紫茎泽兰种内竞争试验

紫茎泽兰(Eupatorium adenophorum)是一种入侵能力极强的世界性恶性杂草.通过不同种植密度的紫茎泽兰盆栽试验,探讨种内竞争对紫茎泽兰个体生长的影响.结果表明,种内竞争降低了紫茎泽兰个体株高、叶片数、根蘖株数和生物量的增长.种植密度与生物量2者的对数值呈负相关关系(r2=0.99,斜率=-5/6).同时,随着种植密度增加,种内竞争加剧,抑制作用增强,种群内部大小等级差异也增大,表明不同个体受到了不同的拥挤压力.但是,高密度的紫茎泽兰种群在强烈竞争下,个体会控制根蘖株的形成、死亡,从而减少资源的消耗,保证种群对生境的长期占领.建议在进行紫茎泽兰的替代控制时,应注意替代物种的先植,选择优于紫茎泽兰萌发的植物作为替代物种,通过邻体干扰效应抑制紫茎泽兰的生长.     

黑麦草与入侵杂草紫茎泽兰苗期的相对竞争力

为研究利用黑麦草(Lolium perenne)替代种植治理外来入侵杂草紫茎泽兰(Eupatorium adenophorum)再入侵或新入侵丢荒地,采取复合deWit取代试验设计方法用盆栽植物研究了黑麦草和紫茎泽兰在苗期的相对竞争力,观察在若干密度梯度每密度下不同比例条件下两种植物的相对产量、相对产量总和以及竞争攻击力等参数,并比较其表型特征在不同竞争格局下的异同.黑麦草与紫茎泽兰在所有密度及其比例下的相对产量总和(RYT)均近似于1.0,说明这两种植物面临着对相同资源的直接竞争.竞争的结果是,在所有密度及其比例下,紫茎泽兰混种时的生物量均显著小于单种时的生物量(即相对产量RY小于1.0);而黑麦草的相对产量(RY)变化则恰恰相反.黑麦草的株高和地上生物量并不受混种竞争的显著影响(与单种无显著差异),分蘖数反而高于单种,表现出很强的竞争性;而紫茎泽兰在混种竞争下的株高、分株数和地上生物量均显著低于单种(无竞争),表现出较弱的竞争性.对利用黑麦草替代种植治理紫茎泽兰在机械防治后再入侵以及对丢荒地新入侵问题的可行性进行了讨论.图1表3参18     

紫茎泽兰和飞机草在广西的入侵生境植物多样性分析

对紫茎泽兰（Eupatorium adenophorum）和飞机草（Eupatorium odoratum）在广西入侵生境的植物多样性进行了研究。结果表明：在紫茎泽兰、飞机草发生危害的生境,Simpson指数、Shannon-Wiener指数、Pielou均匀度指数均比没有紫茎泽兰、飞机草危害的生境低。在紫茎泽兰样方中,有紫茎泽兰入侵的生境其上述各指数分别比没有紫茎泽兰入侵的低43.65%、55.13%、55.68%。而在飞机草样方中,有飞机草入侵的生境其上述各指数分别比没有飞机草入侵的低33.55%、37.78%、17.98%。说明紫茎泽兰和飞机草对入侵生境的植物多样性影响较大。     

外来入侵植物紫茎泽兰对昆明地区土壤动物群落的影响

2005年雨季前后的6月至9月,共布设144个样方,采样分析了外来入侵植物紫茎泽兰(Eupatorium adeno-phorum)对云南昆明地区针叶林、阔叶林和草地3种主要生态系统类型地表腐叶层土壤动物群落的影响。研究结果表明,紫茎泽兰入侵后土壤动物类群总数显著减少,其中针叶林减少41.3%,阔叶林减少29.0%,草地减少36.7%;土壤动物群落个体总数下降,其中针叶林减少63.5%,阔叶林减少20.4%,草地减少43.2%。紫茎泽兰入侵影响土壤动物群落多样性和均匀度。6月至8月,在没有紫茎泽兰入侵情况下,针叶林和草地生态系统土壤动物群落多样性、均匀度逐步升高;紫茎泽兰入侵后,由于土壤动物类群数量及部分类群个体数量减少,针叶林和草地土壤动物群落多样性、均匀度有所降低。     

紫茎泽兰与伴生植物小藜的竞争效应及其生理生化特征

外来入侵物种紫茎泽兰（Ageratina adenophora Sprengel）是一种世界性入侵杂草,其与本地物种的竞争会对生态系统结构和演替造成严重影响,带来较大经济损失;拟通过分析紫茎泽兰与本地物种小藜的竞争效应及生理生化特征,以探讨外来入侵物种紫茎泽兰的竞争机理。在温室条件下,设置紫茎泽兰、小藜（Chenopodium serotinum）的种内和种间竞争盆栽试验,测定了两种植物不同处理下的植株生物量;并通过氮蓝四唑光化还原法、紫外吸收法、三氯乙酸法和酸性茚三酮法,分别测定了功能叶片的超氧化物歧化酶活性、过氧化氢酶活性、丙二醛含量、脯氨酸含量。结果表明：紫茎泽兰与小藜混种时,紫茎泽兰的单株生物量、相对产量（RY）均显著高于小藜对应指标,其竞争平衡指数（CB）显著大于0,而相对产量总和（RYT）显著小于1。混种与单种的结果比较表明,紫茎泽兰的混种生物量比在单种时显著增高,增幅达22.01%;而小藜的混种生物量比在单种时显著降低,降低了44.81%。在混种中,紫茎泽兰功能叶片的丙二醛、脯氨酸含量均比在单种时显著降低,而超氧化物歧化酶、过氧化氢酶活性均比在单种时显著升高;小藜功能叶片的丙二醛含量显著高于单种,而脯氨酸含量、超氧化物歧化酶活性、过氧化氢酶活性与单种无显著变化。这说明紫茎泽兰的相对竞争能力比小藜强,紫茎泽兰通过调整生理生化特征来应对种间竞争可能是其竞争取胜的重要策略。     

UV-B辐射增强对紫茎泽兰和艾草生长形态及竞争效应的影响

为了解外来入侵植物紫茎泽兰(Eupatorium adenophorum L.)与本地土著植物艾草(Artemisia argyi Levl)在UV-B辐射增强条件下生长形态和竞争关系的变化,以这两种植物为试验材料,以自然光为对照进行5周UV-B辐射增强实验和2周恢复实验,并测定和分析植株形态指标(株高、叶片鲜重、叶长、叶宽和叶面积)、叶片解剖结构(上下表皮、栅栏组织和海绵组织)和竞争能力指标(株高、叶生物量和茎生物量).结果显示:艾草叶片鲜重和叶面积在辐射前两周显著减小(P0.05)和极显著减小(P0.01),株高没有差异,而紫茎泽兰的株高、叶鲜重和叶面积在辐射期间都明显减小,且恢复实验时仍差异显著.艾草叶片厚度在UV-B辐射下极显著增大(上表皮、栅栏组织和海绵组织极显著增大),紫茎泽兰叶片变厚但不明显,恢复实验时显著减小,叶片解剖结构表明UV-B辐射使两类杂草叶片细胞间隙变大.UV-B辐射对紫茎泽兰生物量的抑制比较显著,对艾草生物量的抑制在混种时显著;在UV-B辐射下,紫茎泽兰和艾草的相对生物量分别为1.03和0.81,在自然状态下分别为0.91和0.97,两者的相对生物量总和不变,为0.94.本研究表明艾草对UV-B辐射的形态抗性较强,UV-B辐射刺激了紫茎泽兰的种内竞争,也降低了艾草的种间竞争能力,但无论在自然条件下还是UV-B辐射增强条件下艾草的种间竞争能力都比紫茎泽兰强,但不足以淘汰对方.     

Pb、Cd及其复合污染对紫茎泽兰生长及吸收富集特征的影响

外来植物紫茎泽兰（Eupatorium adenophorum）入侵我国西南地区并造成了严重的生态灾难,通过研究Pb、Cd及其复合污染对紫茎泽兰生长及吸收富集特征的影响,有助于从生态学角度为紫茎泽兰的综合防控提供依据。采用模拟Pb、Cd污染土壤培养法研究了不同浓度Pb、Cd及其复合污染作用下紫茎泽兰的生长响应及重金属吸收、富集和迁移特征变化。结果表明：低浓度的Pb、Cd对紫茎泽兰的生长有促进作用,高浓度则表现出一定的抑制作用,生物量,株高,根长均明显减少。紫茎泽兰体内Pb、Cd吸收量与污染土壤具有良好的相关性,随处理浓度增加明显增大,极端浓度Pb、Cd胁迫下紫茎泽兰各器官Pb、Cd积累量与对照相比显著增加,1000 mg·kg-1处理时紫茎泽兰根、茎、叶的Pb质量分数均分别高达603.69、568.31、598.85 mg·kg-1;100 mg·kg-1 Cd处理时其根、茎、叶的Pb、Cd累积量依次为165.21、93.59、152.79 mg·kg-1。说明紫茎泽兰对Pb、Cd具有较好吸收累积及转运能力,可作为重金属污染地区的一种理想的修复植物。     

外来植物紫茎泽兰入侵对根际土壤有益功能细菌群、酶活性和肥力的影响

通过对紫茎泽兰不同入侵阶段下的实地采样,分析了外来入侵植物紫茎泽兰对入侵地根际土壤有益微生物菌群和土壤酶活性以及肥力的影响。发现除了全磷、全钾以外,重度入侵土壤的功能菌数量、酶活性、土壤肥力都要显著高于其它土壤区系。根际土中有机磷细菌差异最显著,其重度入侵土中的含量是轻度入侵土中含量的3.0倍,是当地植物土中含量的1.8倍,是空白地区含量的22.2倍。同时,土壤微生物类群、土壤酶活与土壤肥力的相关分析表明,它们之间存在显著相关关系,自生固氮菌与全氮相关性最明显,为0.922。外来植物对入侵地的影响是其入侵力和生态系统可入侵性的重要组成部分,紫茎泽兰入侵提高了土壤功能菌种群和土壤酶活,从而使土壤肥力也发生了相应的变化,这可能促进其养分转化吸收,提高种群竞争力。本文为紫茎泽兰成功入侵的土壤微生物学机制提供理论依据。     

外来入侵植物紫茎泽兰对土壤养分的影响

选取云南、四川省3个不同生境作为样地,研究紫茎泽兰入侵对不同生态系统土壤中碱解氮、速效磷、速效钾含量的影响.结果表明,紫茎泽兰入侵造成样地a土壤碱解氮、速效磷、速效钾含量分别显著下降33.9%、44.2%和32.2%;样地b仅土壤速效磷显著下降31.0%;样地c土壤各营养元素未见显著变化.在不同时间,样地a处理组各营养元素含量基本低于对照组,以2005年7月至10月的差异最显著.这说明紫茎泽兰入侵对土壤养分的影响因生境不同而异,且与紫茎泽兰的生长节律有关.     

不同林木种群对紫茎泽兰营养生长和生殖生长的影响

外来植物紫茎泽兰（Eupatorlum adenophorum）入侵我国西南地区并造成了严重的生态灾难,通过研究不同林木种群下紫茎泽兰的生长特性和发生规律,有助于从生态学角度为紫茎泽兰的综合防控提供事实依据。我们分别于2009、2011和2012年在西昌袁家山上开展了不同人工林木群落下紫茎泽兰营养生长和生殖生长特性的调查。调查研究的结果表明,阔叶林（青冈林）、阔叶针叶混交林（油茶柏树混交林）和阔叶混交林（油茶青冈混交林）下光照强度显著低于两种针叶林（落叶松林和柏树林）和空旷地,光照强度较空旷地减少率均在90％以上。空旷地紫茎泽兰的发生密度可达到111-218株·m-2,两种针叶林（落叶松林和柏树林）对紫茎泽兰的发生表现出一定的抑制作用,抑制率能达到46．2％～77．1％。油茶柏树混交林和青冈林下紫茎泽兰只有零星发生,对紫茎泽兰发生抑制率3年均在90％以上,而在油茶青冈混交林下未发现有紫茎泽兰发生。空旷地紫茎泽兰株高和分枝数均要显著高于其他人工林木群落,单株株高可达160．5～180．3cm,单株分枝数达到14．9～17．4,其中两种针叶林下紫茎泽兰的株高和分枝数要显著高于两种混交林和青冈林,株高达到59．5～113．4cm,单株分枝数为6．4～14．8。此外种植人工林木也显著抑制了紫茎泽兰的开花结实,空旷地紫茎泽兰单株种子量能达到8314～15410粒,两种针叶林（落叶松林和柏树林）下紫茎泽兰单株种子发生量为1330-4666-3粒,而两种混交林和青冈林下紫茎泽兰只有零星开花或不开花结实。相关性分析结果显示,光照强度的大小与紫茎泽兰的发生密度、株高、分枝数、单株花苞数、单株种子数都呈显著正相关,即光照强度显著影响着紫茎泽兰的发生密度、生长以及开花结实。阔叶林下光照强度的减弱是导致紫茎泽兰发生量减少原因之一。开展植树造林,采用种植青冈林、油茶青冈、油茶柏树混交林等阔叶混栽的方式对紫茎泽兰的发生不仅能起到显著的生态控制效果,而且能绿化荒山,给农民带来经济效益。     

Role of Light Availability and Dispersal in Exotic Plant Invasion along Roads and Streams in the H. J. Andrews Experimental Forest, Oregon

Abstract: We examined the roles of dispersal mechanism, a biological barrier; light availability, an environmental barrier; and level of disturbance, a physical barrier, in explaining the spatial patterns of exotic plant species along road and stream segments in a forest landscape in the western Cascade Range of Oregon (U.S.A). The presence or absence of 21 selected exotic plant species and light levels were observed along 0.3- to 1.0-km transects within four habitat types. Each habitat represented a different level of disturbance: high-use roads, low-use roads, abandoned roads, and streams in the H. J. Andrews Experimental Forest. Nearly 300 50 × 2–m sampling units were surveyed along five transects in each habitat type. We used ordination (nonmetric multidimensional scaling) and logistic regression to analyze data. All of the nearly 200 sampling units along roads with high and low levels of vehicle traffic contained at least one exotic plant species, and some contained as many as 14. Streams that were most recently disturbed by floods 20–30 years ago and abandoned spur roads with no traffic for 20–40 years also had numerous exotic species. Roads and streams apparently serve multiple functions that enhance exotic species invasion in this landscape: they act as corridors or agents for dispersal, provide suitable habitat, and contain reservoirs of propagules for future episodes of invasion. Species-specific dispersal mechanisms, habitat characteristics, and disturbance history each explain some, but not all, of the patterns of exotic species invasion observed in this study.     

Characterizing the landscape dynamics of an invasive plant and risk of invasion using remote sensing.

Improved understanding of the spatial dynamics of invasive plant species may lead to more effective land management and reduced future invasion. Here, we identified the spatial extents of nonnative cheatgrass (Bromus tectorum) in the north central Great Basin using remotely sensed data from Landsat MSS, TM, and ETM+. We compared cheatgrass extents in 1973 and 2001 to six spatially explicit landscape variables: elevation, aspect, hydrographic channels, cultivation, roads, and power lines. In 2001, Cheatgrass was 10% more likely to be found in elevation ranges from 1400 to 1700 m (although the data suggest a preferential invasion into lower elevations by 2001), 6% more likely on west and northwest facing slopes, and 3% more likely within hydrographic channels. Over this time period, cheatgrass expansion was also closely linked to proximity to land use. In 2001, cheatgrass was 20% more likely to be found within 3 km of cultivation, 13% more likely to be found within 700 m of a road, and 15% more likely to be found within 1 km of a power line. Finally, in 2001 cheatgrass was 26% more likely to be present within 150 m of areas occupied by cheatgrass in 1973. Using these relationships, we created a risk map of future cheatgrass invasion that may aid land management. These results highlight the importance of including land use variables and the extents of current plant invasion in predictions of future risk.     

Estimating non-native plant richness with a species-accumulation model along roads

Monitoring non-native plant richness is important for biodiversity conservation and scientific research. The species-area model (SA model) has been used frequently to estimate the total species richness within a region. However, the conventional SA model may not provide robust estimations of non-native plant richness because the ecological processes associated with the accumulation of exotic and native plants may differ. Because roads strongly dictate the distributions of exotic plants, we propose a species-accumulation model along roads (SR model), rather than an SA model, to estimate the non-native plant richness within a region. Using 270 simulated data sets, we compared the differences in performance between the SR and SA models. A decision tree based on prediction accuracy was created to guide model application, which was validated using field data from 3 national nature reserves in 3 different provinces in China. The SR model significantly outperformed the SA model when non-native species were restricted to the roadsides and the proportion of uncommon exotic species was small. More importantly, the SR model accurately estimated the non-native plant richness in all field sites with an error of <1 species per site. We believe our new model meets the practical need to efficiently and robustly estimate non-native plant richness, which may facilitate effective biodiversity conservations and promote research on non-native plant invasion and vegetation dynamics.     

The Role of Roadsides in Plant Invasions: a Demographic Approach

Abstract:  Non-native plant species are common along roadsides, but presence does not necessarily indicate spread along the road axis. Roadsides may serve merely as habitat for a species spreading independently of roads. The potential conduit function of roads depends on the habitat specificity of the spreading species, its dispersal range relative to the spacing of roads in the landscape, and the relative importance of long- and short-range dispersal. We describe a demographic model of the road × species interaction and suggest methods of assessing conduit function in the field based on the model results. A species limited to roadside habitat will be constrained to spread along the road axis unless its long-range dispersal is sufficient to carry it across the intervening unfavorable area to another road. It will propagate along a road corridor at a rate determined by the scale of short-range dispersal. Effective management of an invasion requires distinguishing between the habitat and conduit functions, a distinction difficult to make with only snapshot data. Invasions can be reconstructed by several methods, but none is totally satisfactory. We suggest comparing stem distributions on transects parallel and perpendicular to the road axis, and beside the road, and away from it, with an idealized Gaussian curve. Such comparisons would allow discrimination between pattern determined by habitat suitability and pattern reflecting random and facilitated dispersal.     

The Ecological Road-Effect Zone of a Massachusetts (U.S.A.) Suburban Highway

Abstract: Ecological flows and biological diversity trace broad patterns across the landscape, whereas transportation planning for human mobility traditionally focuses on a narrow strip close to a road or highway. To help close this gap we examined the "road-effect zone" over which significant ecological effects extend outward from a road. Nine ecological factors—involving wetlands, streams, road salt, exotic plants, moose, deer, amphibians, forest birds, and grassland birds—were measured or estimated near 25 km of a busy four-lane highway west of Boston, Massachusetts. The effects of all factors extended > 100 m from the road, and moose corridors, road avoidance by grassland birds, and perhaps road salt in a shallow reservoir extended outwards > 1 km. Most factors had effects at 2–5 specific locations, whereas traffic noise apparently exerted effects along most of the road length. Creating a map of these effects indicates that the road-effect zone averages approximately 600 m in width and is asymmetric, with convoluted boundaries and a few long fingers. We conclude that busy roads and nature reserves should be well separated, and that future transportation systems across landscapes can provide for ecological flows and biological diversity in addition to safe and efficient human mobility.     

Salamander Abundance along Road Edges and within Abandoned Logging Roads in Appalachian Forests

Abstract:  Roads may be one of the most common disturbances in otherwise continuous forested habitat in the southern Appalachian Mountains. Despite their obvious presence on the landscape, there is limited data on the ecological effects along a road edge or the size of the "road-effect zone." We sampled salamanders at current and abandoned road sites within the Nantahala National Forest, North Carolina (U.S.A.) to determine the road-effect zone for an assemblage of woodland salamanders. Salamander abundance near the road was reduced significantly, and salamanders along the edges were predominantly large individuals. These results indicate that the road-effect zone for these salamanders extended 35 m on either side of the relatively narrow, low-use forest roads along which we sampled. Furthermore, salamander abundance was significantly lower on old, abandoned logging roads compared with the adjacent upslope sites. These results indicate that forest roads and abandoned logging roads have negative effects on forest-dependent species such as plethodontid salamanders. Our results may apply to other protected forests in the southern Appalachians and may exemplify a problem created by current and past land use activities in all forested regions, especially those related to road building for natural-resource extraction. Our results show that the effect of roads reached well beyond their boundary and that abandonment or the decommissioning of roads did not reverse detrimental ecological effects; rather, our results indicate that management decisions have significant repercussions for generations to come. Furthermore, the quantity of suitable forested habitat in the protected areas we studied was significantly reduced: between 28.6% and 36.9% of the area was affected by roads. Management and policy decisions must use current and historical data on land use to understand cumulative impacts on forest-dependent species and to fully protect biodiversity on national lands     

Predicting species distributions from samples collected along roadsides

Predictive models of species distributions are typically developed with data collected along roads. Roadside sampling may provide a biased (nonrandom) sample; however, it is currently unknown whether roadside sampling limits the accuracy of predictions generated by species distribution models. We tested whether roadside sampling affects the accuracy of predictions generated by species distribution models by using a prospective sampling strategy designed specifically to address this issue. We built models from roadside data and validated model predictions at paired locations on unpaved roads and 200 m away from roads (off road), spatially and temporally independent from the data used for model building. We predicted species distributions of 15 bird species on the basis of point-count data from a landbird monitoring program in Montana and Idaho (U.S.A.). We used hierarchical occupancy models to account for imperfect detection. We expected predictions of species distributions derived from roadside-sampling data would be less accurate when validated with data from off-road sampling than when it was validated with data from roadside sampling and that model accuracy would be differentially affected by whether species were generalists, associated with edges, or associated with interior forest. Model performance measures (kappa, area under the curve of a receiver operating characteristic plot, and true skill statistic) did not differ between model predictions of roadside and off-road distributions of species. Furthermore, performance measures did not differ among edge, generalist, and interior species, despite a difference in vegetation structure along roadsides and off road and that 2 of the 15 species were more likely to occur along roadsides. If the range of environmental gradients is surveyed in roadside-sampling efforts, our results suggest that surveys along unpaved roads can be a valuable, unbiased source of information for species distribution models.     

"The upper limits of vegetation on Mauna Loa, Hawaii": a 50th-anniversary reassessment

In January 1958, a survey of alpine flora was conducted along a recently constructed access road across the upper volcanic slopes of Mauna Loa, Hawaii (2525-3397 m). Only five native Hawaiian species were encountered on sparsely vegetated historic and prehistoric lava flows adjacent to the roadway. A resurvey of roadside flora in 2008 yielded a more than fourfold increase to 22 species, including nine native species not previously recorded. Eight new alien species have now invaded this alpine environment, although exclusively limited to a few individuals in ruderal habitat along the roadway. Alternative explanations for species invasion and altitudinal change over the past 50 years are evaluated: (1) changes related to continuing primary succession on ameliorating (weathering) young lava substrates; (2) local climate change; and (3) road improvements and increased vehicular access which promote enhanced car-borne dispersal of alien species derived from the expanding pool of potential colonizers naturalized on the island in recent decades. Unlike alpine environments in temperate latitudes, the energy component (warming) in climate change on Mauna Loa does not appear to be the unequivocal driver of plant invasion and range extension. Warming may be offset by other climate change factors including rainfall and evapotranspiration.     

The human footprint in the west: a large-scale analysis of anthropogenic impacts

Anthropogenic features such as urbanization, roads, and power lines, are increasing in western United States landscapes in response to rapidly growing human populations. However, their spatial effects have not been evaluated. Our goal was to model the human footprint across the western United States. We first delineated the actual area occupied by anthropogenic features, the physical effect area. Next, we developed the human footprint model based on the ecological effect area, the zone influenced by features beyond their physical presence, by combining seven input models: three models quantified top-down anthropogenic influences of synanthropic predators (avian predators, domestic dog and cat presence risk), and four models quantified bottom-up anthropogenic influences on habitat (invasion of exotic plants, human-caused fires, energy extraction, and anthropogenic wildland fragmentation). Using independent bird population data, we found bird abundance of four synanthropic species to correlate positively with human footprint intensity and negatively for three of the six species influenced by habitat fragmentation. We then evaluated the extent of the human footprint in relation to terrestrial (ecoregions) and aquatic systems (major rivers and lakes), regional management and conservation status, physical environment, and temporal changes in human actions. The physical effect area of anthropogenic features covered 13% of the western United States with agricultural land (9.8%) being most dominant. High-intensity human footprint areas (class 8-10) overlapped highly productive low-elevation private landholdings and covered 7% of the western United States compared to 48% for low-intensity areas (class 1-3), which were confined to low-productivity high-elevation federal landholdings. Areas within 1 km of rivers were more affected by the human footprint compared to lakes. Percentage human population growth was higher in low-intensity human footprint areas. The disproportional regional effects of the human footprint on landscapes in the western United States create a challenge to management of ecosystems and wildlife populations. Using footprint models, managers can plan land use actions, develop restoration scenarios, and identify areas of high conservation value at local landscapes within a regional context. Moreover, human footprint models serve as a tool to stratify landscapes for studies investigating floral and faunal response to human disturbance intensity gradients.