CN115368911B - 一种氟喹诺酮类抗生素污染土壤修复方法 - Google Patents
一种氟喹诺酮类抗生素污染土壤修复方法 Download PDFInfo
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Abstract
本发明公开了一种氟喹诺酮类抗生素污染土壤修复方法;向含氟喹诺酮类抗生素污染的土壤添加一定比例的生物炭,提供光照,并使土壤保持一定含水率,通过吸附和光化学反应去除土壤中的氟喹诺酮类抗生素;壳聚糖将基体生物炭、TiO2和钨酸铋三者紧密结合在一起,能显著提高复合光催化剂的光催化活性、吸光效率、氧化还原能力,并实现对土壤中氟喹诺酮类抗生素的快速高效降解。
Description
技术领域
本发明涉及环境保护中土壤治理领域,具体为一种氟喹诺酮类抗生素污染土壤修复方法。
背景技术
土壤是是生物赖以生存的物质基础,然而,随着人类活动的日益频繁,现在土壤污染越来越严重;尤其土壤中的抗生素含量严重超标,引发环境多重污染,备受社会关注;畜禽养殖业为了预防动物疾病大量使用抗生素,主要是添加抗生素至畜禽饲料,因畜禽对这些元素无法完全吸收,导致残留的抗生素随粪便排入环境。土壤中抗生素等污染物种类和含量的不断增加,严重破坏生态平衡;
氟喹诺酮类抗生素是指人工合成的含有4-喹酮母核的一类抗生素,主要作用于DNA旋转酶,其特点是对革兰氏阴性菌与支原体有着明显的灭杀作用,且组织渗透力强,广泛用于人类和畜禽疾病治疗。常见的氟喹诺酮类抗生素主要有环丙沙星、恩诺沙星和诺氟沙星等。
氟喹诺酮类抗生素在动物和人体内不能够被完全代谢,会以原形和活性代谢产物的形式排到体外,能够在环境中形成母体,诱导土壤中微生物逐渐产生抵抗性,造成抗药基因的诱变、抗药性菌群的富集,且破坏土壤生态功能、肥力水平;农作物会吸收累积在土壤中氟喹诺酮类抗生素,氟喹诺酮类抗生素会通过食物链进入人类体中,危害人类健康;
吸附常用的污染物去除手段,对于抗生素主的去除主要是使用吸附剂进行物理化学吸附,使其固定到吸附剂上而减少在抗生素的迁移,但是对于吸附后抗生素,仍然是存在于吸附剂表层;
生物炭具有可观的比表面积和孔隙,与表面钨酸铋因具有带隙合适、晶体结构独特、光稳定性高、绿色无毒等特点,被广泛应用于光催化;但因可见光吸收能力弱、光生载流子分离能力低致其光催化活性较低,单一使用限制了钨酸铋的实际应用;
因此,研制一种高效快速、低成本降解土壤中氟喹诺酮类抗生素的方法具有广阔的使用价值和应用前景。
发明内容
本发明的目的在于提供一种氟喹诺酮类抗生素污染土壤修复方法,以解决上述背景技术中提出的问题。
为了解决上述技术问题,本发明提供如下技术方案:
一种氟喹诺酮类抗生素污染土壤修复方法,所述方法包括如下步骤:
S1:选取被氟喹诺酮类抗生素污染的土壤进行松动处理,使土壤含水量为45~85%,向土壤中添加3~10%w/w的改性生物炭,得到待修复土壤;
S2:模拟太阳光照在20~40℃下对待修复土壤进行48~72h光照处理。
进一步的,所述步骤S1中,所述土壤中氟喹诺酮类抗生素为环丙沙星、恩诺沙星、诺氟沙星中的任意一种或多种,每1kg土壤中氟喹诺酮类抗生素的含量为10~250mg。
进一步的,所述步骤S2中,光照处理使用的太阳光照为氙灯,氙灯的功率为500w或1000w中的任意一种。
进一步的,所述步骤S1中,改性生物炭为一种负载复合光催化剂的生物炭,
进一步的,所述生物炭为水稻秸秆生物炭、稻壳生物炭、玉米芯生物炭中的任意一种或多种,所述复合光催化剂为TiO2和钨酸铋复合而成;所述生物炭具有多孔结构和大比表面积,TiO2为片状层级纳米结构,钨酸铋为鸟巢状纳米结构。
进一步的,所述步骤S1中,改性生物炭的制备包括如下步骤:
将秸秆、稻壳和玉米芯粉碎,装入瓷坩埚中,在马弗炉中500℃煅烧,并保温2h,得到生物炭;
将H2O、浓硝酸、钛酸四丁酯、乙醇分散,在恒温磁力搅拌器上剧烈搅拌,待出现透明凝胶后停止搅拌,陈化,在105℃烘箱中烘干至恒重,得到TiO2;
将五水硝酸铋、表面活性剂和二水钨酸钠依次溶解于乙二醇中,搅拌30~45min后加入TiO2和生物炭粉末继续搅拌1~2h,将悬浮液转移到高压反应釜中,放入160~200℃的高温中反应5h;冷却后用无水乙醇和水反复清洗,50~70℃真空干燥,冷却后粉碎细化球磨处理,得到改性生物炭。
进一步的,所述马弗炉升温速率为5~15℃/min;表面活性剂为十二烷基磺酸钠、聚乙烯吡咯烷酮中的一种或两种。
进一步的,所述H2O:浓硝酸:钛酸四丁酯:乙醇的体积比为2:0.4:4:20。
进一步的,所述五水硝酸铋:二水钨酸钠:TiO2的摩尔比为2:1:(2~3)。
进一步的,所述步骤S1中,改性生物炭的制备包括如下步骤:
将秸秆、稻壳和玉米芯粉碎后加入KOH溶液中,加热搅拌,过滤,洗涤,干燥,得到碱活化颗粒;将碱活化颗粒和四氧化三铁加入到2-甲基咪唑溶液中,超声分散,在搅拌状态下滴入Zn(NO3)2·6H2O溶液,过滤,真空干燥,得到复合改性颗粒;将复合改性颗粒装入瓷坩埚中,在氮气气氛下置于500℃马弗炉中煅烧,并保温2h,调节pH值为7,干燥,得到基体生物炭;
将五水硝酸铋、表面活性剂和二水钨酸钠依次溶解于乙二醇中,搅拌30~45min后加入TiO2继续搅拌1~2h,将悬浮液转移到高压反应釜中,放入160~200℃的高温中反应5h;冷却后用无水乙醇和水反复清洗,50~70℃真空干燥,冷却后粉碎细化球磨处理,得到复合光催化剂;将复合光催化剂和基体生物炭加入壳聚糖溶液中,搅拌均匀,得到混合溶液;将混合溶液缓慢注入NaOH溶液中,静置,过滤,洗涤pH至中性,干燥,得到改性生物炭;
其中,所述KOH溶液浓度为2.5~3.5mol/L,2-甲基咪唑溶液浓度为0.1~1mol/L,Zn(NO3)2·6H2O溶液浓度为0.1~1mol/L,碱性活化颗粒:四氧化三铁:2-甲基咪唑溶液:Zn(NO3)2·6H2O溶液质量比为1:1:6:4;壳聚糖溶液中壳聚糖质量占比为3~5%,其余为浓度为0.5%乙酸溶液;复合光催化剂:基体生物炭的质量比为(1~1.3):(3.7~4.3)。
与现有技术相比,本发明所达到的有益效果是:本发明创造性地以生物炭为载体,利用TiO2修饰鸟巢状钨酸铋,形成新型的生物炭-TiO2-钨酸铋复合光催化剂;解决了单一钨酸铋作为光催化剂存在催化活性差、吸收能力差、光生电子-空穴复合速率快等问题。
本发明的复合光催化剂是生物炭、TiO2、钨酸铋复合而成;生物炭是比表面积为200-300㎡/g的类球型结构,比表面积大;TiO2为块状结构,在钨酸铋中,纳米小方片层层叠加构成鸟巢状钨酸铋的圆盘表面,圆盘半径450-550nm,纳米小方片的尺寸在40-90nm;
鸟巢状钨酸铋结构上的小方片嵌入到TiO2的块状结构中形成紧密结合的异质结,附着在生物炭表面上,铋、钨、碳、氧在三元催化剂中共存且分布均匀;
生物炭、TiO2、钨酸铋均属于光催化剂,生物炭、TiO2、钨酸铋三者共同作用可以形成三元异质结,会产生协同效应,能提高复合光催化剂对紫外-可见光的吸收性能并增加光生载流子的分离效率;
在降解氟喹诺酮类抗生素中,钨酸铋与生物炭、TiO2与生物炭在进行光生电荷的迁移时均使用间接Z型电子空穴传导机制,与直接Z型体系相比,间接Z型体系中引入的电子介体可以有效降低复合光催化剂电子的传输阻力,保持光生电荷强的氧化还原能力,更有利于推动光催化反应;
本发明有利于污染土壤中微生物稳定性和多样性的快速恢复,符合环境友好性型生产要求,符合绿色持续可发展,对氟喹诺酮类抗生素污染的土壤直接进行修复,方法简单,操作方便,修复周期短,效率高,易于推广;
本发明通过在腐殖酸改性生物炭中引入ZIF-8有机框架制备得到基体生物炭,能够促进芳香族共轭-π结构的形成,有利于通过π-π电子与供体相互作用提高吸附能,生物炭能够改善ZIF-8的团聚现象,使得更多的活性点位暴露,增强生物炭的吸附容量和稳定性;同时腐殖酸改性生物炭中的腐殖酸能够抑制四氧化三铁在水体中的团聚与氧化,磁性物质能够促进吸附剂的循环利用,有效避免金属离子溶解造成的二次污染,改变了生物炭的表面结构,提高了对抗生素的吸附性能;
本发明通过壳聚糖实现复合光催化剂的固定化,制备得到改性生物炭,钨酸铋与四氧化三铁形成的异质结构,能够加速光生电子的转移,抑制了光生载流子的复合,增强了光催化活性,四氧化三铁的加入能够有效避免二氧化钛和钨酸铋的团聚,为光催化剂提供附着点位,基体生物炭与壳聚糖丰富的含氧官能团,进一步提高光催化性能,同时基体生物炭中的ZIF-8有机框架中的Zn/ZnOx纳米异质结作为活化点位与二氧化钛形成协同增强效应,构成立体催化降解复合体系,提高了光催化降解能力。
具体实施方式
下面将对本发明实施例中的技术方案进行清楚、完整地描述,显然,所描述的实施例仅仅是本发明一部分实施例,而不是全部的实施例。基于本发明中的实施例,本领域普通技术人员在没有做出创造性劳动前提下所获得的所有其他实施例,都属于本发明保护的范围。
以下实施例中,改性活性炭按如下方法制备:
将100g秸秆、稻壳和玉米芯粉碎,装入瓷坩埚中,在马弗炉中500℃煅烧,并保温2h,得到生物炭;
将20mLH2O、4mL浓硝酸、4mL钛酸四丁酯、200mL乙醇分散,在恒温磁力搅拌器上剧烈搅拌,待出现透明凝胶后停止搅拌,陈化,在105℃烘箱中烘干至恒重,得到TiO2;
将30g五水硝酸铋、0.5g十二烷基磺酸钠和10g二水钨酸钠依次溶解于200mL乙二醇中,搅拌30min后加入TiO2和生物炭粉末继续搅拌1h,将悬浮液转移到高压反应釜中,放入160℃的高温中反应5h;冷却后用无水乙醇和水反复清洗,70℃真空干燥,冷却后粉碎细化球磨处理,得到改性生物炭。
实施例1
S1:选取被环丙沙星污染的红壤进行松动处理,每1kg红壤中环丙沙星含量为10mg,使红壤含水量保持在45%,添加5%的改性生物炭;
S2:功率为500w的氙灯在20℃下对红壤进行光照48h处理。
测定光照处理前后的红壤中环丙沙星的含量,计算得出此方法对污染土壤中氟喹诺酮类抗生素的去除率为33%。
实施例2
S1:选取被恩诺沙星污染的红壤进行松动处理,每1kg红壤中含量为100mg,使红壤含水量保持在65%,添加3%的改性生物炭;
S2:功率为1000w的氙灯在30℃下对红壤进行光照48h处理。
测定光照处理前后的红壤中土霉素的含量,计算得出此方法对污染土壤中氟喹诺酮类抗生素的去除率为27%。
实施例3
S1:选取被诺氟沙星污染的红壤进行松动处理,每1kg红壤中诺氟沙星含量为250mg,使红壤含水量保持在80%,添加7%的改性生物炭;
S2:功率为1000w的氙灯在40℃下对红壤进行光照48h处理。
测定光照处理前后的红壤中诺氟沙星的含量,计算得出此方法对污染土壤中氟喹诺酮类抗生素的去除率为37%。
实施例4
将100g秸秆、稻壳和玉米芯粉碎后加入200mL浓度为3mol/L的KOH溶液中,加热至65℃搅拌2h,过滤,洗涤至pH为中性,70℃下干燥至恒重,得到碱活化颗粒;将10g碱活化颗粒和10g四氧化三铁加入到60g浓度为1mol/L的2-甲基咪唑溶液中,超声分散30min,在搅拌状态下滴入40g浓度为1mol/L的Zn(NO3)2·6H2O溶液,过滤,60℃下真空干燥至恒重,得到复合改性颗粒;将复合改性颗粒装入瓷坩埚中,在氮气气氛下置于500℃马弗炉中煅烧,并保温2h,调节pH值为7,干燥,得到基体生物炭;
将H2O、浓硝酸、钛酸四丁酯、乙醇分散,在恒温磁力搅拌器上剧烈搅拌,待出现透明凝胶后停止搅拌,陈化,在105℃烘箱中烘干至恒重,得到TiO2粗颗粒;研磨后置于500℃马弗炉中煅烧,并保温2h,得到TiO2;
将30g五水硝酸铋、0.5g表面活性剂和10g二水钨酸钠依次溶解于200mL乙二醇中,搅拌30min后加入TiO2继续搅拌1h,将悬浮液转移到高压反应釜中,放入160℃的高温中反应5h;冷却后用无水乙醇和水反复清洗,70℃真空干燥,冷却后粉碎细化球磨处理,得到复合光催化剂;将13g复合光催化剂和3.7g基体生物炭加入100mL浓度为5%的壳聚糖溶液中,搅拌均匀,得到混合溶液;将混合溶液缓慢注入500mL浓度为35%NaOH溶液中,静置,过滤,洗涤pH至中性,60℃下干燥至恒重,得到改性生物炭;
S1:选取被诺氟沙星污染的红壤进行松动处理,每1kg红壤中诺氟沙星含量为250mg,使红壤含水量保持在80%,添加7%的改性生物炭;
S2:功率为1000w的氙灯在40℃下对红壤进行光照48h处理。
测定光照处理前后的红壤中诺氟沙星的含量,计算得出此方法对污染土壤中氟喹诺酮类抗生素的去除率为45%。
对比例1
S1:选取被诺氟沙星污染的红壤进行松动处理,每1kg红壤中诺氟沙星含量为250mg,使红壤含水量保持在80%,添加7%的生物炭;
S2:功率为1000w的氙灯在40℃下对红壤进行光照48h处理。
测定光照处理前后的红壤中诺氟沙星的含量,计算得出此方法对污染土壤中氟喹诺酮类抗生素的去除率为25%。
对比例2
将100g秸秆、稻壳和玉米芯粉碎后加入200mL浓度为3mol/L的KOH溶液中,加热至65℃搅拌2h,过滤,洗涤至pH为中性,70℃下干燥至恒重,得到碱活化颗粒;将碱活化颗粒装入瓷坩埚中,在氮气气氛下置于500℃马弗炉中煅烧,并保温2h,调节pH值为7,干燥,得到基体生物炭;
将H2O、浓硝酸、钛酸四丁酯、乙醇分散,在恒温磁力搅拌器上剧烈搅拌,待出现透明凝胶后停止搅拌,陈化,在105℃烘箱中烘干至恒重,得到TiO2粗颗粒;研磨后置于500℃马弗炉中煅烧,并保温2h,得到TiO2;
将30g五水硝酸铋、0.5g表面活性剂和10g二水钨酸钠依次溶解于200mL乙二醇中,搅拌30min后加入TiO2继续搅拌1h,将悬浮液转移到高压反应釜中,放入160℃的高温中反应5h;冷却后用无水乙醇和水反复清洗,70℃真空干燥,冷却后粉碎细化球磨处理,得到复合光催化剂;将13g复合光催化剂和3.7g基体生物炭加入100mL浓度为5%的壳聚糖溶液中,搅拌均匀,得到混合溶液;将混合溶液缓慢注入500mL浓度为35%NaOH溶液中,静置,过滤,洗涤pH至中性,60℃下干燥至恒重,得到改性生物炭;
S1:选取被诺氟沙星污染的红壤进行松动处理,每1kg红壤中诺氟沙星含量为250mg,使红壤含水量保持在80%,添加7%的改性生物炭;
S2:功率为1000w的氙灯在40℃下对红壤进行光照48h处理。
测定光照处理前后的红壤中诺氟沙星的含量,计算得出此方法对污染土壤中氟喹诺酮类抗生素的去除率为32%。
对比例3
将100g秸秆、稻壳和玉米芯粉碎后加入200mL浓度为3mol/L的KOH溶液中,加热至65℃搅拌2h,过滤,洗涤至pH为中性,70℃下干燥至恒重,得到碱活化颗粒;将10g碱活化颗粒和10g四氧化三铁加入到60g浓度为1mol/L的2-甲基咪唑溶液中,超声分散30min,在搅拌状态下滴入40g浓度为1mol/L的Zn(NO3)2·6H2O溶液,过滤,60℃下真空干燥至恒重,得到复合改性颗粒;将复合改性颗粒装入瓷坩埚中,在氮气气氛下置于500℃马弗炉中煅烧,并保温2h,调节pH值为7,干燥,得到基体生物炭;
将H2O、浓硝酸、钛酸四丁酯、乙醇分散,在恒温磁力搅拌器上剧烈搅拌,待出现透明凝胶后停止搅拌,陈化,在105℃烘箱中烘干至恒重,得到TiO2粗颗粒;研磨后置于500℃马弗炉中煅烧,并保温2h,得到TiO2;
将30g五水硝酸铋、0.5g表面活性剂和10g二水钨酸钠依次溶解于200mL乙二醇中,搅拌30min后加入TiO2和基体生物炭继续搅拌1h,将悬浮液转移到高压反应釜中,放入160℃的高温中反应5h;冷却后用无水乙醇和水反复清洗,70℃真空干燥,冷却后粉碎细化球磨处理,得到改性生物炭;
S1:选取被诺氟沙星污染的红壤进行松动处理,每1kg红壤中诺氟沙星含量为250mg,使红壤含水量保持在80%,添加7%的改性生物炭;
S2:功率为1000w的氙灯在40℃下对红壤进行光照48h处理。
测定光照处理前后的红壤中诺氟沙星的含量,计算得出此方法对污染土壤中氟喹诺酮类抗生素的去除率为34%。
最后应说明的是:以上所述仅为本发明的优选实施例而已,并不用于限制本发明,尽管参照前述实施例对本发明进行了详细的说明,对于本领域的技术人员来说,其依然可以对前述各实施例所记载的技术方案进行修改,或者对其中部分技术特征进行等同替换。凡在本发明的精神和原则之内,所作的任何修改、等同替换、改进等,均应包含在本发明的保护范围之内。
Claims (5)
1.一种氟喹诺酮类抗生素污染土壤修复方法,其特征在于:所述方法包括如下步骤:
S1:选取被氟喹诺酮类抗生素污染的土壤进行松动处理,使土壤含水量为45~85%,向土壤中添加3~10%w/w的改性生物炭,得到待修复土壤;
S2:模拟太阳光照在20~40℃下对待修复土壤进行48~72h光照处理;
步骤S1中,改性生物炭为一种负载复合光催化剂的生物炭;
步骤S1中,改性生物炭的制备包括如下步骤:
将秸秆、稻壳和玉米芯粉碎后加入KOH溶液中,加热搅拌,过滤,洗涤,干燥,得到碱活化颗粒;将碱活化颗粒和四氧化三铁加入到2-甲基咪唑溶液中,超声分散,在搅拌状态下滴入Zn(NO3)2·6H2O溶液,过滤,真空干燥,得到复合改性颗粒;将复合改性颗粒装入瓷坩埚中,在氮气气氛下置于500℃马弗炉中煅烧,并保温2h,调节pH值为7,干燥,得到基体生物炭;
将五水硝酸铋、表面活性剂和二水钨酸钠依次溶解于乙二醇中,搅拌30~45min后加入TiO2继续搅拌1~2h,将悬浮液转移到高压反应釜中,放入160~200℃的高温中反应5h;冷却后用无水乙醇和水反复清洗,50~70℃真空干燥,冷却后粉碎细化球磨处理,得到复合光催化剂;将复合光催化剂和基体生物炭加入壳聚糖溶液中,搅拌均匀,得到混合溶液;将混合溶液缓慢注入NaOH溶液中,静置,过滤,洗涤pH至中性,干燥,得到改性生物炭。
2.根据权利要求1所述的一种氟喹诺酮类抗生素污染土壤修复方法,其特征在于:步骤S1中,所述土壤中氟喹诺酮类抗生素为环丙沙星、恩诺沙星、诺氟沙星中的任意一种或多种,每1kg土壤中氟喹诺酮类抗生素的含量为10~250mg。
3.根据权利要求1所述的一种氟喹诺酮类抗生素污染土壤修复方法,其特征在于:步骤S2中,光照处理使用的太阳光照为氙灯,氙灯的功率为500w或1000w中的任意一种。
4.根据权利要求1所述的一种氟喹诺酮类抗生素污染土壤修复方法,其特征在于:所述马弗炉升温速率为5~15℃/min;表面活性剂为十二烷基磺酸钠、聚乙烯吡咯烷酮中的一种或两种。
5.根据权利要求1所述的一种氟喹诺酮类抗生素污染土壤修复方法,其特征在于:所述五水硝酸铋:二水钨酸钠:TiO2的摩尔比为2:1:(2~3)。
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