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Changes in vegetation and flora of abandoned paddy terraces in responses to drawdown


In order to assess the impacts of drawdown for land-use change on a Sphagnum-marsh, we compared the vegetation and flora of the wetland before and after the drawdown with focusing on the population of Sphagnum palustre L. Remarkable changes in the coverage of S. palustre and the major vegetational components of the wetland were observed. The coverage of S. palustre markedly decreased by about 75% (from approx. 247 m2 in 2011 to approx. 62 m2 in 2015) after the drawdown. Tree species such as Salix spp. extended (from about 70% to about 83% in the total coverage of the wetland), whereas herbaceous species shrunk after the drawdown. Upland-inhabiting species such as obligate plants for uplands (OBU) increased, whereas wetland-inhabiting species such as facultative plants for wetlands (FACW) and OBW decreased in terms of vegetational coverage. The total number of plant species decreased from 70 species to 62 species after the drawdown, including the disappearance of some wetland-inhabiting species from the wetland. We suggest that the attention for further studies on the abandoned paddy terraces (APTs) and effort for the management and conservation of APTs and APT-inhabiting species that are vulnerable to human-induced disturbances have to be paid more.


Wetland plants usually show highly adaptive characteristics under inundated environments such as adventitious root, aerenchyma tissue, dimorphic leaf, and phenotypic plasticity (biomass allocation) (Vretare et al. 2001; Hong and Kim 2016; Moor et al. 2017). On the other hand, despite the fact that some wetland plant species such as Phragmites australis [Cav.] Trin. ex Steud. and Lythrum anceps (Koehne) Makino exhibit high tolerance to dry stress, most wetland plant species are vulnerable to dry condition (Blossey et al. 2001; Hong and Kim 2012; Hong et al. 2018). Thus, drawdown (draw-off) in wetland ecosystems, causing changes in hydrology, may alter wetland vegetation and flora as well (Odland and del Moral 2002). For example, varying water levels and subsequent vegetational differences within abandoned paddy terraces (hereafter APTs) are likely the results from different drawdown processes within APTs after abandonment (Hong and Kim 2013b; Park et al. 2013). APTs, sometimes, may undergo terrestrialization process due to the severe drawdown for a long period of time (Kirschner et al. 2001; Lee et al. 2002).

Vegetational alterations in wetland ecosystems due to drawdown do not simply mean the shifts in species composition but potential threats for some vulnerable species (Wisheu and Keddy 1991). Desiccation stress by drawdown can be fatal to some vulnerable species particularly in seedling stage (Pence and Clark 2005). For another example, when compared to vascular plant species, wetland bryophytes such as Sphagnum spp. may be more vulnerable to dry stress than vascular plant species because those mosses do not develop cuticle and leaf stomata, which are of importance in preventing water loss (Titus et al. 1983; Schouwenaars and Gosen 2007). Most of all, when the period of drawdown becomes longer, dry stress could cause irreversible damage to Sphagnum spp. and even withering-to-death in the end (Wagner and Titus 1984).

Thus, many researchers have stressed the importance of management for stable hydrology in wetland ecosystems with considering the conservation of vulnerable species (Byun et al. 2008; Hong et al. 2012; Hong and Kim 2016). Some researchers have noted that stable maintenances of water level in wetland ecosystems seems likely to be much important for some endangered species (Shin et al. 2015; Hong et al. 2018). Nevertheless, numerous studies have reported unintended changes in the vegetation and flora of wetland ecosystems particularly in responses to drawdown (ter Braak and Wiertz 1994; Odland and del Moral 2002). In particular, unexpected changes in vegetation and flora by human activities such as land-use change may lead to the deterioration of wetland ecosystems due to biodiversity loss.

In the present study, we tried to focus on a naturalized Sphagnum-marsh that was once developed as a paddy field within a mountainous area (APTs). In Korea, most of the populations of Sphagnum spp. have been reported in montane wetlands with high altitude of over 1,000 m asl (Kim 2009; Park and Kim 2012), whereas the study site located in the area with an altitude of about 80 m asl adjacent to urban areas (Hong and Kim 2013). Recently, the study site has been undergone drawdown for 4 years because of land-use change into a dry field for land-crop production. In order to assess the impacts of drawdown on the Sphagnum-marsh, we compared the vegetation and flora of the wetland before and after the drawdown with focusing on a wetland moss species (Sphagnum palustre L.).


The study site (37°17'09.5"N and 126°55'20.3"E) of approximately 3200 m2 in area was located within a mountainous area of Ansan (about 80 m asl) in Gyeonggi Province, Korea. Mean values of daily mean temperature and monthly precipitation of the study site from 2011 to 2018 were ranged from about − 2 °C (January) to about 27 °C (August) and from about 13 mm (January) to about 380 mm (July), respectively (Additional file 1: Figure S1). The wetland is a typical APTs consisting of seven wetland units (Hong and Kim 2013a). Inflow water from the watershed of the study site was the major water source and precipitation was the minor one (Hong and Kim 2013a). Diverse plant species (a total of 70 species in 2011) including herbaceous species, tree species such as Salix spp., and a wetland moss species (S. palustre) with mosaic forms were reported from the study site (Hong and Kim 2013a). The inhabitation of an endangered species, scarlet pygmy dragonfly (Nannophya pygmaea Rambur), was also reported from the study site before the drawdown (Hong and Kim 2013a).

In order to exclude possible negative effects of rainy spell in the summer season from the study (Additional file 1: Figure S1), the field surveys for examining water and vegetational characteristics were performed in mid-June 2011 (before) and 2015 (after drawdown). Measuring and sampling water were performed within the area of open water. The values of water depth of each layer (wetland unit) were measured by using a wood-stick ruler (n = 9) and averaged. Dissolved oxygen (DO), electric conductivity (EC), and pH were measured at each sampling spot by using portable meters: DO (Orion 3 Star Portable DO meter; Thermo Fisher Scientific, USA), EC (Corning Checkmate model 311; Corning, USA), and pH (model AP 63; Fisher, USA). Water samples (n = 11 in 2011 and n = 6 in 2015) were carried to the laboratory in Seoul National University and were filtered by using nitrocellulose membrane filter (0.45 μm) for chemical analyses. Different numbers of water samples in 2011 (n = 11) and 2015 (n = 6) were due to different areas of inundated fields of the study site between before and after drawdown. Macronutrients (NO3–N, NH4–N, and PO4–P) were analyzed by the hydrazine method (Kamphake et al. 1967), indo-phenol method (Solorzano 1969), and ascorbic acid reduction method (Murphy and Riley 1962), respectively. Cations (K+, Ca2+, Na+, and Mg2+) as micronutrients were also analyzed by using an atomic absorption spectrometer (Model AA240FS; Varian, USA). To examine possible differences in physicochemical characteristics of wetland water, t test was performed by using statistical software, SPSS package for Windows (IBM SPSS Version 22.0, New York).

In order to estimate the areas of each vegetational cover on the study site, we assumed that each area of the vegetational components could be divided into individual area units (1 m2 in area). To meet the assumption, we divided each vegetational cover into grid-based meshes on the field by using several measuring tapes (50 m long). The plant species that formed some vegetational patches with less than 1 m2 in area were not included in the vegetational map but in the list of the flora. The taxonomic nomenclature designated by Lee (2003) and the Korean plant names index (KPNI, were used to identify vascular plant species of the wetland. The classification on plant species into five categories based on the frequency of each species in its habitats (obligate for wetlands (OBW), facultative for wetlands (FACW), facultative (FAC), facultative for uplands (FACU), and obligate for uplands (OBU)) was performed according to the literature by Choung et al. (2012).

Results and discussion

Effects of drawdown on water environments and S. palustre population

In order to assess the effects of drawdown on water environments and the S. palustre population in the study site, we compared physicochemical characteristics of wetland water and the coverage of S. palustre in 2011 (before) and 2015 (after drawdown) as the results in responses to environmental changes. Water chemistry of the study site did not show any remarkable change after drawdown. Although both nitrate nitrogen (0.25 ± 0.28 mg/L in 2011 and 0.34 ± 0.08 mg/L in 2015) and sodium (5.52 ± 0.40 mg/L in 2011 and 6.70 ± 0.65 mg/L in 2015) showed small increases with a statistical significance (p < .05) (Additional file 1: Table S1), it would be difficult to consider those differences as meaningful change possibly causing differences in the S. palustre population. On the other hand, water depth showed remarkable changes after the drawdown when compared to water chemistry. All the wetland units showed statistically significant decreases in water depth after the drawdown (Fig. 1). In some wetland units, water depth decreased to less than the half level by the drawdown. Although we did not measure the inundated areas within the wetland accurately, it seemed likely that not only the overall water depth but also the area of inundated fields of the wetland markedly decreased simultaneously after the drawdown (Fig. 1).

Fig. 1
figure 1

Inundated areas, S. palustre cover, and water depth of wetland units (n = 9, mean ± 1SD) in 2011 (before) and 2015 (after drawdown). Different alphabets next to water-depth values indicate statistically different sub-groups between 2011 and 2015 by t test (p < .05)

The coverage of S. palustre in the study site markedly decreased by about 75% (from approx. 247 m2 in 2011 to approx. 62 m2 in 2015) after the drawdown (Fig. 1). In particular, all the S. palustre on the tussock structures of grasses and sedges that had accounted for 73.8% of the total S. palustre coverage in 2011 clearly disappeared from the wetland. Instead, some dead parts of the moss only remained on the tussock structures. In other words, after the drawdown, the S. palustre population remained only on the slope side under the canopy of Pinus densiflora Siebold & Zucc. in the study site. It appeared that decreases in both water depth and inundated area of the study site might negatively affect the S. palustre population by desiccation stress with a long period of time (Wagner and Titus 1984; Hong and Kim 2013c). According to a previous study on the study site (Hong and Kim 2013a), as a hummock species, S. palustre patches were mostly found on the tussock structure with a depth of about 20 cm and partly on the slope side with a depth of about 5 cm. That is, the sharp decrease in the coverage of S. palustre on the tussock structure does not simply mean the reduction in the horizontal distribution of S. palustre only but remarkable reduction in the biomass production of S. palustre population.

Effects of drawdown on vegetation and flora of APTs

From our study, it seemed likely that a sharp decrease in water depth by drawdown not only reduced the area of S. palustre population but also markedly changed the vegetational map of the wetland (Fig. 2). First of all, the total coverage of tree species increased from about 2235 m2 accounting for about 70% of the total wetland area in 2011 to about 2643 m2 accounting for about 83% in 2015 (Additional file 1: Table S2). For example, Salix pierotii Miq. (from 1203 m2 to 1410 m2), S. koriyanagi Miq. (from 189 m2 to 276 m2), and Amorpha fruticosa L. (from 388 m2 to 445 m2) showed large increases in coverage areas after drawdown (Additional file 1: Table S2). In particular, despite the fact that Rosa multiflora Thunb. is an obligate plant for uplands (OBU), the tree species also showed an increase in the coverage (from 38 m2 to 47 m2) within the wetland (Fig. 2).

Fig. 2
figure 2

Vegetation maps of the study site in 2011 (before) and 2015 (after drawdown)

The occupied areas by tree species within the wetland increased, whereas most of the area of established herbaceous wetland species remarkably decreased after the drawdown. Polygonum thunbergii Siebold & Zucc. that was the most widely distributed herbaceous species in 2011 showed a sharp decrease in the coverage after the drawdown (from 292 m2 to 94 m2). In addition to P. thunbergii, some obligate plants for wetlands (OBW) such as Zizania latifolia (Griseb.) Turcz. ex Stapf (from 254 m2 to 175 m2), Phragmites australis (Cav.) Trin. ex Steud. (from 123 m2 to 53 m2), Carex dickinsii Franch. & Sav. (from 57 m2 to 29 m2), and Scirpus wichurae Boeckeler (from 38 m2 to 16 m2) also exhibited remarkable decreases in the coverage (Additional file 1: Table S2). In particular, some herbaceous wetland species such as Leersia japonica (Honda) Honda, Juncus effusus L., and Scirpus karuisawensis Makino were not included as the major vegetational components in 2015 because of decreased areas of their coverages. In contrast, established OBU species such as Mosla dianthera (Buch.-Ham. ex Roxb.) Maxim. did not show any decrease in the coverage and Artemisia princeps Pampanini, rather, showed a small increase in its coverage after the drawdown (Additional file 1: Table S2).

On the other hand, some herbaceous OBU species such as Perilla frutescens (L.) Britton (30 m2), Erigeron annuus (L.) Pers. (23 m2), and Setaria viridis (L.) P. Beauv. (7 m2) newly appeared in 2015. In addition, two herbaceous species [Echinochloa crus-galli (L.) P. Beauv. and Humulus scandens (Lour.) Merr.] also appeared after the drawdown. Although these species are classified as facultative plants for wetlands (FACW), they are also considered to be the species mainly occurring under environmentally disturbed wetlands (Maun and Barrett 1986; Kim and Kim 2009).

The total number of plant species of the study site slightly decreased from a total of 70 species to 62 species after the drawdown (Additional file 1: Table S3). Although only eight species decreased based on the flora list, it could not be simply considered to be just a reduction in the number of plant species of the study site. Most of all, some FACW [Eclipta prostrata (L.) L., Lobelia chinensis Lour., and Persicaria hydropiper (L.) Delarbre] and an OBW (Eriocaulon parvum Körn.) species disappeared not only in the vegetational map but also in the list of the flora of the study site in 2015.

Hydrological regimes including water depth (level), amplitude, and period are influential factors in determining the characteristics of wetland ecosystems (Carter 1986; Aldous et al. 2005). In particular, water depth as a physical characteristic is known as a critical driver determining the vegetational components of wetland ecosystems (Nam et al. 2014; Byun et al. 2017; Hong et al. 2018). On the other hand, decreases in water depth may alter the vegetational characteristics of wetland ecosystems and even cause terrestrialization (Lee et al. 2002; Byun et al. 2008), which means the transformation of wetlands into upland-like fields (Kirschner et al. 2001).

Such a remarkable alteration in the vegetational components was observed in our study. Tree species extended, whereas herbaceous species shrunk after the drawdown. Upland-inhabiting species such as OBU increased, whereas wetland-inhabiting species such as FACW and OBW decreased in terms of vegetational coverage. Some wetlands-inhabiting species disappeared even after the drawdown. Although we may consider such changes in the study site as a natural process on the trajectory of secondary succession in wetland ecosystems (Shim et al. 2013), it would be more reasonable to see such dramatic alterations as the results by a human-induced disturbance drawdown. In fact, replacement of herbaceous species by tree species often occurs particularly in APTs in which water depth is maintained with low levels or badly maintained (Lee et al. 2002; Byun et al. 2008). On the other hand, it has also been reported that the introduction of tree species such as Salix spp. could be prevented in APTs when deep water condition is maintained (Hong and Kim 2013c; Choi and Kim 2015; Hong et al. 2018).

Implications for APTs and APT-inhabiting species

According to the private conversation with the landowner of the study site, the wetland was planned to be utilized as a dry field for the production of terrestrial crops after the drawdown process. He also said that there are only few choices that the landowner could choose in practically utilizing such paddy fields within a montane area of low economic value due to low accessibility. Unfortunately, most APTs in Korea are locating in such private lands within mountainous areas (Hong et al. 2012; Park et al. 2013), indicating that those wetlands are also placed under potential threats from human activities such as land-use change as seen in our study site (Uchida and Ushimaru 2014).

During the last several decades, in Japan, high ecological value of APTs as wetland ecosystems has been stressed based on numerous ecological studies particularly on APT-inhabiting rare species including Sphagnum spp. (Uematsu and Ushimaru 2013; Kim et al. 2016; Fukamachi 2017). Based on those ecological studies on APTs, many attempts have been performed for the restoration and conservation of APTs as valuable biotopes (Washitani 2007; Nishio et al. 2017). On the other hand, in Korea, not only the wetland inventory for APTs in a national scale but also the ecological study on those wetlands are lacking yet. In the case of our study site, despite the fact that the inhabitation of an endangered species (N. pygmaea) was once reported before (Hong and Kim 2013a), unfortunately, the Sphagnum-marsh has been undergone drawdown due to land-use change resulting in decreases in herbaceous wetland species such as J. effusus that is essential for the endangered dragonfly species (Yoon et al. 2010).

In addition to the endangered dragonfly species in the study site, the remarkable decrease in the cover of S. palustre population after the drawdown might also be another ecological problem that we have to consider seriously. Sphagnum spp. are known as more vulnerable than vascular plant species to human-induced threats such as eutrophication and desiccation so that many countries have already designated some vulnerable Sphagnum spp. as rare species (Andrus et al. 1992; Terracciano et al. 2012). On the other hand, in Korea, Sphagnum spp. have not received much attention by researchers yet. Some studies on the taxonomic classification (Choi et al. 1989) and distributional characteristics (Kim 2009; Paik 2010; Park and Kim 2012; Hong and Kim 2013a; Kim and Kim 2014) of Sphagnum spp. of Korea have been performed only. In particular, the ecological study on Sphagnum spp. is still lacking. Hong and Kim (2013c) reported only a case study on an artificial wetland for guaranteeing the inhabitation of S. palustre with other macrophytes in lowlands.

In Korea, it appeared that APTs and APT-inhabiting vulnerable species such as rare plant species and Sphagnum spp. are placed under blind spots in terms of research, management, and conservation yet. We strongly suggest that the attention for further ecological studies and effort for the management and conservation of APTs and APT-inhabiting species that are vulnerable to human-induced disturbances have to be paid more. As naturalized wetlands, it has been noted that APTs show characteristics as both natural (hydrology and biology) (Park et al. 2013) and artificial wetlands (structure and topography) (Katoh et al. 2009; Nam et al. 2018). In that respect, existing APTs may play ecologically important roles as alternatives to artificial wetlands in various ways. In other words, restoration (or reclamation) and following conservation on existing APTs would be more cost-effective and ecologically appropriate instead of constructing more artificial wetlands particularly as biotopes.



Abandoned paddy terraces




Facultative for uplands


Facultative for wetlands


Obligate for uplands


Obligate for wetlands


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This research was supported by the National Research Foundation of Korea (NRF) funded by the Ministry of Education (NRF-2015R1D1A1A01057373) and by the Korea government (MSIT) (NRF-2018R1A2B2002267).

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The datasets during and/or analyzed during the current study are available from the corresponding author on reasonable request.

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MGH participated in the design of the study, field survey, and data analyses and wrote the manuscript draft. BEN participated in the field survey and data analyses and edited the manuscript draft. JGK conceived the study, participated in the design of study, edited the manuscript draft, and secured the funding. All authors read and approved the final manuscript.

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Correspondence to Jae Geun Kim.

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Figure S1. Precipitation (mean ± 1SD) and temperature (mean ± 1SE) of the study site from 2011 to 2018. Table S1. Water characteristics of the study site in 2011 (before) and 2015 (after drawdown). Boldface letters indicate significant difference between the two years in t test at p < 0.05 range. Table S2. Differences in the area of vegetational components between in 2011 (before) and 2015 (after drawdown). Table S3. The flora of the study site in 2011 (before) and 2015 (after drawdown). (DOCX 75 kb)

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Hong, M.G., Nam, B.E. & Kim, J.G. Changes in vegetation and flora of abandoned paddy terraces in responses to drawdown. j ecology environ 43, 22 (2019).

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