卫生采伐对新源县退化野苹果无性繁殖与更新的影响
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摘要
为给野苹果的管护和更新复壮提供参考,在新疆新源县野苹果林设置样地,调查野苹果生存状况与卫生采伐后的保留体萌生枝、根蘖苗和干基苗的生长特征。针对野苹果生存状况,卫生采伐以保留存活树体为原则,将自然死亡、受病虫危害和其他自然因素损伤的部分伐除。结果表明:研究区域中,存活Ⅰ～Ⅵ级野苹果的数量比例分别为4.03%、24.19%、21.77%、1.21%、12.50%和36.29%,其中Ⅲ级～Ⅵ级属于濒危至死亡的个体占71.77%,种群数量衰亡现象严重。经卫生采伐后的野苹果林地内,存在受较轻度干扰和中度以上卫生干扰等多种野苹果个体类型,其中野苹果树受中度以上卫生干扰后形成伐桩、头木和截枝木3类数量较多的保留体,其平均高度分别为(0.58±0.25)、(2.47±0.90)和(7.59±1.99) m,基径分别为(22.33±1.76)、(23.13±2.10)和(24.52±2.06) cm,三者的基径之间有显著差异,存活率由高到低依次为截枝木、头木、伐桩。野苹果可天然繁殖根蘖苗和干基苗,伐桩、头木和截枝木3类保留体还可产生萌生枝,且萌生枝在3种无性繁殖苗中生长力最强,其次是根蘖苗,干基苗最弱,未发现萌生枝代替主干和根蘖苗建成幼树(胸径≥5 cm)的更新现象。保留体的3种无性繁殖苗中,仅萌生枝可生长发育到具有繁殖种子的能力,可开花和结果的保留体分别占26.66%和22.77%,比例由高到低依次为截枝木、头木、伐桩。尽早对衰亡严重的野苹果进行生态性的卫生采伐,既可减缓野苹果退化,又可促进保留体的无性繁殖与复壮更新。
In order to provide some references for management, protection, renewing and rejuvenating of Malus sieversii, we set up a sample plot of M. sieversii forest in Xinyuan County of Xinjiang, and investigated living conditions of M. sieversii and growth characteristics of sprouting branches, root tiller seedlings and stem base seedlings in retained plants after health cutting. Based on living conditions of M. sieversii and a principle of retained living trees, some parts were removed year by year, including natural dead, damaged by pests and diseases, and damaged by other natural factors. The results showed that: in the study area, proportions of survival grade I to VI of M. sieversii were 4.03%, 24.19%, 21.77%, 1.21%, 12.50% and 36.29%, respectively, of which grade III to VI belonged to endangered individuals and accounted for 71.77%, so the population degradation was seriously. There were many types of M. sieversii after health cutting, and living M. sieversii trees were affected mild and severe health interfering. Three kinds of main retained plants were lopping wood, head wood and stump, which were seriously interfered by health cutting, their average heights were(0.58±0.25),(2.47±0.90) and(7.59±1.99) m, respectively. Their base diameter were(22.33±1.76),(23.13±2.10) and(24.52±2.06) cm, and there was a significant difference between the base diameters. Based on survival rates from high to low, order was stump, head wood, lopping wood. M. sieversii could naturally propagate through root tiller seedlings and stem base seedlings, and three kinds of retained plants could produce sprouting branches. Sprouting branch showed the best growing power among the three asexual propagation seedlings, followed by root tiller seedling, and stem base seedling was the weakest. There was no renewing phenomenon that sprouting branch replace trunk and root tiller seedlings to build young trees(diameter at breast height ≥ 5 cm). Among the three types of asexual propagation seedlings of retained plants, only sprouting branch had the ability to reproduce seeds. The flowering and fruiting retained plants accounted for 26.66% and 22.77%, respectively, and order was lopping wood, head wood, stump based on the percentage from high to low. Ecological health cutting should be carried out in severe degraded M. sieversii forest as soon as possible. It not only could slow down degradation of M. sieversii, but also could promote asexual propagation, renewing and rejuvenating of retained plants.
In order to provide some references for management, protection, renewing and rejuvenating of Malus sieversii, we set up a sample plot of M. sieversii forest in Xinyuan County of Xinjiang, and investigated living conditions of M. sieversii and growth characteristics of sprouting branches, root tiller seedlings and stem base seedlings in retained plants after health cutting. Based on living conditions of M. sieversii and a principle of retained living trees, some parts were removed year by year, including natural dead, damaged by pests and diseases, and damaged by other natural factors. The results showed that: in the study area, proportions of survival grade I to VI of M. sieversii were 4.03%, 24.19%, 21.77%, 1.21%, 12.50% and 36.29%, respectively, of which grade III to VI belonged to endangered individuals and accounted for 71.77%, so the population degradation was seriously. There were many types of M. sieversii after health cutting, and living M. sieversii trees were affected mild and severe health interfering. Three kinds of main retained plants were lopping wood, head wood and stump, which were seriously interfered by health cutting, their average heights were(0.58±0.25),(2.47±0.90) and(7.59±1.99) m, respectively. Their base diameter were(22.33±1.76),(23.13±2.10) and(24.52±2.06) cm, and there was a significant difference between the base diameters. Based on survival rates from high to low, order was stump, head wood, lopping wood. M. sieversii could naturally propagate through root tiller seedlings and stem base seedlings, and three kinds of retained plants could produce sprouting branches. Sprouting branch showed the best growing power among the three asexual propagation seedlings, followed by root tiller seedling, and stem base seedling was the weakest. There was no renewing phenomenon that sprouting branch replace trunk and root tiller seedlings to build young trees(diameter at breast height ≥ 5 cm). Among the three types of asexual propagation seedlings of retained plants, only sprouting branch had the ability to reproduce seeds. The flowering and fruiting retained plants accounted for 26.66% and 22.77%, respectively, and order was lopping wood, head wood, stump based on the percentage from high to low. Ecological health cutting should be carried out in severe degraded M. sieversii forest as soon as possible. It not only could slow down degradation of M. sieversii, but also could promote asexual propagation, renewing and rejuvenating of retained plants.
引文
[1]缪宁,刘世荣,史作民,等.强度干扰后退化森林生态系统中保留木的生态效应研究综述[J].生态学报,2013, 33(13):3889-3897.
[2]史济彦,肖生灵.生态性采伐系统[M].哈尔滨:东北林业大学出版社,2001.
[3]朱之悌.树木的无性繁殖与无性系育种[J].林业科学,1986,22(3):280-290.
[4]王祝雄,吴秀丽.森林抚育规程解读[M].北京:中国林业出版社,2016.
[5]张会儒.落叶松云冷杉林生长模拟及生态采伐更新技术体系研究[D].北京:中国林业科学研究院, 2006.
[6]姜秀荣,王秋波,张光美.人工林抚育效益显著:人工落叶松透光抚育间伐效益、生长量与存在问题关系的调查[J].中国林业,2010(18):46.
[7]杨保林,张文辉,周建云.秦岭北坡不同干扰条件下栓皮栎无性繁殖在其种群更新中的作用[J].东北林业大学学报,2010,38(10):27-29,43.
[8]薛瑶芹,张文辉,周建云,等.秦岭南坡不同生境条件下栓皮栎伐桩萌芽特性[J].林业科学,2011,47(7):57-64.
[9]马闯,张文辉,薛瑶芹,等.邻体竞争和环境因子对栓皮栎伐桩萌苗表型特征的影响[J].西北农林科技大学学报(自然科学版),2011,39(10):71-80.
[10]邓磊,张文辉,何景峰,等.不同采伐强度对辽东栎林幼苗更新的影响[J].西北林学院学报,2011,26(2):160-166.
[11]荆涛,马万里,KUJANSUU J,等.水曲柳萌芽更新的研究[J].北京林业大学学报,2002,24(4):12-15.
[12] PACIOREK C J, CONDIT R, HUBBELL S P, et al. The demographics of resprouting in tree and shrub species of a moist tropical forest[J]. Journal of Ecology,2000,88(5):765-777.
[13] MWAVU E N, WITKOWSKI E T F. Sprouting of woody species following cutting and tree-fall in a lowland semi-deciduous tropical rainforest, North-Western Uganda[J]. Forest Ecology&Management, 2008,255(3/4):982-992.
[14]何东,魏新增,李连发,等.神农架山地河岸带连香树的种群结构与动态[J].植物生态学报,2009,33(3):469-481.
[15]卢志军.栓皮栎种群生殖生态学研究[D].杨凌:西北农林科技大学,2002.
[16]张新时.伊犁野果林的生态地理特征和群落学问题[J].植物生态学报,1973,15(2):95-109.
[17]徐佳宁,刘钢,马盼,等.新疆野苹果逆境响应机制研究进展[J].山东农业科学,2014,46(8):138-141.
[18]李飞飞,崔大方,廖文波,等.中国新疆野苹果种群地理分布格局及其遗传关系研究[J].干旱区地理,2011,34(6):926-932.
[19]阎国荣,张立运,许正.天山野果林生态系统受损现状及其保护[J].干旱区研究,1999,16(4):1-4.
[20]刘忠权,陈卫民,许正,等.新疆天山西部野苹果林分布与苹果小吉丁虫危害现状研究[J].北方园艺,2014(17):121-124.
[21]梅闯,闫鹏,艾沙江·买买提,等.新疆野苹果(Malus sieversii)受苹小吉丁虫危害程度与树皮厚度、径阶的关系[J].中国农业科技导报,2016,18(4):24-30.
[22]房冰,段辛乐,张彦龙,等.苹果小吉丁虫微卫星开发及其种群遗传结构分析[J].植物保护学报,2017,44(4):559-566.
[23]阎国荣,许正.天山野生果树主要病害及其分布[J].干旱区研究,2001,18(2):47-49.
[24]林培钧,崔乃然.天山野果林资源:伊犁野果林综合研究[M].北京:中国林业出版社,2000.
[25]沈国舫.森林培育学[M].北京:中国林业出版社,2001.
[26] BELLINGHAM P J, SPARROW A D. Resprouting as a life history strategy in woody plant communities[J]. Oikos, 2000,89(2):409-416.
[27]吴明作,刘玉萃,姜志林.栓皮栎种群生殖生态与稳定性机制研究[J].生态学报,2001,21(2):225-230.
[28]薛瑶芹,张文辉,马闯,等.秦岭北坡栓皮栎干基萌苗生长特性研究[J].西北农林科技大学学报(自然科学版),2014,42(9):70-77.
[29] GOTO Y, YOSHITAKE T, OKANO M, et al. Seedling regeneration and vegetative resprouting after fires in Pinus densiflora forests[J]. Vegetatio,1996,122(2):157-165.
[30]董喜斌.落叶松人工林生态采伐模式及评价[D].哈尔滨:东北林业大学,2008.
[31] LOCKHART B R, CHAMBERS J L. Cherrybark oak stump sprout survival and development five years following plantation thinning in the lower Mississippi alluvial valley, USA[J]. New Forests, 2007,33(2):183-192.
[32]唐建维,施济普,张光明,等.西双版纳不同斑块望天树种群的密度、结构和生物量[J].植物生态学报,2008,32(1):40-54.
[33] SUH M H, LEE D K. Stand structure and regeneration of Quercus mongolica forests in Korea[J]. Forest Ecology&Management, 1998,106(1):27-34.
[34]曹德昌,李景文,陈维强,等.额济纳绿洲不同林隙胡杨根蘖的发生特征[J].生态学报,2008,29(4):1954-1961.
[35]武逢平,李俊清,李景文,等.胡杨(Populus euphratica)在额济纳绿洲三种生境内的根蘖繁殖特性[J].生态学报,2008,28(10):4703-4709.
[36]李景文,聂绍荃,安滨河.东北东部林区次生林主要阔叶树种的萌芽更新规律[J].林业科学,2005,41(6):75-80.
[37]夏玉洁,姚小华,王开良,等.不同无性系山核桃结果性状对比分析[J].中南林业科技大学学报,2018,38(11):53-60.
[38]古巧云,胡德活,黄光亮,等.南洋楹无性系种子园生长种实评价[J].中南林业科技大学学报,2019,39(4):16-21.
[39]夏玉洁,傅松玲,姚小华,等.22个山核桃无性系树体性状的比较[J].经济林研究,2017,35(4):231-235.
[40]龚发萍,石卓功,黄佳聪,等.怒江流域滇橄榄优树选择及优树无性系早期测定[J].经济林研究,2018,36(1):23-28.
[2]史济彦,肖生灵.生态性采伐系统[M].哈尔滨:东北林业大学出版社,2001.
[3]朱之悌.树木的无性繁殖与无性系育种[J].林业科学,1986,22(3):280-290.
[4]王祝雄,吴秀丽.森林抚育规程解读[M].北京:中国林业出版社,2016.
[5]张会儒.落叶松云冷杉林生长模拟及生态采伐更新技术体系研究[D].北京:中国林业科学研究院, 2006.
[6]姜秀荣,王秋波,张光美.人工林抚育效益显著:人工落叶松透光抚育间伐效益、生长量与存在问题关系的调查[J].中国林业,2010(18):46.
[7]杨保林,张文辉,周建云.秦岭北坡不同干扰条件下栓皮栎无性繁殖在其种群更新中的作用[J].东北林业大学学报,2010,38(10):27-29,43.
[8]薛瑶芹,张文辉,周建云,等.秦岭南坡不同生境条件下栓皮栎伐桩萌芽特性[J].林业科学,2011,47(7):57-64.
[9]马闯,张文辉,薛瑶芹,等.邻体竞争和环境因子对栓皮栎伐桩萌苗表型特征的影响[J].西北农林科技大学学报(自然科学版),2011,39(10):71-80.
[10]邓磊,张文辉,何景峰,等.不同采伐强度对辽东栎林幼苗更新的影响[J].西北林学院学报,2011,26(2):160-166.
[11]荆涛,马万里,KUJANSUU J,等.水曲柳萌芽更新的研究[J].北京林业大学学报,2002,24(4):12-15.
[12] PACIOREK C J, CONDIT R, HUBBELL S P, et al. The demographics of resprouting in tree and shrub species of a moist tropical forest[J]. Journal of Ecology,2000,88(5):765-777.
[13] MWAVU E N, WITKOWSKI E T F. Sprouting of woody species following cutting and tree-fall in a lowland semi-deciduous tropical rainforest, North-Western Uganda[J]. Forest Ecology&Management, 2008,255(3/4):982-992.
[14]何东,魏新增,李连发,等.神农架山地河岸带连香树的种群结构与动态[J].植物生态学报,2009,33(3):469-481.
[15]卢志军.栓皮栎种群生殖生态学研究[D].杨凌:西北农林科技大学,2002.
[16]张新时.伊犁野果林的生态地理特征和群落学问题[J].植物生态学报,1973,15(2):95-109.
[17]徐佳宁,刘钢,马盼,等.新疆野苹果逆境响应机制研究进展[J].山东农业科学,2014,46(8):138-141.
[18]李飞飞,崔大方,廖文波,等.中国新疆野苹果种群地理分布格局及其遗传关系研究[J].干旱区地理,2011,34(6):926-932.
[19]阎国荣,张立运,许正.天山野果林生态系统受损现状及其保护[J].干旱区研究,1999,16(4):1-4.
[20]刘忠权,陈卫民,许正,等.新疆天山西部野苹果林分布与苹果小吉丁虫危害现状研究[J].北方园艺,2014(17):121-124.
[21]梅闯,闫鹏,艾沙江·买买提,等.新疆野苹果(Malus sieversii)受苹小吉丁虫危害程度与树皮厚度、径阶的关系[J].中国农业科技导报,2016,18(4):24-30.
[22]房冰,段辛乐,张彦龙,等.苹果小吉丁虫微卫星开发及其种群遗传结构分析[J].植物保护学报,2017,44(4):559-566.
[23]阎国荣,许正.天山野生果树主要病害及其分布[J].干旱区研究,2001,18(2):47-49.
[24]林培钧,崔乃然.天山野果林资源:伊犁野果林综合研究[M].北京:中国林业出版社,2000.
[25]沈国舫.森林培育学[M].北京:中国林业出版社,2001.
[26] BELLINGHAM P J, SPARROW A D. Resprouting as a life history strategy in woody plant communities[J]. Oikos, 2000,89(2):409-416.
[27]吴明作,刘玉萃,姜志林.栓皮栎种群生殖生态与稳定性机制研究[J].生态学报,2001,21(2):225-230.
[28]薛瑶芹,张文辉,马闯,等.秦岭北坡栓皮栎干基萌苗生长特性研究[J].西北农林科技大学学报(自然科学版),2014,42(9):70-77.
[29] GOTO Y, YOSHITAKE T, OKANO M, et al. Seedling regeneration and vegetative resprouting after fires in Pinus densiflora forests[J]. Vegetatio,1996,122(2):157-165.
[30]董喜斌.落叶松人工林生态采伐模式及评价[D].哈尔滨:东北林业大学,2008.
[31] LOCKHART B R, CHAMBERS J L. Cherrybark oak stump sprout survival and development five years following plantation thinning in the lower Mississippi alluvial valley, USA[J]. New Forests, 2007,33(2):183-192.
[32]唐建维,施济普,张光明,等.西双版纳不同斑块望天树种群的密度、结构和生物量[J].植物生态学报,2008,32(1):40-54.
[33] SUH M H, LEE D K. Stand structure and regeneration of Quercus mongolica forests in Korea[J]. Forest Ecology&Management, 1998,106(1):27-34.
[34]曹德昌,李景文,陈维强,等.额济纳绿洲不同林隙胡杨根蘖的发生特征[J].生态学报,2008,29(4):1954-1961.
[35]武逢平,李俊清,李景文,等.胡杨(Populus euphratica)在额济纳绿洲三种生境内的根蘖繁殖特性[J].生态学报,2008,28(10):4703-4709.
[36]李景文,聂绍荃,安滨河.东北东部林区次生林主要阔叶树种的萌芽更新规律[J].林业科学,2005,41(6):75-80.
[37]夏玉洁,姚小华,王开良,等.不同无性系山核桃结果性状对比分析[J].中南林业科技大学学报,2018,38(11):53-60.
[38]古巧云,胡德活,黄光亮,等.南洋楹无性系种子园生长种实评价[J].中南林业科技大学学报,2019,39(4):16-21.
[39]夏玉洁,傅松玲,姚小华,等.22个山核桃无性系树体性状的比较[J].经济林研究,2017,35(4):231-235.
[40]龚发萍,石卓功,黄佳聪,等.怒江流域滇橄榄优树选择及优树无性系早期测定[J].经济林研究,2018,36(1):23-28.