1t) Check for updates Received: 4 July 2019 Revised: 10 December 2019 Accepted: 18 December 2019 DOI: 10.1002/ece3.5985 ORIGINAL RESEARCH Ecology and Evolution WILEY Plant community assembly in suburban vacant lots depends on earthmoving legacy, habitat connectivity, and current mowing frequency Yoichi Tsuzuki1 | Tomoyo F. Koyanagi2 | Tadashi Miyashita1 School of Agriculture and Life Sciences, The University of Tokyo, Tokyo, Japan 2Field Studies Institute for Environmental Education, Tokyo Gakugei University, Tokyo, Japan Correspondence Yoichi Tsuzuki, School of Agriculture and Life Sciences, The University of Tokyo, Bunkyo-ku, Tokyo, Japan. Email: yoichi.tsuzuki.95@gmail.com Present address Yoichi Tsuzuki, Graduate School of Environmental Science, Hokkaido University, Sapporo, Japan Abstract In suburban regions, vacant lots potentially offer significant opportunities for biodiversity conservation. Recently, in Japan, due to an economic recession, some previously developed lands have become vacant. Little is known, however, about the legacy of earlier earthmoving, which involves topsoil removal and ground leveling before residential construction, on plant community composition in such vacant lots. To understand (dis)assembly processes in vacant lots, we studied 24 grasslands in a suburban region in Japan: 12 grasslands that had experienced earthmoving and 12 that had not. We surveyed plant community composition and species richness, and clarified compositional turnover (replacement of species) and nestedness (nonran-dom species loss) by distance-based fj-diversities, which were summarized by PCoA analysis. We used piecewise structural equation modeling to examine the effects of soil properties, mowing frequency, past and present habitat connectivities on compositional changes. As a result, past earthmoving, mowing frequency, soil properties, and past habitat connectivity were found to be the drivers of compositional turnover. In particular, we found legacy effects of earthmoving: earthmoving promoted turnover from native grassland species to weeds in arable lands or roadside by altering soil properties. Mowing frequency also promoted the same turnover, implying that extensive rather than intensive mowing can modify the negative legacy effects and maintain grassland species. Decrease in present habitat connectivity marginally enhanced nonrandom loss of native grassland species (nestedness). Present habitat connectivity had a positive effect on species richness, highlighting the important roles of contemporary dispersal. Our study demonstrates that community assembly is a result of multiple processes differing in spatial and temporal scales. We suggest that extensive mowing at local scale, as well as giving a high conservation priority to grasslands with high habitat connectivity at regional scale, is the promising actions to maintain endangered native grassland species in suburban landscapes with negative legacy effects of earthmoving. This is an open access article under the terms of the Creative Commons Attribution License, which permits use, distribution and reproduction in any medium, provided the original work is properly cited. © 2020 The Authors. Ecology and Evolution published by John Wiley & Sons Ltd. Ecology and Evolution. 2020;10:1311-1323. www.ecolevol.org | 1311 1312 ~Wl LEY-ecology and Evolution TSUZUKI ET AL. KEYWORDS beta diversity, community disassembly, habitat connectivity, land-use change, legacy effects, species nestedness, species turnover 1 | INTRODUCTION Habitat loss and degradation caused by human land use in suburban landscapes are a strong driver of biodiversity loss and ecosystem degradation (Deng, Wang, Hong, & Qi, 2009; Foley et al., 2005). Suburban regions, however, have recently drawn attention as areas where conservation activities should be promoted; not only for biodiversity conservation but also for supplying various ecosystem services, such as temperature regulation, air purification, and recreation (Gomez-Baggethun et al., 2013; Lepczyk et al., 2017). To determine the most effective strategies for biodiversity conservation in suburban landscapes, we need to understand the mechanisms of how human activities alter biological communities in space and time. This then enables managers to prioritize places for conservation and to understand the most effective management actions to achieve conservation objectives. It is important to note that past land use can be one of the crucial drivers that influence biological communities in suburban regions, that is, legacies of past land use play predominant roles in determining present community composition in human-disturbed landscapes (Foster et al., 2003; Hermy & Verheyen, 2007). For example, past agricultural activities and settlement have long-lasting effects on soil physical and chemical properties, and the altered soil affects present plant communities even after the land use ceased (Brudvig, Grman, Habeck, Orrock, & Ledvina, 2013; Dupouey, Dambrine, Laffite, & Moares, 2002; Freschet, Ostlund, Kichenin, & Wardle, 2014). Such legacy effects of past anthropogenic activities should be important processes determining present plant communities in suburban landscapes. Moreover, spatial processes also play a role, as biological communities in suburban landscapes are fragmented by artificial land cover (Liu, He, & Wu, 2016), which affects between-habitat dispersal maintaining species diversity (Ramalho, Laliberte, Poot, & Hobbs, 2014; Rudolph, Velbert, Schwenzfeier, Kleinebecker, & Klaus, 2017). Spatial dispersal could affect communities with time-delay in recently fragmented landscapes, which are known as extinction debt or colonization credit (Jackson & Sax, 2010; Kuussaari et al., 2009). For example, contemporary species richness is correlated with past landscape structures, rather than present, indicating the legacy effects of past dispersal (Helm, Hanski, & Partel, 2006; Lindborg & Eriksson, 2004). Examining multiple processes differing in their spatial (local to regional) and temporal (past to present) scales is thus necessary to understand community assembly mechanism in suburban regions. Suburban grassland plant communities in Japan are typically formed by complex spatial and temporal processes. Grasslands in Japan are being fragmented and destroyed due to both land development and abandonment of traditional management, such as mowing and burning (Shoji, Yamamoto, & Suyama, 1995; Yamato & Hattori, 2000) . This has led to severe decrease in grassland specialist plant species (Koyanagi & Furukawa, 2013; Yamato, Hattori, & Inagaki, 2001) . In suburban regions, earthmoving that involves topsoil removal and ground leveling for residential construction (Sasaki, Morimoto, & Imanishi, 2007; Tamura & Takeuchi, 1980) has caused large declines in grassland area. Currently, as Japan experiences economic recession and a population decline, places previously developed using earthmoving techniques are being abandoned resulting in vacant lots covered with herbaceous plants. These vacant lots offer the potential to boost the conservation of native grassland species that exist in remnant grasslands (Klaus, 2013). It is unknown, however, what legacy effects the earthmoving has on these vacant lots that may serve as potential habitats for grassland species. Added to this is the effect that mowing regimes have on grasslands in suburban landscapes; a management action that has diverse impacts on soil conditions, and consequently grassland biodiversity (Nagata & Ushimaru, 2016). Earlier studies that examined plant community assembly in human-disturbed landscapes evaluated both legacy effects and dispersal process (Johnson, Borowy, & Swan, 2018; Turley, Orrock, Ledvina, & Brudvig, 2017). However, the mechanisms of community assembly are not well clarified, because these studies used only alpha (or gamma) diversity as response variables. Focusing on the compositional differences, or beta diversity, between communities in different spatio-temporal contexts may enable us to infer the processes of community assembly in response to human land-use alterations. Beta diversity consists of two antithetic (but not exclusive) patterns: species turnover and nestedness (Baselga, 2010). Species turnover reflects the replacement of species from one site to another, which could be the result of environmental sorting, historical processes, or competition (Baselga, 2010; Hill, Heino, Thornhill, Ryves, & Wood, 2017). Nestedness implies that communities with fewer species are the subset of richer Time Past Present Regional Space Local FIGURE 1 Expected mechanisms of plant community assembly in this research communities. Nested assemblages reflect nonrandom species loss, which could be found along the gradient of habitat isolation or environmental harshness (Ulrich, Almeida-Neto, & Gotelli, 2009). Identifying the mechanisms that drive turnover and nested-ness would provide a comprehensive understanding of community assembly in human-dominated landscapes (Conradi, Temperton, & Kollmann, 2017; Hill etal., 2017). In this paper, we aimed to identify the mechanisms of community assembly in suburban grassland plant communities in Japan, by relating human activities, soil properties, and landscape structures to species richness, species turnover and nestedness (Figure 1). The specific hypotheses we tested were (a) past earthmoving makes soil oligotrophic by topsoil removal and has long-lasting legacy effects that promote compositional turnover from native grassland species to species typical for disturbed environments; (b) present mowing increases soil organic matter from plant cut residues (Poeplau, Marstorp, Thored, & Katterer, 2016) and accelerates nutrient cycling, which subsequently fertilizes soil and promotes species turnover in an opposite way to earthmoving; and (c) habitat connectivity promotes past and present immigration, thereby increasing present species richness and making nested structure (i.e., native grassland species decrease with decreasing habitat connectivity). 2 | MATERIALS AND METHODS 2.1 | Study sites The study region is located in the northern part of Shimousa Hill in Chiba Prefecture, 30-40 km of northeast of Tokyo metropolitan area, Japan (Figure 2a). Shimousa Hill is one of the largest flat hills in Japan and is covered with layers of volcanic ash on top (Natural History Museum & Institute, Chiba, 2001). Seminatural grasslands are sparsely distributed in this region and can be categorized largely into three types: Pleioblastus argenteostriatus and Miscanthus sin-ens/s-dominated grasslands which establish at extensively mowed (once a year or in several years) grasslands, and Imperata cylindrica-dominated grasslands that establish at occasionally mowed (twice a year) grasslands, and Zoysia japon/ca-dominated grasslands that establish at frequently mowed (more than three times a year) grasslands (Natural History Museum & Institute, Chiba, 2001). Grasslands in this region had historically been maintained as a pasture for warhorses, but since the middle of 19th century began to be changed to coppice woodlands dominated mainly by pine trees (Miyamoto & Yokohari, 2010). Due to frequent tree cutting, the coppice in these landscapes was generally sparse with short trees, allowing grassland-like vegetation to persist until the 1960s (Koyanagi, Kusumoto, Yamamoto, &Takeuchi, 2012b; Noda, Kondoh, & Nishihiro, 2019). After this, suburban development took place and earthmoving accompanied by topsoil removal and ground leveling was carried out in this region. Further, as humans became more urbanized, the activity of coppicing declined resulting in a closed canopy with a dark understory in many of the remaining grasslands. More recently, due to economic recession in Japan, some developed lands were underutilized or abandoned and converted to vacant lots dominated by herbaceous plants (Figure 2b). Vegetation in these vacant lots is likely to be influenced by the legacy effects of earth-moving due to building activities. Besides, some places became open grasslands without earthmoving as a result of constant management activities or land-use changes other than building construction (e.g., cultivation). Since the study region contains fragmented grasslands with different land-use histories as described above, this system was ideal for examining the multiple assembly processes including anthropogenic effects. We selected 24 grasslands based on the presence/absence of earthmoving (earthmoving: 12 grasslands, no earthmoving: 12 grasslands, Figure 2c and Table SI). 2.2 | Vegetation and mowing frequency Vegetation surveys were carried out in May, July, and September of 2017. In May, each grassland was divided into one to four sections based on the difference in dominant herbaceous species (see Table SI for the number of transects in each grassland). One 9-m transect was established in each section, and five 1 m x 1 m quadrats were placed along the transect at 1-m intervals. These transects and quadrats were fixed and were also examined in later surveys (July, September). In each survey, all species present in each quadrat were recorded. Presence/absence at a given quadrat was determined based on whether or not it was present at least once in three surveys. Occurrence of a given species per transect was then calculated as the number of quadrats in which that species was present. Mowing frequency was estimated for each transect by asking landowners and managers or, failing that, the signs of having been mown at the time of field surveys. 2.3 | Soil analysis Soil samples were collected in June 2017. Before sampling, soil hardness was measured at the center of the quadrats of the vegetation survey with a Yamanaka-type soil hardness tester (Fujiwara Scientific Co., Japan), and the mean hardness of 5 quadrats was calculated for each transect. Soil cores (5 cm diameter, 5 cm height) were sampled from the topsoil at the center of the quadrats, and the mixed soils were used for analysis. After air-drying for 5 days, samples were ground with a mortar and pestle, and sifted with a 2-mm sieve. The following 9 chemical and physical properties were measured, that is, pH, EC (electrical conductivity), CEC (cation exchange capacity), exchangeable potassium, available phosphorus, total C, total N, CN ratio, and particle size composition (for detailed methods see Table S2). Principal component analysis (PCA) was carried out to summarize particle size composition into 2 axes representing predominance of medium particles and particle size, respectively (Figure SI). Using these two principal components and the other eight soil properties, 1314 ~Wl LEY-ecology and Evolution TSUZUKI ETAL. 139°30.00 140=30.00' 141°0.00' 36°0.00' 35°30.00 FIG U R E 2 (a) The location of the study region (Shiroi, Inzai, and Kashiwa City in Chiba Prefecture, Japan); (b) a vacant lot that became dominated by herbaceous plants after earthmoving (left) and an old remnant grassland (right); (c) Enlarged view of the study region and the detailed location of 24 study sites. Filled sites have experienced earthmoving, while open sites have not „ , • Earthmoving 8 km O Without earthmoving an additional PCA was conducted to produce variables that represented integrated soil properties. Physical and chemical features of the resultant primary components were identified by factor loadings (Figure 3) The first four axes, which accounted for 77.8% of the total variance, were used for the subsequent analyses. 2.4 | Land-use survey Aerial photographs and satellite images of the study region taken in 20 different time points in the last 70 years were used for the reconstruction of land-use history (i.e., 1947, 1949, 1966, 1969, 1975, TSUZUKI ET AL. .Ecology and Evolution —Wl LEY' 1315 Hardness [kg/cm2] pH EC [mS/m] CEC [cmolc/kg] -Exchangeable potassium [mg/100 mg] ■ Available P [mg/100 g] Total C [%] Total N [%] CN ratio -Particle size PCI -Particle size PC2 PCI (39.6%) PC2 (17.6%) PC3 (11.9%) PC4 (8.6%) -1—i—i—i—i—i—i— —i—i—i—i—i—i—i— —i—i—i—i—i—i—i— —i—i—i—i—i—i—i ■0.6 -0.2 0.2 0.6 -0.6 -0.2 0.2 0.6 -0.6 -0.2 0.2 0.6 -0.6 -0.2 0.2 0.6 Factor loading FIGURE 3 Factor loadings of 4 primary components (PCI to PC4) of soil properties. 77.8% of the total variance was explained. Horizontal axis shows the value of factor loadings 1979, 1984, 1989, 1992, 1995, 1996, 1997, 1998, 2001, 2006, 2008 [Geospatial Information Authority of Japan (GSI), http://mapps.gsi. go.jp/maplibSearch.do#l], 2009, 2012, 2014, and 2017 [Google Earth]). According to the vegetation survey in 1968 (just before the town development), pine-dominated forests were occupied by grassland-like vegetation harboring grassland species. Therefore, all forests were regarded as grasslands until 1970, which is the period before region-wide earthmoving. Forests after 1970 were regarded as genuine forests because coppicing management was abandoned, resulting in dark understory with no grassland vegetation. We then identified the presence/absence of earthmoving, and the year when a focal study site became a grassland (from arable land, building, and forest). The occurrence of earthmoving was judged by the trace of topsoil removal or the presence of heavy equipment for earthmoving. The initial year (Table SI) was estimated as the mid-point of years before and after a given land-use change was identified by photographs. However, when ongoing earthmoving (such as partially modified land use with heavy equipment) was recognized in study sites that subsequently became grasslands after earthmoving, the year when the image was taken was regarded as the initial year. In old grasslands that had no history of land conversion during the past 70 years, the initial year was set to 1947, when the oldest aerial photograph was taken. new-town development and earthmoving began), (c) from 1985 to 2001 (land development progressed further), (d) from 2002 to 2017 (land-use change gradually decreased). Aerial photographs taken in 1966,1984, and 2001 (acquired from GSI website) and ESRI satellite image taken in 2017, covering the whole study region, were used. We defined initial and present landscapes for each grassland as those in the period including the initial year and period (d), respectively. We extracted grasslands that had experienced no earthmoving within a 500 m radius buffer from study sites. Habitat connectivity was then measured for each study site as the area proportion of the extracted grasslands to the buffer. The 500m buffer size was determined based on earlier studies that examined the distribution of grassland species or of species diversity in suburban landscapes (Duguay, Eigenbrod, & Fahrig, 2007; du Toit, Kotze, & Cilliers, 2016; Koyanagi, Akasaka, Oguma, & Ise, 2017; Vakhlamova, Rusterholz, Kanibolotskava, & Baur, 2014). All spatial analyses were conducted on QGIS 2.8.18 (QGIS Development Team, 2018). Aerial photographs for the first three periods were georeferenced, and the ESRI satellite image for the fourth period was acquired via QuickMapServices plugin. 2.6 I Species richness and ordination 2.5 | Habitat connectivity The area of the surveyed grasslands and connectivity to surrounding grasslands were measured for the following four periods (each approximately 18 years) in the past 70 years: (a) before 1966 (no major landscape change occurred), (b) from 1967 to 1984 (extensive Species richness was calculated per transect as a measure of alpha diversity. For all transect pairs, beta diversity was first calculated from Sorensen dissimilarity (psor) and then decomposed into species turnover (replacement of species) and nestedness (nonrandom species loss; Baselga, 2010), fisor ~ fisim fines (-1) 1316 ~Wl LEY-ecology and Evolution TSUZUKI ETAL. where f)sim is Simpson's dissimilarity index arising from species turnover, while f)nes represents nestedness. These p diversities were computed by an R package betapart (Baselga & Orme, 2012). To evaluate compositional changes underlying species turnover and nestedness, principal coordinate analysis (PCoA) was performed separately for/?sjm and f)nes. Based on the explained variance of each PCoA axis, 3 axes from f)sim and one axis from f)nes were used for the following analysis, as they had much higher explanatory power in comparison to the rest of the axes (Figure 4). To identify characteristic species for ordination axes, Pearson's correlation coefficients between PCoA axes and species occurrence of all 247 species recorded were calculated. Statistical significance of the correlation coefficients was tested by a randomization test with 9,999 replications, and the significance threshold of 0.05 was adjusted with the sequential Bonferroni method. For species having a significant correlation with any of the four axes, species characteristics (height, longevity, origin, and grassland species or not) were examined based on earlier studies (Kaneko, Mimura, Amano, & Hasegawa, 2009; Koyanagi & Furukawa, 2013; Miyawaki, 1986; Natural History Museum & Institute, Chiba, 2003) to understand plant compositional shifts along each ordination axis. Correlations among the four ordination axes and species richness were also tested using sequential Bonferroni method. 2.7 | Statistical analysis We used piecewise structural equation model (piecewise SEM) to estimate causal effects in a priori hypotheses (Figure 1). As with traditional SEM, piecewise SEM can quantify causal networks but it differs in its estimation procedures: the whole causal network is decomposed into a series of regression models, each of which is evaluated separately with a generalized linear model (Lefcheck, 2016; Shipley, 2009). Thus, piecewise SEM can operate with limited sample sizes and incorporate various model features, such as random effects and hierarchical structure. The regression model we used here is a hierarchical linear model (Raudenbush & Bryk,), because our study has two data hierarchies: transect-level (lower level) and site-level (upper level). The model for transect / in site j is as follows: Yij = b0j+b1W1 + b2W2 + - b0j = c0 + qXj + c2X2 + — +Uj (2) (3) The transect-level data were used for Equation (2), and the site-level data were used for Equation (3). Y~ is a transect-level response variable, while Wand Xare, respectively, the transect-level and site-level explanatory variables. boj is the intercept for study site j and is modeled with site-level variables, e- is the error term, and u. is a random effect of study site. We established five models, each of which used one of the four ordination axes of p diversities or species richness as a response variable. The explanatory variables in Equation (2) (W) were four soil PCs and mowing frequency, and those in Equation (3) (X) were initial and present connectivity and earthmoving. We also evaluated causal effects from mowing frequency or earthmoving to soil properties (four soil PCs), using mowing frequency as W in Equation (2) and earthmoving as X in Equation (3). Analyses were conducted in R 3.5.2 (R Development Core Team, 2018). Function "Ime" in package "nlme" was used for each hierarchical linear model, and function "psem" in package "piecewiseSEM" was used for specifying the whole causal network (Lefcheck, 2016). All response and explanatory variables were standardized. Our analyses paid attention to the following statistical problems, (a) correlations among unlinked factors and (b) spatial autocorrelation among study sites. In piecewise SEM, the goodness-of-fit of the whole causal network is evaluated by directed separation, which tests (conditional) independence for the basis set, that is, pairs of variables that are not linked directly in Figure 1 (e.g., earthmoving-mowing pair), using Fisher's C (Lefcheck, 2016; Shipley, 2009). It should be noted that some pairs in the basis set are (conditionally) interrelated because of plausible causalities that are of no interest. One such relationship Turnover PCoA Nestedness PCoA 0.06 iS 0.04 Q. X 0) .5 0.02 - 0.00 Axis Axis FIGURE 4 Explained variance of PCoA axes. In turnover PCoA, axis 4 or later had low explanatory power compared to the first three axes (axis 1:6.2%; axis 2:5.5%; axis 3:4.9%). In nested PCoA, only the first axis had prominent explanatory power (7.4%) is a temporal correlation between initial and present habitat connectivity (correlation coefficient = 0.57, p = .004). Moreover, as earthmoving was carried out in a spatially continuous manner in the study region, negative correlations between earthmoving and habitat connectivity were observed (earthmoving and initial connectivity: -0.66, p < .001; earthmoving and present connectivity: -0.40, p = .053). As these associations could severely decrease the goodness-of-f it of the model due to collinearity, they were excluded from the basis set and treated as correlated errors. To account for spatial autocorrelation, we first defined neighboring relationships using Delaunay Triangulation weighted by distance and then conducted Moran's I test (a = .05) for the site-level value of each variable. As a result, turnover axis 3, soil PCI, earthmoving, and present habitat connectivity had significant spatial autocorrelations (Table S3). When assessing the causal effects among these variables, we incorporated 6 additional variables that are significant in MEM (Moran's eigenvector maps; Dray, 2018) as covariates. grassland species with low height (negatively correlated) to tall herbaceous species and vines characteristic to roadside or abandoned crop fields (positively correlated). Turnover axis 2 represents a gradient from native grassland species (negatively correlated) to weeds in arable lands or roadside (positively correlated). Species correlated with turnover axis 3, either positively or negatively, were typical for disturbed environments (e.g., roadside and vacant lots), indicating that turnover axis 3 represents species replacement among these species. Nestedness axis 1 correlated negatively with native grassland species, representing gradual loss of grassland species with increasing value of nestedness axis 1. This gradual loss might underlie decrease in species richness, since nestedness axis 1 was significantly correlated with species richness (Figure 5). It should be noted that species identities of native grassland species were different between axes, although they partly overlapped (Figure 6, Table S4), indicating that different subsets of grassland species are represented in different ordination axes. 3 | RESULTS 3.1 | Community compositions represented by PCoA axes Four PCoA axes of beta diversity were independent each other (Figure 5) and reflected different aspects of community composition (Figure 6, Table S4). Turnover axis 1 represents a gradient from native v- rv >< .2? -2? -2? 10 d) a; a) -£ s s s 5 o o o £ p p p co % T % .05 in directed separation, indicating sufficient goodness-of-fit. 4 | DISCUSSION We have shown that four ordination axes were subjected to different explanatory variables. This could be attributed to interspecific variations in crucial factors for presence/absence, as the four ordination axes represent different compositional changes. We will discuss assembly mechanisms underlying these compositional shifts in detail below. 4.1 | Legacy effect of earthmoving and mowing frequency Our results indicate that past earthmoving altered soil properties, and that the altered soil triggered turnover from native grassland species to weeds inhabiting arable lands or roadsides (Figure 7b), supporting our first hypothesis. In contrast to our second hypothesis, this turnover was not mediated by mowing frequency; mowing frequency also induced the same direction of species turnover, decreasing native grassland species (Figure 7b). Past land use is known to cause long-lasting changes in soil properties, which in turn affects plant communities (Brudvig et al., 2013; Dupouey et al., 2002; Freschet et al., 2014; Isbell, Tilman, Polasky, Binder, & Hawthorne, 2013; Mattingly & Orrock, 2013). TSUZUKI ET AL. (a) ctí Past Present Habitat connectivity ------r^sin— turnover axis 1 X Earthmoving —-0. 1 N 1 1 soil PC2 soil PC3 -0.6J0** hr* soil PCI soil PC4 i i i i 1 mowing frequency - J I .Ecology and Evolution Past Wiley- Present 1319 (C) Past Present (d) Past Present o o 'on Habitat connectivity Habitat connectivity z turnover axis 3 /I 0.20^1-0.20* "HE -^>.46 I— Nestedness axis 1 o -J soil PC2 soil PC3 Earthmoving H -0.60" 4*-i soil PCI soil PC4 mowing frequency (e) Past Present a o 'co o ctí Habitat connectivity Habitat connectivity 0.38*---------- Species richness soil PC2 soil PC3 CO o Earthmoving H-0.60" yW soil PCI 1 soil PC4 Mowing frequency FIGURE 7 Results of piecewise structural equation model: (a) turnover axis 1, (b) turnover axis 2, (c) turnover axis 3, (d) nestedness axis 1, and (e) species richness. Only significant (**p < .01; *p < .05) paths are shown for convenient visualization, except marginally significant (p < .1) paths in (d) nestedness axis 1. Red and blue arrows indicate positive and negative effects, respectively. Factors without significant paths coming in or out of are shown in semitransparent. Fisher's C of all the 5 diagrams satisfied p > .05, indicating enough goodness-of-fit However, few researches have investigated the legacy effects of earthmoving, despite this practice being conducted at an increasing rate worldwide as a result of global human population growth (Hooke, 2000). We have shown that past earthmoving increased pH, decreased CEC, total C, total N, and medium particles, and that native grassland species are negatively affected by the edaphic changes induced by earthmoving. Increase in pH and decrease in CEC, total C, and total N caused by earthmoving can be attributed to topsoil removal, since acidic soil organic matters like humus originate mainly from topsoil. The predominance of medium particles might be due to the loss of large and small particles, resulting from breakup of large particles caused by earthmoving and the removal of small particles such as clay. It appears that environmental filtering plays a role in subsequent processes: the altered soil conditions are unsuitable for native grassland species, thus reducing their occurrence. Soil in the study region is mostly acidic, as a result of the weathering of volcanic ash. The soil is also rich in organic matter, but plant-available phosphate is poor which is caused by high phosphate absorption coefficient (Hiradate, Morita, & Kusumoto, 2008; Shoji, Hayashi, Kohyama, & Sasaki, 2010). While native grassland species are very common in such soil environments, they occur less in high pH soil environments disturbed by land development or fertilization, where alien species dominate instead (Hiradate et al., 2008). This finding agrees with our result showing indirect effects of earthmoving on soil and vegetation. Our finding that mowing frequency had a negative effect on native grassland species might seem inconsistent with earlier studies showing that mowing maintains grassland environment and contributes to the establishment of grassland species in general (Brys, Jacquemyn, Endels, de Blust, & Hermy, 2004; Cousins & Eriksson, 2002; Ehrlen, Syrjanen, Leimu, Garcia, & Lehtila, 2005; MacDougall & Turkington, 2007; Valko, Torok, Matus, & Tothmeresz, 2012). However, frequent mowing observed in our study sites resulted in very low plant height, indicating intensive rather than moderate mowing intensity was implemented in these grasslands. In fact, some of the grasslands in our study region received high frequency, excessive mowing (more than four times a year), which inhibited the establishment of grassland species (Kaneko, Tanikawa, & Hasegawa, 2012). Thus, a wide range of mowing gradient, including intensive mowing, may explain the observed negative impacts of mowing on grassland species occurrence. Earthmoving and mowing frequency affected differently the compositional turnover among species typical in disturbed environments (Figure 7c). The species turnover was also correlated with available P, EC, and exchangeable K, all of which can be interpreted as soil nutrient components. These indicate that species positively correlated with turnover 3 tend to occur in oligotrophic environment while those correlated negatively in fertile condition. Therefore, this compositional turnover may reflect species sorting by nutritional gradients arising from interspecific variation in the tolerance to oligotrophic environment. In Europe, species habitat requirements are quantified by Ellenberg indicator values (Diekmann, 2003), but there are no counterpart proxies in Japan, making it difficult to confirm the possible effects of the nutritional gradient. Evaluation of species environmental requirements is needed to fully understand the mechanisms of compositional changes. 4.2 | Landscape structure and its consequences on species composition Habitat connectivity had significant effects on both species richness and turnover (Figure 7a,e), as well as marginally significant effect on nestedness (Figure 7d), in a way that boosts species richness or the occurrence of native grassland species. Therefore, our third hypothesis that habitat connectivity increases species richness and native grassland species was supported, implying dispersal limitation on species richness and the occurrence of grassland species in fragmented grasslands. Species richness and nestedness (although marginally) were affected by present connectivity, but not by past connectivity (Figure 7d,e), indicating that current immigration from surrounding habitats maintains high species richness and grassland specialist plants. In contrast to this result, time-delayed responses to landscape change (Jackson & Sax, 2010) have been reported for species richness (Bagaria, Helm, Roda, & Pino, 2015; Helm et al., 2006; Koyanagi, Kusumoto, Yamamoto, Okubo, et al., 2012a; Lindborg & Eriksson, 2004; Otsu, lijima, Nagaike, Takuo, & Hoshino, 2017) and nested components (Koyanagi, Furukawa, & Osawa, 2018) of grassland plant communities. Cousins (2009) found that time-delayed response is detected in regions where contemporary landscapes retain >10% of traditional habitats. As our study region maintains only 2.8% of remnant grasslands of those in 1880s (Noda et al., 2019), delayed responses may not have been observed. There might be time-delayed response, however, in the turnover pattern since initial, rather than present, habitat connectivity had a significant effect (Figure 7a). This result highlights the importance to evaluate p diversity when considering community dynamics at landscape scales, because evaluation of species richness (or alpha diversity) alone did not reveal the impact of the past landscape structure. The significant effect of initial connectivity indicates that grassland species had immigrated more to grasslands with higher initial connectivity and persisted thereafter, resulting in high occurrence in the present community (Jackson & Sax, 2010). In contrast, grasslands with low connectivity initially might have suffered from dispersal limitation in early successional stage, and instead, species associated with roadside or abandoned crop fields immigrated from the surrounding human-dominated landscape. 4.3 | Suggestions for the conservation of grassland vegetation We have successfully extracted four ordination axes of compositional turnover and nestedness, which were shaped by different assembly processes. Hence, the present community is a complex composite of multiple compositional shifts. Our study is notable for estimating the mechanisms of each assembly pattern with reference to various processes, including legacy effects of earthmoving, spatial dispersal, and time-delayed response to landscape changes. These findings provide implications for the conservation of grassland vegetation. Firstly, the results we show on the legacy effects of earthmoving and mowing frequency would be helpful for local management. Earthmoving had a negative legacy effect on grassland species. Considering that mowing frequency had a significant negative effect on the same species, improving mowing regimes in ways such as lowering frequency and intensity could possibly buffer against the worst of the legacy effects of earthmoving. In the study region, the time elapsed since the practice of mowing started plays an important role in the survival of endangered grassland plants (Kaneko, Akeboshi, Hasegawa, & Miyashita, 2013). Quantifying the causal effects of time, therefore, would be needed to suggest more effective management strategies. Secondly, the effect of habitat connectivity revealed by our study is helpful for prioritizing grassland habitats for conservation at a regional scale. We found that initial and present habitat connectivity is, in some way, a determinant of grassland specialist occurrence. Therefore, in addition to the grasslands where many endangered species currently persist, it is desirable to prioritize places which are surrounded by grasslands that do not have a history of earthmoving. This would make the best use of immigration from surrounding grasslands and support grassland specialist occurrence. As we have demonstrated, communities are made up of multiple compositional subsets which are shaped by different assembly processes. If we had focused only on species richness, we would have missed important anthropogenic impacts including legacy effects and would not have suggested conservation implications outlined above. Therefore, our approach of decomposing community composition into multiple assembly patterns (i.e., turnover and nestedness) and evaluating anthropogenic impacts on each of them is necessary for the study of biodiversity conservation. ACKNOWLEDGMENTS We are grateful to J. Nishihiro and A. Noda for providing data on historical vegetation and landscape change in the study region. We thank M. Hasegawa for arranging the lodging facility for comfortable field surveys. We thank K. Tange, T. Kagaya, and T. Oda for providing laboratory facilities that are necessary for soil analyses. We appreciate diverse advice and assistance from K. Nakajima. We thank M. J. Evans for helpful comments and suggestions on a draft manuscript. CONFLICT OF INTEREST None declared. AUTHOR CONTRIBUTIONS Y. Tsuzuki, T. F. Koyanagi, and T. Miyashita conceived the ideas and designed the methodology; Y. Tsuzuki collected data and performed the statistical analyses; Y. Tsuzuki, T. F. Koyanagi, and T. Miyashita discussed the results; Y. Tsuzuki led the writing of the manuscript. All authors contributed critically to the drafts and gave final approval for publication. DATA AVAILABILITY STATEMENT Data on species occurrence, soil properties, past and present habitat connectivity, land-use changes, and mowing frequency are all available from the Dryad Digital Repository (https://doi.org/10.5061/ dryad.khl893226). ORCID Yoichi Tsuzuki® https://orcid.org/0000-0002-9109-0528 REFERENCES Bagaria, G., Helm, A., Roda, F., & Pino, J. (2015). Assessing coexisting plant extinction debt and colonization credit in a grassland-forest change gradient. Oecologia, 179(3), 823-834. https://doi.org/10.1007/ S00442-015-3377-4 Baselga, A. (2010). Partitioning the turnover and nestedness components of beta diversity. Global Ecology and Biogeography, 19(1), 134-143. https://doi.Org/10.llll/j.1466-8238.2009.00490.x Baselga, A., & Orme, C. D. L. (2012). betapart: An R package for the study of beta diversity. Methods in Ecology and Evolution, 3(5), 808-812. https://doi.Org/10.llll/j.2041-210X.2012.00224.x Brudvig, L. A., Grman, E., Habeck, C. W., Orrock, J. L., & Ledvina, J. A. (2013). Strong legacy of agricultural land use on soils and un-derstory plant communities in longleaf pine woodlands. Forest Ecology and Management, 310, 944-955. https://doi.Org/10.1016/j. foreco.2013.09.053 Brys, R., Jacquemyn, H., Endels, P., de Blust, G., & Harmy, M. (2004). The effects of grassland managementon plant performance and demography in the perennnial herb Primula veris.JournalofAppHedEcology,41(6), 1080-1091. https://doi.Org/10.llll/j.0021-8901.2004.00981.x Conradi, T., Temperton, V. M., & Kollmann, J. (2017). Beta diversity of plant species in human-transformed landscapes: Control of community assembly by regional productivity and historical connectivity. Perspectives in Plant Ecology Evolution and Systematics, 24,1-10. https ://doi.org/10.1016/j.ppees.2016.10.001 Cousins, S. A. O. (2009). Extinction debt in fragmented grasslands: Paid or not? Journal of Vegetation Science, 20(1), 3-7. https://doi. org/10.1111/j.l654-1103.2009.05647.x Cousins, S. A. O., & Eriksson, O. (2002). The influence of management history and habitat on plant species richness in a rural hemiboreal landscape. Sweden. Landscape Ecology 17(6), 517-529. https://doi. org/10.1023/A:1021400513256 Deng, J. S., Wang, K., Hong, Y., & Qi, J. G. (2009). Spatio-temporal dynamics and evolution of land use change and landscape pattern in response to rapid urbanization. Landscape and Urban Planning, 92(3-4), 187-198. https://doi.Org/10.1016/j.landurbplan.2009.05.001 Diekmann, M. (2003). Species indicator values as an important tool in applied plant ecology—A review. Basic and Applied Ecology 4, 493-506. https://doi.org/10.1078/1439-1791-00185 Dray, S. (2018). adespatial: Moran's Eigenvector Maps and related methods for the spatial multiscale analysis of ecological communities. Retrieved from https://cran.r-project.org/web/packages/adespatial/vignettes/ tutorial.html du Toit, M. J., Kotze, D. J., & Cilliers, S. S. (2016). Landscape history, time lags and drivers of change: Urban natural grassland remnants in Potchefstroom, South Africa. Landscape Ecology 31(9), 2133-2150. https://doi.org/10.1007/sl0980-016-0386-6 Duguay, S., Eigenbrod, F., & Fahrig, L. (2007). Effects of surrounding urbanization on non-native flora in small forest patches. Landscape Ecology 22(4), 589-599. https://doi.org/10.1007/ sl0980-006-9050-x Dupouey, J. L, Dambrine, E., Laffite, J. D., & Moares, C. (2002). Irreversible impact of past land use on forest soils and biodiversity. Ecology 83(11), 2978-2984. https://doi.org/10.1890/0012-9658(2002)083[2978:IIOPLU]2.0.CO;2 Ehrlen, J., Syrjanen, K., Leimu, R., Garcia, M. B., & Lehtila, K. (2005). Land use and population growth of Primula veris: An experimental demographic approach. Journal of Applied Ecology, 42(2), 317-326. https:// doi.org/10.1111/j.l365-2664.2005.01015.x Foley, J. A., DeFries, R., Asner, G. P., Barford, C, Bonan, G., Carpenter, S. R. et al (2005). Global consequences of land use. Science, 309(5734), 570-574. https://doi.org/10.1126/science.1111772 Foster, D., Swanson, F., Aber, J., Burke, I., Brokaw, N., Tilman, D., & Knapp, A. (2003). The importance of land-use legacies to ecology and conservation. Bioscience, 53(1), 77-88. https://doi. org/10.1641/0006-3568(2003)053[0077:TIOLUL]2.0.CO;2 Freschet, G. T., Ostlund, L., Kichenin, E., & Wardle, D. A. (2014). Aboveground and belowground legacies of native Sami land use on boreal forest in northern Sweden 100 years after abandonment. Ecology, 95(4), 963-977. https://doi.Org/10.1890/13-0824.l Gomez-Baggethun, E., Gren, A., Barton, D. N., Langemeyer, J., McPhearson, T., O'Farrell, P., Anderson, E..... Kremer, P. (2013). Urban ecosystem services. InT. Elmqvist, M. Fragkias, J. Goodness, B. Guneralp, P. J. Marcotullio, R. I. McDonald, ... C. Wilkinson (Eds.), Urbanization, biodiversity and ecosystem services: Challenges and opportunities (pp. 175-251). Dordrecht, Netherlands: Springer. Helm, A., Hanski, I., & Partel, M. (2006). Slow response of plant species richness to habitat loss and fragmentation. Ecology Letters, 9(1), 72-77. https://doi.Org/10.llll/j.1461-0248.2005.00841.x Hermy, M., &Verheyen, K. (2007). Legacies of the past in the present-day forest biodiversity: A review of past land-use effects on forest plant species composition and diversity. Ecological Research, 22(3), 361-371. https://doi.org/10.1007/sll284-007-0354-3 Hill, M. J., Heino, J., Thornhill, I., Ryves, D. B., & Wood, P. J. (2017). Effects of dispersal mode on the environmental and spatial correlates of nestedness and species turnover in pond communities. Oikos, 126(11), 1575-1585. https://doi.org/10.llll/oik.04266 Hiradate, S., Morita, S., & Kusumoto, Y. (2008). Effects of soil chemical properties on the habitats of alien and endemic plants. Nougyougijutsu, 63(10), 469-474. Hooke, R. L. (2000). On the history of humans as geomorphic agents. Geology, 28(9), 843-846. https://doi.org/10.1130/0091-7613(2000)28<843:OTHOHA>2.0.CO;2 Isbell, F., Tilman, D., Polasky, S., Binder, S., & Hawthorne, P. (2013). Low biodiversity state persists two decades after cessation of nutrient enrichment. Ecology Letters, 16(4), 454-460. https://doi.org/10.llll/ ele.12066 Jackson, S. T., & Sax, D. F. (2010). Balancing biodiversity in a changing environment: Extinction debt, immigration credit and species turnover. Trends in Ecology & Evolution, 25(3), 153-160. https://doi. org/10.1016/j.tree.2009.10.001 Johnson, A. L., Borowy, D., & Swan, C. M. (2018). Land use history and seed dispersal drive divergent plant community assembly patterns in urban vacant lots. Journal of Applied Ecology, 55(1), 451-460. https:// doi.org/10.1111/1365-2664.12958 Kaneko, K., Akeboshi, A., Hasegawa, M., & Miyashita, T. (2013). The effects of growth of grassland plants which flower in the spring compared to the difference of the long-term mowing management of semi-natural grasslands in the Hokuso region of Chiba Prefecture in Japan. Landscape Ecology and Management, 18(2), 189-199. https:// doi.org/10.5738/jale.18.189 Kaneko, K., Mimura, K., Amano, M., & Hasegawa, M. (2009). Flora of grassland with different of management practices in Shiroi-city, Chiba Prefecture. Landscape Ecology and Management, 14(2), 163-176. https://doi.org/10.5738/jale.14.163 Kaneko, K., Tanikawa, M., & Hasegawa, M. (2012). Difference of vegetation by mowing frequency in semi-natural grasslands in the Yata district of Shiroi-city, Chiba Prefecture. Landscape Ecology and Management, 16(2), 71-77. https://doi.org/10.5738/jale.16.71 Klaus, V. H. (2013). Urban grassland restoration: A neglected opportunity for biodiversity conservation. Restoration Ecology 21(6), 665-669. https://doi.org/10.llll/rec.12051 Koyanagi, T. F., Akasaka, M., Oguma, H., & Ise, H. (2017). Evaluating the local habitat history deepens the understanding of the extinction debt for endangered plant species in semi-natural grasslands. Plant Ecology, 218(6), 725-735. https://doi.org/10.1007/ sll258-017-0724-z Koyanagi, T. F., & Furukawa, T. (2013). Nation-wide agrarian depopulation threatens semi-natural grassland species in Japan: Sub-national application of the Red List Index. Biological Conservation, 167(1), 1-8. https://doi.Org/10.1016/j.biocon.2013.07.012 Koyanagi, T. F., Furukawa, T., & Osawa, T. (2018). Nestedness-resultant community disassembly process of extinction debt in a highly fragmented semi-natural grassland. Plant Ecology, 219(9), 1093-1103. https://doi.org/10.1007/sll258-018-0861-z Koyanagi, T., Kusumoto, Y, Yamamoto, S., Okubo, S., Iwasaki, N., & Takeuchi, K. (2012a). Grassland plant functional groups exhibit distinct time-lags in response to historical landscape change. Plant Ecology, 213(2), 327-338. https://doi.org/10.1007/sll258-011-9979-y Koyanagi, T., Kusumoto, Y, Yamamoto, S., & Takeuchi, K. (2012b). Potential roles of small and linear habitat fragments in satoyama landscapes for conservation of grassland plant species. Urban Ecosystems, 15(4), 893-909. https://doi.org/10.1007/sll252-012-0253-4 Kuussaari, M., Bommarco, R., Heikkinen, R. K., Helm, A., Krauss, J., Lindborg, R.....Steffan-Dewenter, I. (2009). Extinction debt: A challenge for biodiversity conservation. Trends in Ecology & Evolution, 24(10), 564-571. https://doi.Org/10.1016/j.tree.2009.04.011 Lefcheck, J. S. (2016). piecewiseSEM: Piecewise structural equation modelling in R for ecology, evolution, and systematics. Methods in Ecology and Evolution, 7(5), 573-579. https://doi. org/10.1111/2041-210X.12512 Lepczyk, C. A., Aronson, M. F., Evans, K. L., Goddard, M. A., Lerman, S. B., & Maclovor, J. S. (2017). Biodiversity in the city: Fundamental questions for understanding the ecology of urban green spaces for biodiversity conservation. Bioscience, 67(9), 799-807. https://doi. org/10.1093/biosci/bix079 Lindborg, R., & Eriksson, O. (2004). Historical landscape connectivity affects present plant species diversity. Ecology, 85(7), 1840-1845. https://doi.org/10.1890/04-0367 Liu, Z., He, C, & Wu, J. (2016). The relationship between habitat loss and fragmentation during urbanization: An empirical evaluation from 16 world cities. PLoS ONE, 11(4), e0154613. https://doi.org/10.1371/ journal.pone.0154613 MacDougall, A. S., & Turkington, R. (2007). Does the type of disturbance matter when restoring disturbance-dependent grasslands? Restoration Ecology, 15(2), 263-272. https://doi. org/10.1111/j.l526-100X.2007.00209.x Mattingly, W. B., & Orrock, J. L. (2013). Historic land use influences contemporary establishment of invasive plant species. Oecologia, 172(4), 1147-1157. https://doi.org/10.1007/s00442-012-2568-5 Miyamoto, M., & Yokohari, M. (2010). Relationships between land grant processes of government-ruled pasturelands and transformation processes of land use after the modernization in Shimousa Plateau, Japan. Journal of the Japanese Institute of Landscape Architecture, 73(5), 631-63 6. https://doi.org/10.5632/jila.73.631 Miyawaki, A., & Okuda, S. (1986). Vegetation of Japan Kanto. Tokyo, Japan: Shibundo. Nagata, Y. K., & Ushimaru, A. (2016). Traditional burning and mowing practices support high grassland plant diversity by providing intermediate levels of vegetation height and soil pH. Applied Vegetation Science, 19(4), 567-577. https://doi.org/10.llll/avsc.12252 Natural History Museum and Institute, Chiba. (2001). Natural History of Chiba Prefecture 5 - Plants in Chiba Prefecture 2. Chiba: Chiba Prefecture. Natural History Museum and Institute, Chiba. (2003). Vegetation of Chiba. Chiba, Japan: Chiba Prefecture. Noda, A., Kondoh, A., & Nishihiro, J. (2019). Changes in land cover and grassland area over the past 120 years in a rapidly urbanised area in Japan. One Ecosystem, 4, e37669. https://doi.org/10.3897/ oneeco.4.e37669 Otsu, C, lijima, H., Nagaike, T., & Hoshino, Y. (2017). Evidence of extinction debt through the survival and colonization of each species in semi-natural grasslands. Journal of Vegetation Science, 28(3), 464-474. https://doi.org/10.llll/jvs.12514 Powplau, C, Marstorp, H., Thored, K., & Katterer, T. (2016). Effect of grassland cutting frequency on soil carbon storage—A case study on public lawns in three Swedish cities. So/7, 2, 175-184. https://doi. org/10.5194/soil-2-175-2016 QGIS Development Team. (2018). QGIS Geographic Information System. Open Source Geospatial Foundation Project. Retrieved from http:// qgis.osgeo.org R Development Core Team. (2018). R: A language and environment for statistical computing. Vienna, Austria: R Foundation for Statistical Computing. Retrieved from http://www.R-project.org Ramalho, C. E., Laliberte, E., Poot, P., & Hobbs, R. J. (2014). Complex effects of fragmentation on remnant woodland plant communities of a rapidly urbanizing biodiversity hotspot. Ecology, 95(9), 2466-2478. https://doi.Org/10.1890/13-1239.l Raudenbush, S. W., & Bryk, A. S.. (2002). Hierarchical linear models: Applications and data analysis methods. (Advanced quantitative techniques in the social sciences.) Newbury Park, CA: Sage. Rudolph, M., Velbert, F., Schwenzfeier, S., Kleinebecker, T., & Klaus, V. H. (2017). Patterns and potentials of plant species richness in high- and low-maintenance urban grasslands. Applied Vegetation Science, 20, 18-27. https://doi.org/10.llll/avsc.12267 Sasaki, T., Morimoto, Y., & Imanishi, J. (2007). The stand structure and soil properties of the forested area in a large scale reclamation site for 30 years after construction. Journal of the Japanese Institute of Landscape Architecture, 70(5), 413-418. https://doi.org/10.5632/ jila.70.413 Shipley, B. (2009). Confirmatory path analysis in a generalized multilevel context. Ecology, 90(2), 363-368. https://doi.org/ 10.1890/08-1034.1 Shoji, A., Hayashi, H., Kohyama, K., & Sasaki, H. (2010). Effects of horse grazing on plant species richness and abundance of Iris setosa in a boreal semi-natural grassland, Japan. Grassland Science, 57(1), 1-8. https://doi.Org/10.llll/j.1744-697X.2010.00201.x Shoji, A., Yamamoto, Y., & Suyama, T. (1995). Analysis of landscape changes with geographic information system, a case study of Mt. Sanbe region, Shimane Pref.[Japan]. Journal of the Japanese Society of Irrigation, Drainage and Reclamation Engineering, 63(8), 847-853. https://doi.org/10.11408/jjsidrel965.63.8_847 Tamura, T., & Takeuchi, K. (1980). Land characteristics of the hills and their modification by man: With special reference to a few cases in the Tama Hills, west of Tokyo. Geographical Report of Tokyo Metropolitan University, 14(15), 49-94. Turley, N. E., Orrock, J. L., Ledvina, J. A., & Brudvig, L. A. (2017). Dispersal and establish limitation slows plant community recovery in post-agricultural longleaf pine savannas. Journal of Applied Ecology, 54(4), 1100-1109. https://doi.org/10.llll/1365-2664.12903 Ulrich, W., Almeida-Neto, M., & Gotelli, N. J. (2009). A consumer's guide to nestedness analysis. Oikos, 118, 3-17. https://doi. org/10.1111/j.l600-0706.2008.17053.x Vakhlamova, T., Rusterholz, H. P., Kanibolotskaya, Y., & Baur, B. (2014). Changes in plant diversity along an urban-rural gradient in an expanding city in Kazakhstan, Western Siberia. Landscape and Urban Planning, 132, 111-120. https://doi.Org/10.1016/j.landu rbplan.2014.08.014 Valko, O., Torok, P., Matus, G., & Tothmeresz, B. (2012). Is regular mowing the most appropriate and cost-effective management maintaining diversity and biomass of target forbs in mountain hay meadows? Flora-Morphology Distribution, Functional Ecology of Plants, 207(4), 303-309. https://doi.Org/10.1016/j.flora.2012.02.003 Yamato, M., & Hattori, T. (2000). A study of the actual vegetational conditions of the semi-natural grassland in Mt. Higashiotafukuyama [Hyogo, Japan] and its management. Journal of the Japanese Institute of Landscape Architecture, 63(5), 473-476. https://doi.org/10.5632/ jila.63.473 Yamato, M., Hattori, T., & Inagaki, N.(2001). Effect of area reduction and difference of management on species richness of semi-natural grasslands in the southern Osaka plain. Journal of the Japanese Institute of Landscape Architecture, 64(5), 561-564. https://doi.org/10.5632/ jila.64.561 SUPPORTING INFORMATION Additional supporting information may be found online in the Supporting Information section. How to cite this article: Tsuzuki Y, Koyanagi TF, Miyashita T. Plant community assembly in suburban vacant lots depends on earthmoving legacy, habitat connectivity, and current mowing frequency. Ecol Evol. 2020;10:1311-1323. https://doi.org/10.1002/ece3.5985