] |
7.3. Electrochemical Applications
8. Future Research Directions
9. Conclusions
Author Contributions
Funding
Data Availability Statement
Conflicts of Interest
References
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Hasan, M.; Chakma, S.; Liang, X.; Sutradhar, S.; Kozinski, J.; Kang, K. Engineered Biochar for Metal Recycling and Repurposed Applications. Energies 2024, 17, 4674. https://doi.org/10.3390/en17184674
Hasan M, Chakma S, Liang X, Sutradhar S, Kozinski J, Kang K. Engineered Biochar for Metal Recycling and Repurposed Applications. Energies. 2024; 17(18):4674. https://doi.org/10.3390/en17184674
Chicago/Turabian StyleHasan, Mehedi, Soumik Chakma, Xunjia Liang, Shrikanta Sutradhar, Janusz Kozinski, and Kang Kang. 2024. "Engineered Biochar for Metal Recycling and Repurposed Applications" Energies 17, no. 18: 4674. https://doi.org/10.3390/en17184674
APA StyleHasan, M., Chakma, S., Liang, X., Sutradhar, S., Kozinski, J., & Kang, K. (2024). Engineered Biochar for Metal Recycling and Repurposed Applications. Energies, 17(18), 4674. https://doi.org/10.3390/en17184674