CN116328725A - 一种铈改性磁化厌氧发酵尾渣生物炭及其制备方法与应用 - Google Patents
一种铈改性磁化厌氧发酵尾渣生物炭及其制备方法与应用 Download PDFInfo
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Abstract
本发明公开了一种铈改性磁化厌氧发酵尾渣生物炭,所述生物炭由厌氧发酵尾渣为原料,经磁化后铈改性得到。本发明还具体公开了其制备方法,以厌氧发酵尾渣为原料,采用FeCl3·6H2O、FeSO4·7H2O等对生物炭进行改性,以改性生物炭复合材料为吸附剂,根据厌氧发酵尾渣和生物炭的特点,将二者有机结合,既解决了厌氧发酵残余物存在的问题,又实现了水体中Cr(Ⅵ)的去除,对推进厌氧发酵尾渣资源化利用和高效去除水体中Cr(Ⅵ)具有深远的影响。
Description
技术领域
本发明属于吸附剂材料制备技术领域,具体涉及一种铈改性磁化厌氧发酵尾渣生物炭及其制备方法与应用。
背景技术
铬(Cr)是一种典型的重金属,在自然界中一般以Cr(Ⅲ)、Cr(Ⅵ)两种价态存在。Cr(Ⅲ)通常以羟基复合物的形式存在,包括Cr(OH)2+、Cr(OH)2 +、Cr(OH)3、Cr(OH)4 -等,Cr(Ⅲ)的毒性较小,还是人体必须的微量元素,当人体缺少Cr(Ⅲ)时可能会出现动脉硬化等疾病;Cr(Ⅲ)还能激活胰岛素促进糖代谢,但过量的Cr(Ⅲ)引起头痛、恶心、呕吐等不良反应,同时会影响肺部的正常工作。Cr(Ⅵ)的存在状态和pH有关,在水体中主要以HCrO4 -、CrO4 2-、Cr2O7 2-等形式存在。Cr(Ⅵ)的毒性大约是Cr(Ⅲ)的100倍,会对人体的DNA造成氧化损伤,进而导致DNA链断裂以及阻断DNA之间的交联;同时,Cr(Ⅵ)具有刺激性、腐蚀性和强氧化性,会影响人体肝脏、肾脏和内分泌等系统的正常工作,还会通过干扰人体内的氧化还原反应、水解反应和蛋白质的合成等影响人体健康。当水中Cr(Ⅵ)的浓度在0.015-0.050mg/m3时,在短时间内大量接触会造成人体嗅觉和味觉功能的丧失,长时间饮用能够引起肠道炎症,造成肠胃穿孔和溃疡等,还会导致肝细胞和肾脏细胞的变性坏死,进而诱发癌症等疾病。因此,解决水体Cr(Ⅵ)污染问题刻不容缓,对保护人类的健康具有重要意义。
对于处理含铬废水,国内外已经有较多的方法,按照处理原理可以分为三大类:物理,化学和生物处理。每一种技术都有一定的优势,同样也存在着不足。对于自然水体中重金属离子的去除,吸附法具有高效率,成本低,易操作和吸附剂可再生重复利用等优势,在实际生产中吸附法被广泛采用于废水中重金属离子的治理。
在众多吸附材料中,生物炭因其生物质来源丰富,制备简单,成本低廉,且具有较大的比表面积和孔体积,以及丰富的官能团等优点适合用做处理废水中Cr(Ⅵ)的吸附剂。生物炭对Cr(Ⅵ)的吸附性能受到制备原料的影响,当前研究主要集中在以植物残体为原料制备的生物炭,而对以厌氧发酵尾渣为原料制备生物炭的研究相对较少。厌氧发酵作为一种新能源技术,在处理有机废弃物的同时还可以产生沼气,因此得到了大力推广,然而,在厌氧发酵产沼气的同时会伴随尾渣的产生,尾渣难以消纳和二次利用,严重阻碍了厌氧发酵技术的发展,但尾渣中碳含量很高,可用于制备生物炭,而厌氧发酵尾渣生物炭对Cr(Ⅵ)的吸附性能尚未明确。因此,本项目以厌氧发酵尾渣为原料制备生物炭并进行改性,研究改性生物炭对Cr(Ⅵ)的吸附性能,以期为利用生物炭吸附环境中的Cr(Ⅵ)提供理论依据。
发明内容
本发明的目的在于提供一种铈改性磁化厌氧发酵尾渣生物炭,同时提供其制备方法与应用是本发明的又一发明目的。
为达到上述发明目的,本发明采取以下技术方案:
一种铈改性磁化厌氧发酵尾渣生物炭,由厌氧发酵尾渣为原料,经磁化后铈改性得到。
所述的一种铈改性磁化厌氧发酵尾渣生物炭的制备方法,包括以下步骤:
1)生物炭的制备
以厌氧发酵尾渣为原材料制备厌氧发酵尾渣生物炭;
2)制备磁化厌氧发酵尾渣生物炭
将厌氧发酵尾渣生物炭与一定量的FeCl3·6H2O和FeSO4·7H2O充分混合后,加入氨水,于55-95℃下水浴搅拌反应1-2h制得磁化厌氧发酵尾渣生物炭;
3)生物炭的改性
以四水硫酸铈溶液为改性剂,采用浸渍法对磁化厌氧发酵尾渣生物炭进行改性,即得铈改性磁化厌氧发酵尾渣生物炭。
优选地,步骤1)中,生物炭通过以下步骤制备得到:将厌氧发酵尾渣烘干后,粉碎、过网,置于管式炉升温至400~900℃,保温180min,自然降至室温即得生物炭;所述管式炉升温速率为15-20℃·min-1。升温速率是保证生物炭品质的重要影响因素之一,升温速率过高,不利于初始孔隙形成,生物炭产率相对较低,升温速率过低,生物炭机械强度会下降。其次,热解温度越高,生物质的空隙发育越完全,但过高的热解温度也会导致生物质的空隙架构坍塌。
进一步优选地,所述厌氧发酵尾渣的烘干温度为100~105℃,烘干时间为23-25h;过筛采用50-80目不锈钢筛网。
步骤2)中,所述厌氧发酵尾渣生物炭、FeCl3·6H2O、FeSO4·7H2O、氨水的用量比为:(6-10)g:(5-20)g:(5-20)g:(10-20)ml;本发明中,加入氨水的目的是产生的氨气能促进三价铁向零价铁转化,之所以选择FeCl3·6H2O、FeSO4·7H2O按照(5-20)g:(5-20)g混合,原因在于便于生物炭使用过程中的固液分离。
步骤3)中,浸渍过程为将磁化厌氧发酵尾渣生物炭浸渍在四水硫酸铈溶液中,浸渍时间6~9h,浸渍温度为20~30℃;浸渍过程中,所使用的四水硫酸铈的浓度为1.0~2.0g·L-1,磁化厌氧发酵尾渣生物炭与改性剂溶液的用量比为(0.5~1.5)g:(50~150)ml。
利用所述的铈改性磁化厌氧发酵尾渣生物炭去除含铬废水中Cr(Ⅵ)的方法,在填充滤柱底部填充5-20目的石英砂1-1.5cm,其上再填充50-150目的石英砂0.2-0.5cm,作为承托层以防治吸附剂的流失,在底部石英砂和上面石英砂中间是铈改性磁化厌氧发酵尾渣生物炭,控制含铬废水的流速为1.3-1.5mL·min-1,pH4.5-5.5。
与现有技术相比,本发明具有以下技术优势:以厌氧发酵尾渣为原料,采用FeCl3·6H2O、FeSO4·7H2O等对生物炭进行改性,以改性生物炭复合材料为吸附剂,根据厌氧发酵尾渣和生物炭的特点,将二者有机结合,既解决了厌氧发酵残余物存在的问题,又实现了水体中Cr(Ⅵ)的去除,对推进厌氧发酵尾渣资源化利用和高效去除水体中Cr(Ⅵ)具有深远的影响。
附图说明
图1是本发明实施例1制备的铈改性磁化厌氧发酵尾渣生物炭的扫描电镜照片(左图为改性前,右图为改性后)。
具体实施方式
以下是本发明的几个具体实施例,以进一步说明本发明,但本发明的保护范围不限于这些实施例。
实验例1
一种铈改性磁化厌氧发酵尾渣生物炭,由厌氧发酵尾渣为原料,经磁化后铈改性得到。
其制备方法,包括以下步骤:
1)生物炭的制备
以厌氧发酵尾渣为原材料制备厌氧发酵尾渣生物炭;
生物炭通过以下步骤制备得到:将厌氧发酵尾渣100℃烘干24h后,粉碎、过60目不锈钢筛网,置于管式炉升温至700℃,保温180min,自然降至室温即得生物炭;所述管式炉的升温速率为18℃·min-1;
2)制备磁化厌氧发酵尾渣生物炭
将厌氧发酵尾渣生物炭与一定量的FeCl3·6H2O和FeSO4·7H2O充分混合后,加入氨水,于75℃下水浴搅拌反应1.5h制得磁化厌氧发酵尾渣生物炭;所述厌氧发酵尾渣生物炭、FeCl3·6H2O、FeSO4·7H2O、氨水的用量比为:8g:15g:15g:15ml;
3)生物炭的改性
以四水硫酸铈溶液为改性剂,采用浸渍法对磁化厌氧发酵尾渣生物炭进行改性,即得铈改性磁化厌氧发酵尾渣生物炭;所述浸渍过程为将磁化厌氧发酵尾渣生物炭浸渍在四水硫酸铈溶液中,浸渍时间7h,浸渍温度为25℃;浸渍过程中,所使用的四水硫酸铈的浓度为1.5g·L-1,磁化厌氧发酵尾渣生物炭与改性剂溶液的用量比为1.0g:100ml。
实施例2
一种铈改性磁化厌氧发酵尾渣生物炭,由厌氧发酵尾渣为原料,经磁化后铈改性得到。
所述的一种铈改性磁化厌氧发酵尾渣生物炭的制备方法,包括以下步骤:
1)生物炭的制备
以厌氧发酵尾渣为原材料制备厌氧发酵尾渣生物炭;
生物炭通过以下步骤制备得到:将厌氧发酵尾渣105℃烘干23h后,粉碎、过50目不锈钢筛网,置于管式炉升温至400℃,保温180min,自然降至室温即得生物炭;所述管式炉升温速率为15℃·min-1;
2)制备磁化厌氧发酵尾渣生物炭
将厌氧发酵尾渣生物炭与一定量的FeCl3·6H2O和FeSO4·7H2O充分混合后,加入氨水,于55℃下水浴搅拌反应1h制得磁化厌氧发酵尾渣生物炭;所述厌氧发酵尾渣生物炭、FeCl3·6H2O、FeSO4·7H2O、氨水的用量比为:6g:5g:5g:10ml;
3)生物炭的改性
以四水硫酸铈溶液为改性剂,采用浸渍法对磁化厌氧发酵尾渣生物炭进行改性,即得铈改性磁化厌氧发酵尾渣生物炭;所述浸渍过程为将磁化厌氧发酵尾渣生物炭浸渍在四水硫酸铈溶液中,浸渍时间6h,浸渍温度为20℃;浸渍过程中,所使用的四水硫酸铈的浓度为1.0g·L-1,磁化厌氧发酵尾渣生物炭与改性剂溶液的用量比为0.5g:50ml。
实施例3
一种铈改性磁化厌氧发酵尾渣生物炭,由厌氧发酵尾渣为原料,经磁化后铈改性得到。
所述的一种铈改性磁化厌氧发酵尾渣生物炭的制备方法,包括以下步骤:
1)生物炭的制备
以厌氧发酵尾渣为原材料制备厌氧发酵尾渣生物炭;
生物炭通过以下步骤制备得到:将厌氧发酵尾渣100℃烘干25h后,粉碎、过80目不锈钢筛网,置于管式炉升温至900℃,保温180min,自然降至室温即得生物炭;所述管式炉升温速率为20℃·min-1;
2)制备磁化厌氧发酵尾渣生物炭
将厌氧发酵尾渣生物炭与一定量的FeCl3·6H2O和FeSO4·7H2O充分混合后,加入氨水,于95℃下水浴搅拌反应2h制得磁化厌氧发酵尾渣生物炭;所述厌氧发酵尾渣生物炭、FeCl3·6H2O、FeSO4·7H2O、氨水的用量比为:10g:20g:20g:20ml;
3)生物炭的改性
以四水硫酸铈溶液为改性剂,采用浸渍法对磁化厌氧发酵尾渣生物炭进行改性,即得铈改性磁化厌氧发酵尾渣生物炭;所述浸渍过程为将磁化厌氧发酵尾渣生物炭浸渍在四水硫酸铈溶液中,浸渍时间9h,浸渍温度为30℃;浸渍过程中,所使用的四水硫酸铈的浓度为2.0g·L-1,磁化厌氧发酵尾渣生物炭与改性剂溶液的用量比为1.5g:150ml。
对比例1
本对比例所述的一种铈改性磁化厌氧发酵尾渣生物炭,其制备方法同实施例1,不同之处在于:四水硫酸铈的浓度为0.3g·L-1。
对比例2
本对比例所述的一种铈改性磁化厌氧发酵尾渣生物炭,其制备方法同实施例1,不同之处在于:四水硫酸铈的浓度为5.0g·L-1。
性能测试例1本发明产品的结构表征
对实施例1制备得到的铈改性磁化厌氧发酵尾渣生物炭进行XRD分析,结果见图1所示,从图1可以看出,XRD分析生物炭的晶体结构表明,Fe3O4颗粒成功合成并负载到生物炭上。为说明效果,本发明附图给出了实施例1制备的铈改性磁化厌氧发酵尾渣生物炭,其他实施例制备得到的晶体结构同样得到了一致的结论。
性能测试例2本发明实施例1-3及对比例1-2的复合材料对含铬废水中Cr(Ⅵ)吸附性能测试
以实施例1-3和对比例1-2制备的生物炭复合材料为例,测试复合材料去除含铬废水中Cr(Ⅵ)的效果。具体吸附方法为:采用填充滤柱的方法进行吸附,在填充滤柱底部填充5-20目的石英砂1-1.5cm,其上再填充50-150目的石英砂0.2-0.5cm,作为承托层以防治吸附剂的流失,在底部石英砂和上面石英砂中间是铈改性磁化厌氧发酵尾渣生物炭,控制含铬废水的流速为1.3-1.5mL·min-1,pH5。
表1复合材料去除含铬废水中Cr(Ⅵ)的效果
由表1的结果可知,本发明的实施例1-3的吸附量均达到了20mg/g以上。当四水硫酸铈的浓度超过1.0~2.0g·L-1范围时,Cr(Ⅵ)吸附量显著降低。
性能测试例3反应前后材料的扫描电子显微镜(SEM)及透射电子显微镜(TEM)观察
利用扫描电子显微镜(SEM)及透射电子显微镜(TEM)对反应前后材料表面的形貌进行表征,图1是铈改性前后材料的扫描电子显微镜(SEM)及透射电子显微镜(TEM),从图1可以看出,经过铈改性后,有大量的颗粒出现在生物炭的表面。
性能测试例4不同pH条件下,本发明磁性生物炭复合材料去除水中Cr(Ⅵ)的影响
以实施例1制备得到的铈改性磁化厌氧发酵尾渣生物炭为例,按照以下步骤进行处理:在填充滤柱底部填充5-20目的石英砂1.5cm,其上再填充50-150目的石英砂0.4cm,作为承托层以防治吸附剂的流失,在底部石英砂和上面石英砂中间填充铈改性磁化厌氧发酵尾渣生物炭,控制含铬废水的流速为1.3-1.5mL·min-1,控制吸附温度为25℃,控制pH分别为2、2.5、3、4.5、5.5和6,得到不同pH条件下,本发明磁性生物炭复合材料的Cr(Ⅵ)去除结果见下表所示。
表2不同pH条件下,磁性生物炭复合材料的Cr(Ⅵ)去除结果
从上表的结果表明,pH值为4.5-5.5,时Cr(Ⅵ)去除效果最好,达到20.5mg·g-1。
性能测试例5不同吸附温度对Cr(Ⅵ)离子去除的影响
以实施例1制备得到铈改性磁化厌氧发酵尾渣生物炭为例实验过程同性能测试例4,不同之处在于,在pH值为4.5下,吸附温度为分别调整为10℃、15℃、20℃、30℃和40℃。
吸附温度/℃ | 10 | 15 | 20 | 30 | 40 |
Cr(Ⅵ)去除量 | 12.4 | 15 | 22.5 | 20.2 | 13 |
结果表明,吸附温度从10℃上升到40℃的过程中,铈改性生物炭对Cr(Ⅵ)的吸附量呈现先增加后减少的趋势,当在20-30℃时,吸附量达到最大,为22.5mg·g-1。
实验例3磁性生物炭复合材料修复铬污染水体的柱实验模拟研究
近年来,填充滤柱作为一种高效的污染物修复体系,被广泛应用于地下水、工业/生活废水和饮用水的处理。因此,本研究以本发明磁性生物炭复合材料为研究对象,在室内通过柱实验模拟研究磁性生物炭复合材料修复铬污染水体的过程,重点就该体系对铬污染水体修复效率及长效性进行综合评估。
具体评估方法为:底部填充5-20目的石英砂1-1.5cm,其上再填充50-150目的石英砂0.2-0.5cm,作为承托层以防治吸附剂的流失,在底部石英砂和上面石英砂中间,即中间是生物炭,是吸附剂。流速可以直接影响改性生物炭与Cr(Ⅵ)的接触时间,是动态吸附的重要参数之一,控制进水流速范围为1.0-5.0mL·min-1,
随着进水流速的增加,吸附柱对Cr(Ⅵ)的去除率和吸附容量都有所下降,穿透时间也进一步缩短,当进水流量为1.3-1.5mL·min-1时,吸附柱对Cr(Ⅵ)的去除率和吸附总量相对较高,且在510min之后才达到穿透点。
以上所述实施例为该发明的优选实施方式,但本发明并不限于上述实施方式,在不背离本发明的实质内容的情况下,本领域技术人员能够做出的任何显而易见的改进、替换或变型均属于本发明的保护范围。
Claims (7)
1.一种铈改性磁化厌氧发酵尾渣生物炭,其特征在于,由厌氧发酵尾渣为原料,经磁化后铈改性得到。
2.权利要求1所述的一种铈改性磁化厌氧发酵尾渣生物炭的制备方法,其特征在于,包括以下步骤:
1)生物炭的制备
以厌氧发酵尾渣为原材料制备厌氧发酵尾渣生物炭;
2)制备磁化厌氧发酵尾渣生物炭
将厌氧发酵尾渣生物炭与一定量的FeCl3·6H2O和FeSO4·7H2O充分混合后,加入氨水,于55-95℃下水浴搅拌反应1-2h制得磁化厌氧发酵尾渣生物炭;
3)生物炭的改性
以四水硫酸铈溶液为改性剂,采用浸渍法对磁化厌氧发酵尾渣生物炭进行改性,即得铈改性磁化厌氧发酵尾渣生物炭。
3.根据权利要求2所述的一种铈改性磁化厌氧发酵尾渣生物炭的制备方法,其特征在于,步骤1)中,生物炭通过以下步骤制得:将厌氧发酵尾渣烘干后,粉碎、过筛,置于管式炉中升温至400~900℃后,保温180min,自然降至室温,即得到生物炭;所述管式炉的升温速率为15-20℃·min-1。
4.根据权利要求3所述的一种铈改性磁化厌氧发酵尾渣生物炭的制备方法,其特征在于,所述厌氧发酵尾渣的烘干温度为100~105℃,烘干时间为23-25h;
过筛采用50-80目不锈钢筛网。
5.根据权利要求2所述的一种铈改性磁化厌氧发酵尾渣生物炭的制备方法,其特征在于,步骤2)中,所述厌氧发酵尾渣生物炭、FeCl3·6H2O、FeSO4·7H2O、氨水的用量比为:(6-10)g:(5-20)g:(5-20)g:(10-20)ml。
6.根据权利要求2所述的一种铈改性磁化厌氧发酵尾渣生物炭的制备方法,其特征在于,步骤3)中,浸渍过程为将磁化厌氧发酵尾渣生物炭浸渍在四水硫酸铈溶液中,浸渍时间6~9h,浸渍温度为20~30℃;浸渍过程中,所使用的四水硫酸铈的浓度为(1.0-2.0)g·L-1,磁化厌氧发酵尾渣生物炭与改性剂溶液的用量比为(0.5~1.5)g:(50~150)ml。
7.利用权利要求1所述的铈改性磁化厌氧发酵尾渣生物炭去除含铬废水中Cr(Ⅵ)的方法,其特征在于,在填充滤柱底部填充5-20目的石英砂1-1.5cm,其上再填充50-150目的石英砂0.2-0.5cm,作为承托层以防治吸附剂的流失,在底部石英砂和上面石英砂中间填充铈改性磁化厌氧发酵尾渣生物炭,控制含铬废水的流速为1.3-1.5mL·min-1,pH4.5-5.5,吸附温度在20-30℃。
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