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随着工业发展和人类活动的增加,采矿、电镀、冶金等行业所造成的重金属排放已经成为全球性的环境污染问题之一. 如含有铅、锌、汞、铬等重金属离子的工矿业废水会进入各种水域或土壤中. 重金属会通过生物积累和食物链的富集对人体健康造成严重危害[1-3]. 而Cd2+作为最具毒性的重金属离子之一[4-5],很容易在各种器官和组织中积累,从而导致骨骼、肾脏损伤和癌症等病症[6-8]. 生物质炭具有比表面积大、孔隙结构丰富等优点[9-11],已经被证实能够吸附水体中的重金属离子[12-14]. 虽然生物质炭对重金属的吸附效果显著,但是其吸附效果受到原材料和制备温度的影响. 如炭化温度的增加会造成生物质炭表面官能团减少[15],但却会适量增加孔隙结构,从而影响生物质炭对重金属离子的吸附性能. 而原材料的差异是影响生物质炭特性的主要因素,如原材料中所含的元素种类越多,越有利于生物质炭的化学沉淀的形成. 因此原材料的种类也将是影响生物质炭固定重金属的因素之一.
园林废弃物是固体废弃物之一,在城市垃圾填埋场倾倒的垃圾中约有25%是花园垃圾[16]. 城市地区的木质生物质是一个潜在的、巨大的、未被充分利用的资源,这种资源随着城市和绿地面积的扩大而不断增加[17]. 园林废弃物常用的处理方式有堆肥、掩埋、粉碎覆盖和直接燃烧等[18]. 但是这些方法存在降解速率慢和对环境有二次污染等缺点. 而将其制备成生物质炭不仅可以有效缓解园林固体废弃物处置问题,而且有利于降低环境污染修复的成本. 如今已经有研究证实园林类生物质炭能有效吸附固定重金属,例如600 ℃制备的硬木生物质炭被证实能吸附水溶液中47.66 mg·g−1的Pb2+[13]. Ippolito 等[19]发现美国黑松生物质炭能通过提高pH值形成重金属矿物沉淀来降低Cd2+的生物可利用度. 周润娟[20]发现不同原材料的生物质炭对Cd2+的最大吸附容量有很大差异 (水葫芦茎粉:84.79 mg·g−1、根粉:103.57 mg·g−1和植株:142.59 mg·g−1). 汤嘉雯等[21]发现加拿大一枝黄花的茎或茎叶混合物制备而成的生物质炭对水中Cd2+的吸附机理包括离子交换、络合反应、沉淀作用和物理吸附等,但是没对主要机理进行剖析. 园林废弃物除了种类外,其自身的不同部位的差异也会对重金属修复产生影响,然而针对这方面的研究十分有限.
本研究旨在探讨梧桐不同部位废弃物的生物质炭吸附固定Cd2+的性能差异和机理. 本研究假设梧桐不同部位废弃物的初始结构和元素释放是影响Cd2+固定的主要因素. 采用X射线衍射 (XRD)、衰减全反射红外光谱 (ATR-IR)、扫描电镜 (SEM)、比表面积及孔隙分析 (BET) 和电感耦合等离子光谱发生仪 (ICP-OES) 等技术探究梧桐不同部位废弃物生物质炭对Cd2+的吸附性能和矿物学特征.
不同部位梧桐生物质炭对水溶液中镉吸附的机理
Mechanism of cadmium adsorption by biochar from different parts of platanus acerifolia in aqueous solution
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摘要: 为了探究梧桐不同部位废弃物所制备的生物质炭 (皮、枝、叶) 对Cd2+的吸附效率和稳定修复的机理,以此为园林废弃物炭化利用在重金属污染修复方面的应用提供科学依据. 利用实验室模拟法,通过高温煅烧法制备梧桐不同部位生物质炭,采用元素分析仪、比表面积及孔隙分析 (BET)、X射线衍射仪 (XRD)、扫描电镜/能谱 (SEM/EDS) 及衰减全反射红外光谱 (ATR-IR) 等技术研究不同反应时间、重金属浓度和溶液初始pH条件下生物质炭对Cd2+吸附效果的影响,并运用四步萃取法和脱附实验分析生物质炭上Cd2+的吸附形态和稳定性. 3种生物质炭都在8 h左右达到吸附平衡,最终吸附量依次为树皮炭>枝条炭>叶片炭;溶液初始浓度为0.5—2 g·L−1时Cd2+的吸附量呈增长趋势,在2.5—3g·L−1时逐渐平缓;生物质炭Cd2+吸附量均随着pH的升高而升高,但在pH值为5—8时,吸附的趋势逐渐平稳;树皮炭的酸溶态和非生物利用态的稳定Cd形态要高于枝条炭和叶片炭;比表面积不是影响梧桐生物质炭吸附Cd2+的主要影响因素,吸附动力学,ATR,XRD和重金属形态萃取均证实Cd碳酸盐类矿物生成是主导吸附机理;3种生物质炭的脱附量在4 h后逐渐趋于平衡,其中脱附量最大为叶片炭,最小为树皮炭. 梧桐不同部位的初始性质对生物质炭吸附Cd2+具有明显的影响,其中梧桐皮具备更高的吸附量和重金属稳定形态,并且相比其他种类生物质炭有明显优势. 因此,从吸附效果和生产成本的角度,本研究建议以梧桐皮为主,枝条和叶片为辅的生物质炭对重金属Cd进行修复治理.Abstract: To explore the adsorption efficiency of Cd2+ by biochar (bark, branch and leaf) prepared from Wutong waste from different components and the mechanism of repair stability, and provide scientific basis for the application of carbonization of garden wastes in heavy metal pollution remediation. The biochar made from different platanus acerifolia components was prepared by means of laboratory simulation and calcined at high temperature. The effects of reaction time, heavy metal concentration and initial pH on the adsorption of Cd2+ by biochar were studied by elemental analyzer, specific surface area and pore analyzer (BET), X ray diffractometer (XRD), scanning electron microscopy/energy dispersive spectrometry (SEM/EDS) and attenuated total reflectance infrared spectroscopy (ATR-IR). Four step extraction method and desorption experiment were used to analyze the adsorption form and stability of Cd2+ on biochar. All the three biochar reached adsorption equilibrium at about 8 h and the final adsorption amount was bark biochar > branch biochar > leaf biochar; When the initial concentration of Cd2+ solution was 0.5—2 g·L−1, the adsorption amount of Cd2+ by biochar showed an increasing trend and gradually flattens out at 2.5—3 g·L−1; The adsorption of Cd2+ on biochar increased with the increase of pH, but the adsorption trend gradually stabilized at pH 5—8; The acid soluble and abiotic utilization of Cd speciation in bark biochar were more stable than that in branch biochar and leaf biochar. The specific surface area was not the main factor affecting the adsorption of platanus acerifolia biochar, adsorption kinetics, ATR, XRD and heavy metal speciation confirmed that the formation of Cd-carbonate minerals is the dominant adsorption mechanism. The desorption amount of the three biochar tended to balance gradually after 4 h. The maximum desorption amount was leaf biochar and the minimum was bark biochar. Different platanus acerifolia components had obvious effects on Cd2+ adsorption by biochar. The bark biochar had higher adsorption capacity and stable form of heavy metals and it had significant advantages over other biochar species. Therefore, from the perspective of adsorption effect and production cost, this study suggested that biochar should be prepared mainly from bark, supplemented by branches and leaves, and use it to repair and remediation Cd pollution.
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Key words:
- sycamore waste /
- biochar /
- water body /
- cadmium /
- adsorption
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表 1 生物质炭的工业分析和元素分析
Table 1. Industrial analysis and elemental analysis of biochar
生物质炭
Biochar工业分析/%
Proximate analysis元素分析/%
Elemental analysis产率/%
Productivity木质素含量/%
Lignin contents灰分 挥发分 固定碳 碳 (C) 氮 (N) 硫 (S) 其他 C/N 树皮炭 13.12 42.21 40.67 63.59 1.02 0.23 35.16 62.34 26.15 15.81 枝条炭 15.95 38.62 41.43 56.11 1.56 0.25 42.08 35.97 23.76 19.15 叶片炭 17.37 35.42 43.21 55.56 1.67 0.25 42.52 33.27 29.26 23.57 表 2 生物质炭孔隙结构特征
Table 2. Pore structure characteristics of biochar
生物质炭
Biochar比表面积/(m2 ·g−1)
Specific surface area平均孔径/nm
Mean pore size微孔体积/(cm3 ·g−1)
Micropore volume中孔体积/(cm3 ·g−1)
The pore volume总孔隙体积/(cm3 ·g−1)
Total pore volume树皮炭 295.7 2.6 0.022 0.038 0.060 枝条炭 305.5 2.5 0.083 0.111 0.194 叶片炭 312.3 2.9 0.010 0.020 0.030 表 3 不同生物质炭吸附Cd2+动力学参数
Table 3. Kinetic parameters of Cd2+ adsorption by different biochar
生物质炭
BiocharQe/(mg·g−1) k1/min−1 R2 准一级动力学模型 树皮炭 383.590 0.01163 0.97152 枝条炭 345.872 0.01812 0.89178 叶片炭 295.409 0.01470 0.87999 生物质炭
BiocharQe/(mg·g−1) k2/(g· (mg·min)−1) R2 准二级动力学模型 树皮炭 426.845 0.01544 0.99438 枝条炭 379.550 0.02460 0.94299 叶片炭 323.276 0.02103 0.96870 注:Qe为t时刻对应的吸附平衡时的吸附量,k1、k2为速率常数.
Note: Qe is the adsorption amount corresponding to the adsorption equilibrium at time t, k1, k2 are the rate constants.表 4 不同生物质炭吸附等温线参数
Table 4. Adsorption isotherm parameters of different biochar
生物质炭
BiocharLangmuir等温模型
Langmuir isotherm modelFreundlich等温模型
Freundlich isotherm modelQmax/(mg·g−1) b/(L·mg−1) R2 Kf /(mg1+n·g−1·L-n) 1/n R2 树皮炭 292.75 0.0976 0.9901 252.99 -0.763 0.6605 枝条炭 288.51 0.0793 0.9798 242.90 -0.792 0.6836 叶片炭 255.23 0.0777 0.9762 242.08 -0.103 0.6845 注:Qmax为最大吸附量,参数b、Kf分别和与吸附强度和吸附量有关.
Note: Qmax is the maximum adsorption capacity, the parameters b and Kf are respectively related to the adsorption strength and adsorption capacity.表 5 不同生物质炭对水体环境中重金属的去除作用
Table 5. Removal of heavy metals in water environment by different biochar
原材料
Raw
material比表面积 /
(m2 ·g−1 )
BET总孔隙体积/
(cm3 ·g−1)
Total pore volume化学沉淀
Chemical
precipitation制备条件/°C
Preparation
condition吸附量/
(mg·g−1)
Adsorbing capacity吸附动力学模型
Dynamic
adsorption model吸附等温线
Adsorption
isotherm文献
Literature梧桐皮 295.7 0.060 ${\rm{CO}}_3^{2 - }/{\rm{SiO}}_3^{2 - } $ 450 426.845 准二级 Langmuir 本研究 梧桐枝 305.5 0.194 ${\rm{CO}}_3^{2 - }/{\rm{SiO}}_3^{2 - } $ 450 379.550 准二级 Langmuir 本研究 梧桐叶 312.3 0.030 ${\rm{CO}}_3^{2 - }/{\rm{SiO}}_3^{2 - } $ 450 323.276 准二级 Langmuir 本研究 玉米秸秆 70.7 0.036 $ {\rm{CO}}_3^{2 - }$ 600 106.86 准二级 Langmuir [31] 稻杆 73.40 0.065 ${\rm{PO} }_4^{3 - }/{\rm{CO} }_3^{2 - }/{\rm{Si} }{ {\rm{O} }_4^{ - } }$ 700 60.61 准二级 Langmuir [32] 泥煤苔 - - - 800 39.8 准二级 Langmuir [33] 牧豆壳 3.11 - - 350 38.3 准二级 Langmuir [33] 水葫芦 - - ${\rm{PO}}_4^3/{\rm{CO}}_3^{2 - } $ 450 70.3 准二级 Langmuir [34] 牛粪 5.61 - ${\rm{PO} }_4^3/{\rm{CO} }_3^{2 }$ 200 54.6 准二级 Langmuir [35] 果穗 206.45 0.59 - 100 62.5 准二级 Langmuir [36] -
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