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Minor Treatments Can Play a Significant Role in Preserving Natural Habitats and Protected Species on the Shore of a Central European Lake

Minor Treatments Can Play a Significant Role in Preserving Natural Habitats and Protected Species... agronomy Article Minor Treatments Can Play a Significant Role in Preserving Natural Habitats and Protected Species on the Shore of a Central European Lake 1 , 2 1 , 1 Bence Fülöp , Bálint Pacsai * and Judit Bódis Department of Conservation Biology, Institute for Wildlife Management and Nature Conservation, Georgikon Campus, Hungarian University of Agriculture and Life Sciences, Festetics u. 7., H-8360 Keszthely, Hungary; 9112bence@gmail.com (B.F.); bodis.judit.zsuzsanna@uni-mate.hu (J.B.) Balaton-Felvidéki National Park Directorate, Kossuth u. 16., H-8229 Csopak, Hungary * Correspondence: pacsai.balint@uni-mate.hu Abstract: Semi-natural grasslands were previously established through traditional land use and maintained by active management, but their extension nowadays is declining rapidly, particularly in areas that also have tourism potential. In parallel, the conservation value of the remaining areas is increasing. The shore of Lake Balaton is a particularly good example, as Lake Balaton is an area highly affected by tourism, yet there have been valuable habitats able to survive and provide refuge for many vulnerable, protected species. Fortunately, we have reliable information about the vegetation of the area from two decades ago. Comparing these data with our recent surveys we investigated the changes in habitats and the distribution of protected plant species in connection with the active conservation treatments such as grazing or cutting. Our results show that in areas where treatments are still ongoing, protected plant species are more likely to survive, or even other species can appear, which is in clear contrast with conditions experienced in abandoned areas, where at least seven Citation: Fülöp, B.; Pacsai, B.; Bódis, protected species have disappeared. According to our results, minor, but appropriately chosen and J. Minor Treatments Can Play a well-executed management interventions, can help in the long-term maintenance of species-rich Significant Role in Preserving Natural habitats and improving the conservation status of threatened species. Habitats and Protected Species on the Shore of a Central European Lake. Keywords: nature conservation; grassland management; habitat loss; semi-natural habitats; reed bed Agronomy 2021, 11, 1540. https:// doi.org/10.3390/agronomy11081540 Academic Editor: Karoly Penksza 1. Introduction Received: 20 June 2021 Most semi-natural habitats in Europe have been traditionally maintained by anthro- Accepted: 28 July 2021 pogenic activities, such as grazing or mowing [1–7]. Since the 1950s grassland abandonment Published: 31 July 2021 became a general phenomenon in Europe. The factors driving the abandonment were complex but mainly associated with the increasing agricultural intensification, along with Publisher’s Note: MDPI stays neutral socio-economic and political changes [8]. This process was particularly pronounced in with regard to jurisdictional claims in areas with considerable tourism potentials [9,10]. After recognizing the negative effects of published maps and institutional affil- abandonment on wildlife in the 1980s, the restoration of grasslands began primarily for iations. nature conservation purposes [11,12]. Lake Balaton is the largest lake in Central Europe. In surrounding areas, and on its shores, grasslands had great importance until the 1950s [13]. With the development of the bathing culture, which emerged at the beginning of the 20th century, livelihood from Copyright: © 2021 by the authors. agriculture was replaced by tourism. This led to the establishment of beaches, harbours, Licensee MDPI, Basel, Switzerland. and recreational areas in places of reed [Phragmites australis (Cav.) Trin. ex Steud.] beds This article is an open access article and grasslands. Livestock farming in coastal settlements was restricted from 1969 by distributed under the terms and law to support the expansion of tourism, thus coastal grazing was almost completely conditions of the Creative Commons abolished [14]. Attribution (CC BY) license (https:// The shore of Lake Balaton at Fenékpuszta was a rare exception to this as cattle were creativecommons.org/licenses/by/ grazing there until 1983, therefore a ~3 km long coastline remained in a close-to-nature 4.0/). Agronomy 2021, 11, 1540. https://doi.org/10.3390/agronomy11081540 https://www.mdpi.com/journal/agronomy Agronomy 2021, 11, x 2 of 12 Agronomy 2021, 11, 1540 2 of 12 The shore of Lake Balaton at Fenékpuszta was a rare exception to this as cattle were grazing there until 1983, therefore a ~3 km long coastline remained in a close-to-nature state with wet grasslands and wide reed beds connected to them. The natural value of the state with wet grasslands and wide reed beds connected to them. The natural value of area was first recognized by ornithologists and a bird-ringing station was established in the area was first recognized by ornithologists and a bird-ringing station was established the area in 1985. They also began the systematic investigation of the botanical value and in the area in 1985. They also began the systematic investigation of the botanical value began to preserve this with minor conservation treatments from 1987 [15]. The most and began to preserve this with minor conservation treatments from 1987 [15]. The most thorough management took place between 1999 and 2002, when 5–28 cattle were grazing thorough management took place between 1999 and 2002, when 5–28 cattle were grazing in in the area [16]. Detailed monitoring and documentation of the botanical value were car- the area [16]. Detailed monitoring and documentation of the botanical value were carried ried out during this period [15,17]. Later, the intensity and the extent of grazing de- out during this period [15,17]. Later, the intensity and the extent of grazing decreased and creased and became less documented, but in still ongoing to this day. became less documented, but in still ongoing to this day. Our aim was to assess the current natural condition of the area and to summarize Our aim was to assess the current natural condition of the area and to summarize the changes in habitats and the distribution of protected species occurring since 2002, in the changes in habitats and the distribution of protected species occurring since 2002, in connection with the treatments carried out after. We attempted to identify what changes connection with the treatments carried out after. We attempted to identify what changes could be detected in the vegetation and plant species distribution of the treated and un- could be detected in the vegetation and plant species distribution of the treated and treated areas after 18 years and what conditions are currently characterizing them. We untreated areas after 18 years and what conditions are currently characterizing them. We seek to demonstrate that even in an area highly affected by tourism, botanical value and seek to demonstrate that even in an area highly affected by tourism, botanical value and semi-natural habitats could be preserved in the long-term with minor treatments only. semi-natural habitats could be preserved in the long-term with minor treatments only. 2. Materials and Methods 2. Materials and Methods 2. 2.1. 1. St Study udy Are Area a The study The study ar area is loc ea is located ated on the western coast o on the western coast off L Lake ake B Balaton alaton near near the tow the town n of of Keszt Keszthely hely (H (Hungary) ungary) (F (Figur igure e 1) 1).. The e The examined xamined ar area ea is is 3 km 3 km long long and and its its wi width dth rang ranges es between 3 between 320–820 20–820m, m, coveri coveringng 13013 hectar 0 hecta es altogether res altoget . Ither. It is bo is bordered by rdered by th the stream Cs e stream ókakoi ˝ (North), by River Zala (South), by road number 71 (West), and by Lake Balaton (East). Most Csókakői (North), by River Zala (South), by road number 71 (West), and by Lake Balaton of the study area is part of the Natura 2000 site Balaton (N2K HUBF30002), which is a (East). Most of the study area is part of the Natura 2000 site Balaton (N2K HUBF30002), Special Area of Conservation and a Special Protected Area. Despite the intensive use of which is a Special Area of Conservation and a Special Protected Area. Despite the inten- Lake Balaton for touristic purposes, the shores of the lake at Fenékpuszta remained in a sive use of Lake Balaton for touristic purposes, the shores of the lake at Fenékpuszta re- relatively natural state [16]. mained in a relatively natural state [16]. Figure 1. Location of the study area. Figure 1. Location of the study area. Zentai [15] offered us a detailed description of the implementation of conservation Zentai [15] offered us a detailed description of the implementation of conserva- management tion management in Fenékpuszta be in Fenékpuszta tween between 1999 a1999 nd 200 and 2. The shore of Lake Ba 2002. The shore of Lake laton a Balaton t Fen- ékpus at Fenzétkpuszta a was a twas radita iona traditional l pasture a pastur rea fo er cent area ur for ies b centuries ut the gr but azin the g ended grazing in 1 ended 983 [17]. in 1983 [17]. After the years of abandonment, grazing was recommenced in 1999 with five cattle at the middle part of the study area. In the following years, the grazed area gradually Agronomy 2021, 11, x 3 of 12 After the years of abandonment, grazing was recommenced in 1999 with five cattle at the Agronomy 2021, 11, 1540 3 of 12 middle part of the study area. In the following years, the grazed area gradually increased, and by 2002 the total study area had become grazed with the exception of the reed beds. The size of the cattle herd reached its peak in 2001 with a total of 28 animals [16], after that, their number rapidly decreased, followed by shrinkage of the managed area increased, and by 2002 the total study area had become grazed with the exception of the and the focus of the grazing shifted to the southern parts of the area (Figure 2). In 2020, reed beds. the northern part of the area had not received treatment for at least 10 years; the central The size of the cattle herd reached its peak in 2001 with a total of 28 animals [16], part is mowed once a year and after mowing a very light after-grass grazing takes place after that, their number rapidly decreased, followed by shrinkage of the managed area and there, while the southern part has a constant presence of cattle, which trample and graze the focus of the grazing shifted to the southern parts of the area (Figure 2). In 2020, the the area all year round (Figure 2). northern part of the area had not received treatment for at least 10 years; the central part The overall size of the study area decreased by almost 6 hectares between 2002 and is mowed once a year and after mowing a very light after-grass grazing takes place there, 2020 as a result of an average 20-m retreat of the reed beds on the 3 km coastline (Table 1, while the southern part has a constant presence of cattle, which trample and graze the area F all igu year re 3r )ound . (Figure 2). (a) (b) Figure 2. Areas under conservation management (cutting and grazing) in four subsequent years from 1999 to 2002 (a) and Figure 2. Areas under conservation management (cutting and grazing) in four subsequent years from 1999 to 2002 (a) and in 2020 (b). in 2020 (b). To compa The overall re the current vegeta size of the study arti ea on decr and eased distri by bualmost tion of protected p 6 hectares between lant speci 2002 es wi and th previous 2020 as a rdat esult a, we d of anig average italized the h 20-m ra etr bit eat at an of the d protec reed ted species beds on the d 3ikm stribut coastline ion ma (T ps of able 1a, Figure 3). comprehensive study from 2002 [15] using satellite images (Google Earth) and aerial To compare the current vegetation and distribution of protected plant species with photographs (Lechner Nonprofit Ltd., Budapest, Hungary), which have become availa- previous data, we digitalized the habitat and protected species distribution maps of a ble for public use since then. comprehensive study from 2002 [15] using satellite images (Google Earth) and aerial photographs (Lechner Nonprofit Ltd., Budapest, Hungary), which have become available for public use since then. Agronomy 2021, 11, 1540 4 of 12 Table 1. Area changes of the habitat type categories between 2002 and 2020. Habitat Type Area (ha) in 2002 Area (ha) in 2020 Difference (ha) Difference (%) Reed beds 63.66 53.76 9.90 15.56 Wet meadows 14.80 12.77 2.03 13.75 Mesophilous grasslands 2.85 4.94 2.09 73.35 Wet pioneer scrubs and willow carrs 0.80 4.64 3.84 482.42 Uncharacteristic habitats 23.95 12.18 11.77 49.15 Stands of native tree species 9.78 13.85 4.07 41.66 Stands of invasive tree species 6.42 13.84 7.42 115.59 Agricultural and other antropogenic habitats 15.02 15.39 0.30 1.99 Agronomy 2021, 11, x 4 of 12 Total 137.26 131.28 5.98 4.36 (a) (b) Figure 3. Habitat category groups in 2002 (a) and 2020 (b). Figure 3. Habitat category groups in 2002 (a) and 2020 (b). Table 1. Area changes of the habitat type categories between 2002 and 2020. 2.2. Field Work Identification of the habitats was carried out during the vegetation periods of years Area (ha) in Area (ha) in Difference Habitat Type Difference (%) 2019 and 2020, which included thorough surveying of the area on land by foot and also 2002 2020 (ha) by water (with canoe). During these surveys, we collected data on protected plant species Reed beds 63.66 53.76 −9.90 −15.56 by recording GPS coordinates on each occurrence and counting individuals, or in the case Wet meadows 14.80 12.77 −2.03 −13.75 of clonal species, such as Acorus calamus L. and Nymphaea alba L., we estimated the area Mesophilous grasslands 2.85 4.94 2.09 73.35 occupied by each population. The extension and the way of the current management were Wet pioneer scrubs and willow carrs 0.80 4.64 3.84 482.42 also mapped during the fieldwork (Figure 2). In 2020, on the southern part of the area, 20 Uncharacteristic habitats 23.95 12.18 −11.77 −49.15 cattle were grazing, and the northern part of the area was cut once a year during summer. Stands of native tree species 9.78 13.85 4.07 41.66 The grazing usually started in late April and ended in October. Stands of invasive tree species 6.42 13.84 7.42 115.59 Agricultural and other antropogenic habitats 15.02 15.39 0.30 1.99 Total 137.26 131.28 −5.98 −4.36 2.2. Field Work Identification of the habitats was carried out during the vegetation periods of years 2019 and 2020, which included thorough surveying of the area on land by foot and also by water (with canoe). During these surveys, we collected data on protected plant species by recording GPS coordinates on each occurrence and counting individuals, or in the case of clonal species, such as Acorus calamus L. and Nymphaea alba L., we estimated the area occupied by each population. The extension and the way of the current management were also mapped during the fieldwork (Figure 2). In 2020, on the southern part of the Agronomy 2021, 11, 1540 5 of 12 2.3. Protected Species Most protected species in the study area are characteristic to sedge- and reed commu- nities. These habitats, although relatively common along the shoreline of Lake Balaton, are mostly in a poor condition and lacking rare species. In 2002, an overall 23 species were recorded in the study area which are protected by law. Among these species, only Cirsium brachycephalum Jur. is on the 1992 Habitats Directive Annex II list. In 2020, the number of protected species were decreased to 17, most of which belonged to the family Orchidaceae. Among the protected species, some have greater local importance, like Hydrocotyle vulgaris L., as almost all of its occurrences in Hungary are limited to the shoreline of Lake Balaton. Samolus valerandi L., Urtica kioviensis Rogow., and Acorus calamus have considerable portions of their total national population occurring near Lake Balaton as well. Other species, such as Ranunculus lingua L. and Equisetum variegatum Schleich., are rare and very sporadic across the country, therefore their occurrences at Fenékpuszta have regional importance. 2.4. Data Processing First, we classified the vegetation data (habitat descriptions of [15] and the current field data as well) into habitat classes, based on the species pool and structure according to the General National Habitat Classification System of Hungary (Á-NÉR) [18]. Then, we merged the similar classes to the generalized habitat categories for better visualization (Table 1). We also plotted the recorded data of the protected plant species occurrences and areas affected by management, according to [15] and current data as well. 3. Results 3.1. Changes in Habitats and Vegetation Reed beds were that habitat type category which area decreased the most among the categories. This is caused by the die-back from the direction of the open water men- tioned earlier, and to a lesser extent by the area loss caused by shrub encroachment and afforestation on land (Table 2). Table 2. Habitat categories of Á-NÉR occurring in the area and our categorization of them. Generalized Habitat Category Á-NÉR/Natura Habitat Category Reed beds Eu- and mesotrophic reed and Typha beds (B1a) Tussock sedge communities (B4) Non-tussock tall-sedge beds (B5) Wet meadows Rich fens (D1)/7230 Alkaline fens Mesotrophic wet meadows (D34)/ Alluvial meadows of river valleys of the Cnidion dubii (6440) Mesophilous meadows Arrhenatherum hay meadows (E1) Willow carrs (J1a)/Alluvial forests with Alnus glutinosa and Fraxinus Wet pioneer scrubs and willow carrs excelsior (91E0) Wet and mesic pioneer scrub (P2a) Uncharacteristic wetlands (OA) Uncharacteristic mesic grasslands (OB) Uncharacteristic habitats Uncharacteristic dry and semi-dry grasslands (OC) Stands of invasive forbs (OD) Scattered native trees or narrow tree lines (RA) Stands of native tree species Uncharacteristic or pioneer softwood forests (RB) Stands of invasive tree species Spontaneous stands of non-native tree species (S6) Annual intensive arable fields (T1) Agricultural and other anthropogenic habitats Farms (U10) Roads and railroads (U11) Agronomy 2021, 11, 1540 6 of 12 A noticeable decrease in the overall area (13%) of the wet meadows was also detected (Table 2, Figure 3). The northern part of the study area where the grazing was abandoned on the wet meadows in 2002, had become densely covered by invasive tree species and by native tree and shrub species by 2020 (Figure 4). The highest situated part of the wet meadows, where the grazing management is still ongoing became the mesophilous Agronomy 2021, 11, x 7 of 12 meadows with the dominance of Arrhenatherum elatius (L.) and Helictotrichon pubescens (Huds.). Figure 4. Transitions between habitat category groups in hectares and in percentage of the former Figure 4. Transitions between habitat category groups in hectares and in percentage of the former area of the original habitat category group. area of the original habitat category group. The advance of woody stands (of both invasive and native species) is also noticeable in Other species retained their populations to roughly the same extent and number. the whole area. These habitats had the largest increase in their total area, currently covering Populations of Cicuta virosa L. and Allium carinatum L. had not changed substantially, not more than twice their former area described by an earlier study [15]. Unfortunately, these in location, nor in the number of individuals. The situation is similar in the case of two stands are mostly dominated by invasive alien tree species, such as Robinia pseudoacacia orchid species, Ophrys sphegodes Mill. and Neottia ovata (L.) Bluff and Fingerh. L. and Fraxinus pennsylvanica Marshall, whereas the most common native tree species in Some species significantly increased in the number of individuals. Former localities the study area, Populus spp. and Salix alba L., are present sporadically in these forests or of Cephalanthera longifolia (L.) Fritsch are still present in the northern part, and the species forming small groves. appeared in the southern area as well. We recorded new occurrences of Neottia ovata in the northern area beside the large population in the southern part. The former single small population of Samolus valerandi in the northern area went extinct, but the species had appeared in several locations in the southern wet meadows area, mostly on the edges of the grazed area. Agronomy 2021, 11, 1540 7 of 12 3.2. Presence and Distribution of the Protected Species During the 2002 survey, 23 different protected plant species were described from the area. In the year 2020, we found 17 protected plant species (Table 3), from which four species [Epipactis tallosii A. Molnár and Robatsch, Cephalanthera damasonium (Mill.) Druce, Equisetum variegatum, Neottia nidus-avis (L.) Rich] were not described previously from the area (Figure 5). Some of the disappeared species were present earlier only by a few individuals: Anacamptis coriophora (L.) R.M. Bateman, Pridgeon and M.W. Chase, Botrychium lunaria (L.) Sw., Carex paniculata L., Cirsium brachycephalum, Epipactis helleborine (L.) Crantz, Spiranthes spiralis (L.) Chevall., but in other cases, considerable populations vanished or we were not able to find them: Anacamptis morio (L.) R.M. Bateman, Pridgeon and M.W. Chase, Epipactis palustris (L.) Crantz, Hydrocotyle vulgaris, Schoenus nigricans L., Urtica kioviensis. The majority of the newly appeared species, like Epipactis tallosii, Cephalanthera damaso- nium, and Neottia nidus-avis, were found with a few individuals under native tree stands. Substantial populations of Equisetum variegatum were observed in the southern wet meadow area which is currently grazed. The 13 species which were observed in the area during both surveys had some changes in their distribution as well. Table 3. The number of localities and individuals of protected plant species in 2002 and 2020. Number of Localities Number of Individuals Species 2002 2020 2002 2020 2 2 Acorus calamus many 18 ~1500 m ~900 m Allium carinatum 1 1 50–80 45 Anacamptis coriophora 1 – 7 – Anacamptis morio 1 – 107 – Anacamptis palustris 2 1 120–140 10 Botrychium lunaria 1 – 2 – Carex paniculata 1 – 3–5 – Cephalanthera – 2 – 5 damasonium Cephalanthera longifolia 3 5 6 10 Cicuta virosa several 10 few hundred ~100 Cirsium brachycephalum 1 – 10 – Dactylorhiza incarnata several 7 400–450 16 Epipactis helleborine 1 – 2 – Epipactis palustris few – 210–250 – Epipactis tallosii – 5 – 37 Equisetum variegatum – 8 – 16 m Hydrocotyle vulgaris 1 – 50 m – Neottia nidus-avis – 4 – 9 Neottia ovata 3 12 1000–2000 1536 2 2 Nymphaea alba 2 2 500 m ~40 m Ophrys sphegodes 1 1 120 150 Orchis militaris 4 9 250–350 112 Ranunculus lingua 4 1 110–165 1 Samolus valerandi 1 9 16 10–15 m Schoenus nigricans – – – ~200 m Spiranthes spiralis 1 – 1 – Trapa natans 2 1 ~200 m Urtica kioviensis several – few hundred – Agronomy 2021, 11, 1540 8 of 12 Agronomy 2021, 11, x 8 of 12 (a) (b) Figure 5. Habitat category groups in 2002 (a) and 2020 (b). Figure 5. Habitat category groups in 2002 (a) and 2020 (b). Table 3. Ther The e ar nu ember of local species in which ities and in populations dividuals of declined protected considerably plant species in . Acorus 2002 and calamus 2020. disap- peared from the northern area and also from most of its former localities in the southern Number of Localities Number of Individuals area. In 2020, its single large population was located on the grazed wet meadows on Species 2002 2020 2002 2020 the southern part. Large colonies of Nymphaea alba were considerably reduced in their 2 2 Acorus calamus many 18 ~1500 m ~900 m extent. Ranunculus lingua almost disappeared, and in the last vegetation period only one Allium carinatum 1 1 50–80 45 flowering plant was seen. Among the orchids, populations of Anacamptis palustris (Jacq.) Anacamptis coriophora 1 – 7 – R.M. Bateman, Pridgeon and M.W. Chase and Dactylorhiza incarnata (L.) Soó suffered the greatest reduction in size, both represented by only 10–20 flowering plants in the area. Anacamptis morio 1 – 107 – Reduction in the number of individuals was also apparent in the case of Orchis militaris L., Anacamptis palustris 2 1 120–140 10 its population has decreased to the third of its former size. Botrychium lunaria 1 – 2 – Other species retained their populations to roughly the same extent and number. Carex paniculata 1 – 3–5 – Populations of Cicuta virosa L. and Allium carinatum L. had not changed substantially, not Cephalanthera damasonium – 2 – 5 in location, nor in the number of individuals. The situation is similar in the case of two Cephalanthera longifolia 3 5 6 10 orchid species, Ophrys sphegodes Mill. and Neottia ovata (L.) Bluff and Fingerh. Cicuta virosa several 10 few hundred ~100 Some species significantly increased in the number of individuals. Former localities Cirsium brachycephalum 1 – 10 – of Cephalanthera longifolia (L.) Fritsch are still present in the northern part, and the species Dactylorhiza incarnata several 7 400–450 16 appeared in the southern area as well. We recorded new occurrences of Neottia ovata in Epipactis helleborine 1 – 2 – the northern area beside the large population in the southern part. The former single Epipactis palustris few – 210–250 – small population of Samolus valerandi in the northern area went extinct, but the species had Epipactis tallosii – 5 – 37 appeared in several locations in the southern wet meadows area, mostly on the edges of Equisetu the grazed m var area. iegatum – 8 – 16 m Hydrocotyle vulgaris 1 – 50 m – Neottia nidus-avis – 4 – 9 Neottia ovata 3 12 1000–2000 1536 Agronomy 2021, 11, 1540 9 of 12 4. Discussion The dieback of the reed beds—which refers to an average 20 m retreat in our case—is a well-known and general problem at Lake Balaton [19]. Although the reeds spread over many other habitats along the coast, these stands cannot be recognized as autochthonous reed beds, as they do not have the species pool, nor the structure characteristic of such stands, and remnants of the original habitat are still present under the newly formed reed cover. As a result, the overall decrease in the size of the reed bed is even greater than the retreat from the direction of the open water, which equals 9.9 hectares. In the northern areas, a short period of grazing (1999–2003) opened up the structure to the vegetation resulting in a relatively large area of continuous wet meadows [15]. The loss of that habitat type after the abandonment is a consequence of intensive scrubbing and the advance of invasive species [20]. These wet meadows corresponded to the Natura 2000 habitat category ‘6440 Alluvial meadows of river valleys of the Cnidion dubii’, which also indicates that it is a particularly valuable habitat type. Wet meadows are also threatened by drought in connection with climate change, and large areas of this habitat type turning into mesophilous meadows at the highest situated areas. Despite the rise in the water level of Lake Balaton after 2016, we did not experience this transformation in the opposite direction between these habitat category groups, and the number of helo- and hydrophytes have been reduced, to which the abandonment of management may have synergetic contributions. On the other hand, grazing is still actively going on in the southern part, which has allowed the transformation of formerly degraded, uncharacteristic habitats to valuable meadows like other areas of Pannonian vegetation [21]. In the central areas due to the targeted conservation management (which is optimized to maintain the population of Ophrys sphegodes) this area has remained relatively intact. Seven species, Acorus calamus, Schoenus nigricans, Anacamptis palustris, Hydrocotyle vulgaris, Anacamptis coriophora, Epipactis palustris, and Cirsium brachycephalum have all disappeared from the northern parts in connection with the degradation of the former wet meadows. From all the protected species occurring in the area, only several orchid species are still present in the northern part, as these species can survive for a long time even in unfavorable circumstances [22,23], but their numbers have also decreased significantly. Although the effect of the water level rise at Lake Balaton was not perceptible in the meadows, it is possible that the high water level was the reason why we were unable to reach the former localities of Carex paniculata and Urtica kioviensis at the reed beds [19]. Species connected to forest habitats, like Cephalanthera damasonium and Neottia nidus- avis, appeared in the northern part, most likely because of the spontaneous afforestation of the initial habitats. As one of the new Epipactis tallosii occurrences is close to the position of the single former Epipactis helleborine locality, and we could not find the latter species in the area, we suppose that this new taxon for the area is just a result of a recent change in taxonomy. Epipactis tallosii was described in 1997 [24], and by the turn of the millennium, almost all individuals of E. tallosii have still been identified as E. helleborine. At the central part of the study area, a major proportion of the mesophilic mead- ows were afforested by invasive tree species, which finally led to the disappearance of Botrychium lunaria, Anacamptis morio, and Spiranthes spiralis. On the actively grazed field of the southern part, we detected some areas covered by Equisetum variegatum, which this species had not been reported earlier from the area. We suspect that this was only an overlooking as it is a very small and inconspicuous plant. The number of individuals of Samolus valerandi has increased significantly and its occurrences have shifted from the northern parts to the southern region. This species clearly found its living conditions as a result of grazing, typically below the electric fence on the edges of grazed areas. In 2020, most former patches of Acorus calamus had already disappeared in the whole area, but a new one appeared in the currently grazed area. Cattle typically do not con- Agronomy 2021, 11, 1540 10 of 12 sume this species, so it can spread over actively grazed areas. On the western part, the sizeable patch of Neottia ovata and the population of Orchis militaris are also surviving and their numbers remained roughly the same, despite some of their occurrences outside the managed area. Overall, our results show that in contrast with the northern part, where the con- servational management almost entirely ceased, and many protected species that have disappeared, the southern grazed part offered suitable habitat for them. 5. Conclusions Our results confirm the results of previous research on wet grasslands in which a complete lack of treatments can lead to habitat depopulation and species decline or even complete extinction [20,25], but according to previous studies, this process might be reversible [2,26]. Therefore, we need to strive for maintaining some appropriate treatment in as large of an area as possible, preferably by grazing, which can be replaced with mowing on areas where grazing is not feasible. This could prevent the loss of biodiversity by maintaining the species pool and preventing the advance of invasive alien species. The conservation of ecologically valuable coastal reeds must also be given serious emphasis, as their decline in the long-term could mean a serious threat to the ecological status of the lake and even to its use for tourism [19,27]. The shore of Lake Balaton in Fenékpuszta is a good example of the fact that high species richness can occur even in an area that is currently primarily used for touristic purposes. Fortunately, near our sample area, there are other high-diversity habitat patches over the other side of River Zala. We should ensure their permanent connection in order to provide better chances for species to survive. These habitats serve as ecological corridors to larger natural habitats, namely to the Kis-Balaton [28]. Even in development plans determining utilization of the study area, the primary goal should be the preservation of biodiversity. The coast of Lake Balaton at Fenékpuszta could be a great target for eco-tourism and can play an important role in environmental education as well, which has a long tradition in the area [29,30]. It is also worth considering organizing botanical trips besides the bird-ringing programs, but we must not forget to continue the extensive use of the grassland, which can be well aligned with the basic goals of the establishment of the Natura 2000 network. We would also suggest that in the future the overall area of treatments should be increased at least to their previous largest extent (in 2002). Author Contributions: Conceptualization, B.F., J.B. and B.P.; investigation, B.F. and B.P.; resources, B.F. and J.B.; data curation, B.P.; writing—original draft preparation, B.F. and J.B.; writing—review and editing, B.F. and B.P.; visualization, B.P.; supervision, J.B.; project administration, B.F. and J.B.; funding acquisition, J.B. and B.F. All authors have read and agreed to the published version of the manuscript. Funding: The publication is supported by the EFOP-3.6.3-VEKOP-16-2017-00008 project. The project is co-financed by the European Union and the European Social Fund. Institutional Review Board Statement: Not applicable. Informed Consent Statement: Not applicable. Data Availability Statement: Data presented in this study are available on request from the corre- sponding author. Acknowledgments: The article is dedicated to the memory of Sándor Palkó (1959–2002), who discovered the natural value of Fenékpuszta and became a committed protector of this area, which he loved very much. The authors are thankful to Kinga Zentai for the detailed descriptions, to Anikó Benke and Szabolcs Benke for their valuable help in the field, and as well as to Zoltán Botta-Dukát for suggestions to the earlier version of the manuscript. Agronomy 2021, 11, 1540 11 of 12 Conflicts of Interest: The authors declare no conflict of interest. The funders had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or in the decision to publish the results. References 1. Carboni, M.; Dengler, J.; Mantilla-Contreras, J.; Venn, S.; Török, P. Conservation Value, Management and Restoration of Europe’s Semi-Natural Open Landscapes. Hacquetia 2015, 14, 5–17. [CrossRef] 2. Török, P.; Penksza, K.; Tóth, E.; Kelemen, A.; Sonkoly, J.; Tóthmérész, B. Vegetation type and grazing intensity jointly shape grasing on grassland biodiversity. Ecol. Evol. 2018, 8, 10326–10335. [CrossRef] 3. Penksza, K.; Csík, A.; Filep, A.F.; Saláta, D.; Pápay, G.; Kovács, L.; Varga, K.; Pauk, J.; Lantos, C.; Lisztes-Szabó, Z. Possibilities of Speciation in the Central Sandy Steppe, Woody Steppe Area of the Carpathian Basin through the Example of Festuca Taxa. Forests 2020, 11, 1325. 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Kaszálás felhagyásának kezdeti hatása nyugat-magyarországi üde gyepek fajkompozíciójára (Early effects of cessation of mowing on the species composition of wet meadows in Western Hungary). Gyepgazdálkodási Közlemények 2012, 10, 13–20. (In Hungarian) 29. Bajor, Z.; Zimmermann, Z.; Szabó, G.; Fehér, Z.; Járdi, I.; Lampert, R.; Kerény-Nagy, V.; Penksza, P.; Lisztes-Szabó, Z.; Székely, Z.; et al. Effect of conservation management practices on sand grassland vegetation in Budapest, Hungary. Appl. Ecol. Environ. Res. 2016, 14, 233–247. [CrossRef] 30. Dobay, G.; Dobay, B.; Saláta-Falusi, E.; Hajnáczki, S.; Penksza, K.; Bajor, Z.; Lampert, R.; Bakó, G.; Wichmann, B.; Szerdahelyi, T. Effects of sport tourism on temperate grassland communities (Duna-Ipoly National Park, Hungary). Appl. Ecol. Environ. Res. 2017, 15, 457–472. [CrossRef] http://www.deepdyve.com/assets/images/DeepDyve-Logo-lg.png Agronomy Multidisciplinary Digital Publishing Institute

Minor Treatments Can Play a Significant Role in Preserving Natural Habitats and Protected Species on the Shore of a Central European Lake

Fülöp, Bence; Pacsai, Bálint; Bódis, Judit
Agronomy , Volume 11 (8) – Jul 31, 2021
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agronomy Article Minor Treatments Can Play a Significant Role in Preserving Natural Habitats and Protected Species on the Shore of a Central European Lake 1 , 2 1 , 1 Bence Fülöp , Bálint Pacsai * and Judit Bódis Department of Conservation Biology, Institute for Wildlife Management and Nature Conservation, Georgikon Campus, Hungarian University of Agriculture and Life Sciences, Festetics u. 7., H-8360 Keszthely, Hungary; 9112bence@gmail.com (B.F.); bodis.judit.zsuzsanna@uni-mate.hu (J.B.) Balaton-Felvidéki National Park Directorate, Kossuth u. 16., H-8229 Csopak, Hungary * Correspondence: pacsai.balint@uni-mate.hu Abstract: Semi-natural grasslands were previously established through traditional land use and maintained by active management, but their extension nowadays is declining rapidly, particularly in areas that also have tourism potential. In parallel, the conservation value of the remaining areas is increasing. The shore of Lake Balaton is a particularly good example, as Lake Balaton is an area highly affected by tourism, yet there have been valuable habitats able to survive and provide refuge for many vulnerable, protected species. Fortunately, we have reliable information about the vegetation of the area from two decades ago. Comparing these data with our recent surveys we investigated the changes in habitats and the distribution of protected plant species in connection with the active conservation treatments such as grazing or cutting. Our results show that in areas where treatments are still ongoing, protected plant species are more likely to survive, or even other species can appear, which is in clear contrast with conditions experienced in abandoned areas, where at least seven Citation: Fülöp, B.; Pacsai, B.; Bódis, protected species have disappeared. According to our results, minor, but appropriately chosen and J. Minor Treatments Can Play a well-executed management interventions, can help in the long-term maintenance of species-rich Significant Role in Preserving Natural habitats and improving the conservation status of threatened species. Habitats and Protected Species on the Shore of a Central European Lake. Keywords: nature conservation; grassland management; habitat loss; semi-natural habitats; reed bed Agronomy 2021, 11, 1540. https:// doi.org/10.3390/agronomy11081540 Academic Editor: Karoly Penksza 1. Introduction Received: 20 June 2021 Most semi-natural habitats in Europe have been traditionally maintained by anthro- Accepted: 28 July 2021 pogenic activities, such as grazing or mowing [1–7]. Since the 1950s grassland abandonment Published: 31 July 2021 became a general phenomenon in Europe. The factors driving the abandonment were complex but mainly associated with the increasing agricultural intensification, along with Publisher’s Note: MDPI stays neutral socio-economic and political changes [8]. This process was particularly pronounced in with regard to jurisdictional claims in areas with considerable tourism potentials [9,10]. After recognizing the negative effects of published maps and institutional affil- abandonment on wildlife in the 1980s, the restoration of grasslands began primarily for iations. nature conservation purposes [11,12]. Lake Balaton is the largest lake in Central Europe. In surrounding areas, and on its shores, grasslands had great importance until the 1950s [13]. With the development of the bathing culture, which emerged at the beginning of the 20th century, livelihood from Copyright: © 2021 by the authors. agriculture was replaced by tourism. This led to the establishment of beaches, harbours, Licensee MDPI, Basel, Switzerland. and recreational areas in places of reed [Phragmites australis (Cav.) Trin. ex Steud.] beds This article is an open access article and grasslands. Livestock farming in coastal settlements was restricted from 1969 by distributed under the terms and law to support the expansion of tourism, thus coastal grazing was almost completely conditions of the Creative Commons abolished [14]. Attribution (CC BY) license (https:// The shore of Lake Balaton at Fenékpuszta was a rare exception to this as cattle were creativecommons.org/licenses/by/ grazing there until 1983, therefore a ~3 km long coastline remained in a close-to-nature 4.0/). Agronomy 2021, 11, 1540. https://doi.org/10.3390/agronomy11081540 https://www.mdpi.com/journal/agronomy Agronomy 2021, 11, x 2 of 12 Agronomy 2021, 11, 1540 2 of 12 The shore of Lake Balaton at Fenékpuszta was a rare exception to this as cattle were grazing there until 1983, therefore a ~3 km long coastline remained in a close-to-nature state with wet grasslands and wide reed beds connected to them. The natural value of the state with wet grasslands and wide reed beds connected to them. The natural value of area was first recognized by ornithologists and a bird-ringing station was established in the area was first recognized by ornithologists and a bird-ringing station was established the area in 1985. They also began the systematic investigation of the botanical value and in the area in 1985. They also began the systematic investigation of the botanical value began to preserve this with minor conservation treatments from 1987 [15]. The most and began to preserve this with minor conservation treatments from 1987 [15]. The most thorough management took place between 1999 and 2002, when 5–28 cattle were grazing thorough management took place between 1999 and 2002, when 5–28 cattle were grazing in in the area [16]. Detailed monitoring and documentation of the botanical value were car- the area [16]. Detailed monitoring and documentation of the botanical value were carried ried out during this period [15,17]. Later, the intensity and the extent of grazing de- out during this period [15,17]. Later, the intensity and the extent of grazing decreased and creased and became less documented, but in still ongoing to this day. became less documented, but in still ongoing to this day. Our aim was to assess the current natural condition of the area and to summarize Our aim was to assess the current natural condition of the area and to summarize the changes in habitats and the distribution of protected species occurring since 2002, in the changes in habitats and the distribution of protected species occurring since 2002, in connection with the treatments carried out after. We attempted to identify what changes connection with the treatments carried out after. We attempted to identify what changes could be detected in the vegetation and plant species distribution of the treated and un- could be detected in the vegetation and plant species distribution of the treated and treated areas after 18 years and what conditions are currently characterizing them. We untreated areas after 18 years and what conditions are currently characterizing them. We seek to demonstrate that even in an area highly affected by tourism, botanical value and seek to demonstrate that even in an area highly affected by tourism, botanical value and semi-natural habitats could be preserved in the long-term with minor treatments only. semi-natural habitats could be preserved in the long-term with minor treatments only. 2. Materials and Methods 2. Materials and Methods 2. 2.1. 1. St Study udy Are Area a The study The study ar area is loc ea is located ated on the western coast o on the western coast off L Lake ake B Balaton alaton near near the tow the town n of of Keszt Keszthely hely (H (Hungary) ungary) (F (Figur igure e 1) 1).. The e The examined xamined ar area ea is is 3 km 3 km long long and and its its wi width dth rang ranges es between 3 between 320–820 20–820m, m, coveri coveringng 13013 hectar 0 hecta es altogether res altoget . Ither. It is bo is bordered by rdered by th the stream Cs e stream ókakoi ˝ (North), by River Zala (South), by road number 71 (West), and by Lake Balaton (East). Most Csókakői (North), by River Zala (South), by road number 71 (West), and by Lake Balaton of the study area is part of the Natura 2000 site Balaton (N2K HUBF30002), which is a (East). Most of the study area is part of the Natura 2000 site Balaton (N2K HUBF30002), Special Area of Conservation and a Special Protected Area. Despite the intensive use of which is a Special Area of Conservation and a Special Protected Area. Despite the inten- Lake Balaton for touristic purposes, the shores of the lake at Fenékpuszta remained in a sive use of Lake Balaton for touristic purposes, the shores of the lake at Fenékpuszta re- relatively natural state [16]. mained in a relatively natural state [16]. Figure 1. Location of the study area. Figure 1. Location of the study area. Zentai [15] offered us a detailed description of the implementation of conservation Zentai [15] offered us a detailed description of the implementation of conserva- management tion management in Fenékpuszta be in Fenékpuszta tween between 1999 a1999 nd 200 and 2. The shore of Lake Ba 2002. The shore of Lake laton a Balaton t Fen- ékpus at Fenzétkpuszta a was a twas radita iona traditional l pasture a pastur rea fo er cent area ur for ies b centuries ut the gr but azin the g ended grazing in 1 ended 983 [17]. in 1983 [17]. After the years of abandonment, grazing was recommenced in 1999 with five cattle at the middle part of the study area. In the following years, the grazed area gradually Agronomy 2021, 11, x 3 of 12 After the years of abandonment, grazing was recommenced in 1999 with five cattle at the Agronomy 2021, 11, 1540 3 of 12 middle part of the study area. In the following years, the grazed area gradually increased, and by 2002 the total study area had become grazed with the exception of the reed beds. The size of the cattle herd reached its peak in 2001 with a total of 28 animals [16], after that, their number rapidly decreased, followed by shrinkage of the managed area increased, and by 2002 the total study area had become grazed with the exception of the and the focus of the grazing shifted to the southern parts of the area (Figure 2). In 2020, reed beds. the northern part of the area had not received treatment for at least 10 years; the central The size of the cattle herd reached its peak in 2001 with a total of 28 animals [16], part is mowed once a year and after mowing a very light after-grass grazing takes place after that, their number rapidly decreased, followed by shrinkage of the managed area and there, while the southern part has a constant presence of cattle, which trample and graze the focus of the grazing shifted to the southern parts of the area (Figure 2). In 2020, the the area all year round (Figure 2). northern part of the area had not received treatment for at least 10 years; the central part The overall size of the study area decreased by almost 6 hectares between 2002 and is mowed once a year and after mowing a very light after-grass grazing takes place there, 2020 as a result of an average 20-m retreat of the reed beds on the 3 km coastline (Table 1, while the southern part has a constant presence of cattle, which trample and graze the area F all igu year re 3r )ound . (Figure 2). (a) (b) Figure 2. Areas under conservation management (cutting and grazing) in four subsequent years from 1999 to 2002 (a) and Figure 2. Areas under conservation management (cutting and grazing) in four subsequent years from 1999 to 2002 (a) and in 2020 (b). in 2020 (b). To compa The overall re the current vegeta size of the study arti ea on decr and eased distri by bualmost tion of protected p 6 hectares between lant speci 2002 es wi and th previous 2020 as a rdat esult a, we d of anig average italized the h 20-m ra etr bit eat at an of the d protec reed ted species beds on the d 3ikm stribut coastline ion ma (T ps of able 1a, Figure 3). comprehensive study from 2002 [15] using satellite images (Google Earth) and aerial To compare the current vegetation and distribution of protected plant species with photographs (Lechner Nonprofit Ltd., Budapest, Hungary), which have become availa- previous data, we digitalized the habitat and protected species distribution maps of a ble for public use since then. comprehensive study from 2002 [15] using satellite images (Google Earth) and aerial photographs (Lechner Nonprofit Ltd., Budapest, Hungary), which have become available for public use since then. Agronomy 2021, 11, 1540 4 of 12 Table 1. Area changes of the habitat type categories between 2002 and 2020. Habitat Type Area (ha) in 2002 Area (ha) in 2020 Difference (ha) Difference (%) Reed beds 63.66 53.76 9.90 15.56 Wet meadows 14.80 12.77 2.03 13.75 Mesophilous grasslands 2.85 4.94 2.09 73.35 Wet pioneer scrubs and willow carrs 0.80 4.64 3.84 482.42 Uncharacteristic habitats 23.95 12.18 11.77 49.15 Stands of native tree species 9.78 13.85 4.07 41.66 Stands of invasive tree species 6.42 13.84 7.42 115.59 Agricultural and other antropogenic habitats 15.02 15.39 0.30 1.99 Agronomy 2021, 11, x 4 of 12 Total 137.26 131.28 5.98 4.36 (a) (b) Figure 3. Habitat category groups in 2002 (a) and 2020 (b). Figure 3. Habitat category groups in 2002 (a) and 2020 (b). Table 1. Area changes of the habitat type categories between 2002 and 2020. 2.2. Field Work Identification of the habitats was carried out during the vegetation periods of years Area (ha) in Area (ha) in Difference Habitat Type Difference (%) 2019 and 2020, which included thorough surveying of the area on land by foot and also 2002 2020 (ha) by water (with canoe). During these surveys, we collected data on protected plant species Reed beds 63.66 53.76 −9.90 −15.56 by recording GPS coordinates on each occurrence and counting individuals, or in the case Wet meadows 14.80 12.77 −2.03 −13.75 of clonal species, such as Acorus calamus L. and Nymphaea alba L., we estimated the area Mesophilous grasslands 2.85 4.94 2.09 73.35 occupied by each population. The extension and the way of the current management were Wet pioneer scrubs and willow carrs 0.80 4.64 3.84 482.42 also mapped during the fieldwork (Figure 2). In 2020, on the southern part of the area, 20 Uncharacteristic habitats 23.95 12.18 −11.77 −49.15 cattle were grazing, and the northern part of the area was cut once a year during summer. Stands of native tree species 9.78 13.85 4.07 41.66 The grazing usually started in late April and ended in October. Stands of invasive tree species 6.42 13.84 7.42 115.59 Agricultural and other antropogenic habitats 15.02 15.39 0.30 1.99 Total 137.26 131.28 −5.98 −4.36 2.2. Field Work Identification of the habitats was carried out during the vegetation periods of years 2019 and 2020, which included thorough surveying of the area on land by foot and also by water (with canoe). During these surveys, we collected data on protected plant species by recording GPS coordinates on each occurrence and counting individuals, or in the case of clonal species, such as Acorus calamus L. and Nymphaea alba L., we estimated the area occupied by each population. The extension and the way of the current management were also mapped during the fieldwork (Figure 2). In 2020, on the southern part of the Agronomy 2021, 11, 1540 5 of 12 2.3. Protected Species Most protected species in the study area are characteristic to sedge- and reed commu- nities. These habitats, although relatively common along the shoreline of Lake Balaton, are mostly in a poor condition and lacking rare species. In 2002, an overall 23 species were recorded in the study area which are protected by law. Among these species, only Cirsium brachycephalum Jur. is on the 1992 Habitats Directive Annex II list. In 2020, the number of protected species were decreased to 17, most of which belonged to the family Orchidaceae. Among the protected species, some have greater local importance, like Hydrocotyle vulgaris L., as almost all of its occurrences in Hungary are limited to the shoreline of Lake Balaton. Samolus valerandi L., Urtica kioviensis Rogow., and Acorus calamus have considerable portions of their total national population occurring near Lake Balaton as well. Other species, such as Ranunculus lingua L. and Equisetum variegatum Schleich., are rare and very sporadic across the country, therefore their occurrences at Fenékpuszta have regional importance. 2.4. Data Processing First, we classified the vegetation data (habitat descriptions of [15] and the current field data as well) into habitat classes, based on the species pool and structure according to the General National Habitat Classification System of Hungary (Á-NÉR) [18]. Then, we merged the similar classes to the generalized habitat categories for better visualization (Table 1). We also plotted the recorded data of the protected plant species occurrences and areas affected by management, according to [15] and current data as well. 3. Results 3.1. Changes in Habitats and Vegetation Reed beds were that habitat type category which area decreased the most among the categories. This is caused by the die-back from the direction of the open water men- tioned earlier, and to a lesser extent by the area loss caused by shrub encroachment and afforestation on land (Table 2). Table 2. Habitat categories of Á-NÉR occurring in the area and our categorization of them. Generalized Habitat Category Á-NÉR/Natura Habitat Category Reed beds Eu- and mesotrophic reed and Typha beds (B1a) Tussock sedge communities (B4) Non-tussock tall-sedge beds (B5) Wet meadows Rich fens (D1)/7230 Alkaline fens Mesotrophic wet meadows (D34)/ Alluvial meadows of river valleys of the Cnidion dubii (6440) Mesophilous meadows Arrhenatherum hay meadows (E1) Willow carrs (J1a)/Alluvial forests with Alnus glutinosa and Fraxinus Wet pioneer scrubs and willow carrs excelsior (91E0) Wet and mesic pioneer scrub (P2a) Uncharacteristic wetlands (OA) Uncharacteristic mesic grasslands (OB) Uncharacteristic habitats Uncharacteristic dry and semi-dry grasslands (OC) Stands of invasive forbs (OD) Scattered native trees or narrow tree lines (RA) Stands of native tree species Uncharacteristic or pioneer softwood forests (RB) Stands of invasive tree species Spontaneous stands of non-native tree species (S6) Annual intensive arable fields (T1) Agricultural and other anthropogenic habitats Farms (U10) Roads and railroads (U11) Agronomy 2021, 11, 1540 6 of 12 A noticeable decrease in the overall area (13%) of the wet meadows was also detected (Table 2, Figure 3). The northern part of the study area where the grazing was abandoned on the wet meadows in 2002, had become densely covered by invasive tree species and by native tree and shrub species by 2020 (Figure 4). The highest situated part of the wet meadows, where the grazing management is still ongoing became the mesophilous Agronomy 2021, 11, x 7 of 12 meadows with the dominance of Arrhenatherum elatius (L.) and Helictotrichon pubescens (Huds.). Figure 4. Transitions between habitat category groups in hectares and in percentage of the former Figure 4. Transitions between habitat category groups in hectares and in percentage of the former area of the original habitat category group. area of the original habitat category group. The advance of woody stands (of both invasive and native species) is also noticeable in Other species retained their populations to roughly the same extent and number. the whole area. These habitats had the largest increase in their total area, currently covering Populations of Cicuta virosa L. and Allium carinatum L. had not changed substantially, not more than twice their former area described by an earlier study [15]. Unfortunately, these in location, nor in the number of individuals. The situation is similar in the case of two stands are mostly dominated by invasive alien tree species, such as Robinia pseudoacacia orchid species, Ophrys sphegodes Mill. and Neottia ovata (L.) Bluff and Fingerh. L. and Fraxinus pennsylvanica Marshall, whereas the most common native tree species in Some species significantly increased in the number of individuals. Former localities the study area, Populus spp. and Salix alba L., are present sporadically in these forests or of Cephalanthera longifolia (L.) Fritsch are still present in the northern part, and the species forming small groves. appeared in the southern area as well. We recorded new occurrences of Neottia ovata in the northern area beside the large population in the southern part. The former single small population of Samolus valerandi in the northern area went extinct, but the species had appeared in several locations in the southern wet meadows area, mostly on the edges of the grazed area. Agronomy 2021, 11, 1540 7 of 12 3.2. Presence and Distribution of the Protected Species During the 2002 survey, 23 different protected plant species were described from the area. In the year 2020, we found 17 protected plant species (Table 3), from which four species [Epipactis tallosii A. Molnár and Robatsch, Cephalanthera damasonium (Mill.) Druce, Equisetum variegatum, Neottia nidus-avis (L.) Rich] were not described previously from the area (Figure 5). Some of the disappeared species were present earlier only by a few individuals: Anacamptis coriophora (L.) R.M. Bateman, Pridgeon and M.W. Chase, Botrychium lunaria (L.) Sw., Carex paniculata L., Cirsium brachycephalum, Epipactis helleborine (L.) Crantz, Spiranthes spiralis (L.) Chevall., but in other cases, considerable populations vanished or we were not able to find them: Anacamptis morio (L.) R.M. Bateman, Pridgeon and M.W. Chase, Epipactis palustris (L.) Crantz, Hydrocotyle vulgaris, Schoenus nigricans L., Urtica kioviensis. The majority of the newly appeared species, like Epipactis tallosii, Cephalanthera damaso- nium, and Neottia nidus-avis, were found with a few individuals under native tree stands. Substantial populations of Equisetum variegatum were observed in the southern wet meadow area which is currently grazed. The 13 species which were observed in the area during both surveys had some changes in their distribution as well. Table 3. The number of localities and individuals of protected plant species in 2002 and 2020. Number of Localities Number of Individuals Species 2002 2020 2002 2020 2 2 Acorus calamus many 18 ~1500 m ~900 m Allium carinatum 1 1 50–80 45 Anacamptis coriophora 1 – 7 – Anacamptis morio 1 – 107 – Anacamptis palustris 2 1 120–140 10 Botrychium lunaria 1 – 2 – Carex paniculata 1 – 3–5 – Cephalanthera – 2 – 5 damasonium Cephalanthera longifolia 3 5 6 10 Cicuta virosa several 10 few hundred ~100 Cirsium brachycephalum 1 – 10 – Dactylorhiza incarnata several 7 400–450 16 Epipactis helleborine 1 – 2 – Epipactis palustris few – 210–250 – Epipactis tallosii – 5 – 37 Equisetum variegatum – 8 – 16 m Hydrocotyle vulgaris 1 – 50 m – Neottia nidus-avis – 4 – 9 Neottia ovata 3 12 1000–2000 1536 2 2 Nymphaea alba 2 2 500 m ~40 m Ophrys sphegodes 1 1 120 150 Orchis militaris 4 9 250–350 112 Ranunculus lingua 4 1 110–165 1 Samolus valerandi 1 9 16 10–15 m Schoenus nigricans – – – ~200 m Spiranthes spiralis 1 – 1 – Trapa natans 2 1 ~200 m Urtica kioviensis several – few hundred – Agronomy 2021, 11, 1540 8 of 12 Agronomy 2021, 11, x 8 of 12 (a) (b) Figure 5. Habitat category groups in 2002 (a) and 2020 (b). Figure 5. Habitat category groups in 2002 (a) and 2020 (b). Table 3. Ther The e ar nu ember of local species in which ities and in populations dividuals of declined protected considerably plant species in . Acorus 2002 and calamus 2020. disap- peared from the northern area and also from most of its former localities in the southern Number of Localities Number of Individuals area. In 2020, its single large population was located on the grazed wet meadows on Species 2002 2020 2002 2020 the southern part. Large colonies of Nymphaea alba were considerably reduced in their 2 2 Acorus calamus many 18 ~1500 m ~900 m extent. Ranunculus lingua almost disappeared, and in the last vegetation period only one Allium carinatum 1 1 50–80 45 flowering plant was seen. Among the orchids, populations of Anacamptis palustris (Jacq.) Anacamptis coriophora 1 – 7 – R.M. Bateman, Pridgeon and M.W. Chase and Dactylorhiza incarnata (L.) Soó suffered the greatest reduction in size, both represented by only 10–20 flowering plants in the area. Anacamptis morio 1 – 107 – Reduction in the number of individuals was also apparent in the case of Orchis militaris L., Anacamptis palustris 2 1 120–140 10 its population has decreased to the third of its former size. Botrychium lunaria 1 – 2 – Other species retained their populations to roughly the same extent and number. Carex paniculata 1 – 3–5 – Populations of Cicuta virosa L. and Allium carinatum L. had not changed substantially, not Cephalanthera damasonium – 2 – 5 in location, nor in the number of individuals. The situation is similar in the case of two Cephalanthera longifolia 3 5 6 10 orchid species, Ophrys sphegodes Mill. and Neottia ovata (L.) Bluff and Fingerh. Cicuta virosa several 10 few hundred ~100 Some species significantly increased in the number of individuals. Former localities Cirsium brachycephalum 1 – 10 – of Cephalanthera longifolia (L.) Fritsch are still present in the northern part, and the species Dactylorhiza incarnata several 7 400–450 16 appeared in the southern area as well. We recorded new occurrences of Neottia ovata in Epipactis helleborine 1 – 2 – the northern area beside the large population in the southern part. The former single Epipactis palustris few – 210–250 – small population of Samolus valerandi in the northern area went extinct, but the species had Epipactis tallosii – 5 – 37 appeared in several locations in the southern wet meadows area, mostly on the edges of Equisetu the grazed m var area. iegatum – 8 – 16 m Hydrocotyle vulgaris 1 – 50 m – Neottia nidus-avis – 4 – 9 Neottia ovata 3 12 1000–2000 1536 Agronomy 2021, 11, 1540 9 of 12 4. Discussion The dieback of the reed beds—which refers to an average 20 m retreat in our case—is a well-known and general problem at Lake Balaton [19]. Although the reeds spread over many other habitats along the coast, these stands cannot be recognized as autochthonous reed beds, as they do not have the species pool, nor the structure characteristic of such stands, and remnants of the original habitat are still present under the newly formed reed cover. As a result, the overall decrease in the size of the reed bed is even greater than the retreat from the direction of the open water, which equals 9.9 hectares. In the northern areas, a short period of grazing (1999–2003) opened up the structure to the vegetation resulting in a relatively large area of continuous wet meadows [15]. The loss of that habitat type after the abandonment is a consequence of intensive scrubbing and the advance of invasive species [20]. These wet meadows corresponded to the Natura 2000 habitat category ‘6440 Alluvial meadows of river valleys of the Cnidion dubii’, which also indicates that it is a particularly valuable habitat type. Wet meadows are also threatened by drought in connection with climate change, and large areas of this habitat type turning into mesophilous meadows at the highest situated areas. Despite the rise in the water level of Lake Balaton after 2016, we did not experience this transformation in the opposite direction between these habitat category groups, and the number of helo- and hydrophytes have been reduced, to which the abandonment of management may have synergetic contributions. On the other hand, grazing is still actively going on in the southern part, which has allowed the transformation of formerly degraded, uncharacteristic habitats to valuable meadows like other areas of Pannonian vegetation [21]. In the central areas due to the targeted conservation management (which is optimized to maintain the population of Ophrys sphegodes) this area has remained relatively intact. Seven species, Acorus calamus, Schoenus nigricans, Anacamptis palustris, Hydrocotyle vulgaris, Anacamptis coriophora, Epipactis palustris, and Cirsium brachycephalum have all disappeared from the northern parts in connection with the degradation of the former wet meadows. From all the protected species occurring in the area, only several orchid species are still present in the northern part, as these species can survive for a long time even in unfavorable circumstances [22,23], but their numbers have also decreased significantly. Although the effect of the water level rise at Lake Balaton was not perceptible in the meadows, it is possible that the high water level was the reason why we were unable to reach the former localities of Carex paniculata and Urtica kioviensis at the reed beds [19]. Species connected to forest habitats, like Cephalanthera damasonium and Neottia nidus- avis, appeared in the northern part, most likely because of the spontaneous afforestation of the initial habitats. As one of the new Epipactis tallosii occurrences is close to the position of the single former Epipactis helleborine locality, and we could not find the latter species in the area, we suppose that this new taxon for the area is just a result of a recent change in taxonomy. Epipactis tallosii was described in 1997 [24], and by the turn of the millennium, almost all individuals of E. tallosii have still been identified as E. helleborine. At the central part of the study area, a major proportion of the mesophilic mead- ows were afforested by invasive tree species, which finally led to the disappearance of Botrychium lunaria, Anacamptis morio, and Spiranthes spiralis. On the actively grazed field of the southern part, we detected some areas covered by Equisetum variegatum, which this species had not been reported earlier from the area. We suspect that this was only an overlooking as it is a very small and inconspicuous plant. The number of individuals of Samolus valerandi has increased significantly and its occurrences have shifted from the northern parts to the southern region. This species clearly found its living conditions as a result of grazing, typically below the electric fence on the edges of grazed areas. In 2020, most former patches of Acorus calamus had already disappeared in the whole area, but a new one appeared in the currently grazed area. Cattle typically do not con- Agronomy 2021, 11, 1540 10 of 12 sume this species, so it can spread over actively grazed areas. On the western part, the sizeable patch of Neottia ovata and the population of Orchis militaris are also surviving and their numbers remained roughly the same, despite some of their occurrences outside the managed area. Overall, our results show that in contrast with the northern part, where the con- servational management almost entirely ceased, and many protected species that have disappeared, the southern grazed part offered suitable habitat for them. 5. Conclusions Our results confirm the results of previous research on wet grasslands in which a complete lack of treatments can lead to habitat depopulation and species decline or even complete extinction [20,25], but according to previous studies, this process might be reversible [2,26]. Therefore, we need to strive for maintaining some appropriate treatment in as large of an area as possible, preferably by grazing, which can be replaced with mowing on areas where grazing is not feasible. This could prevent the loss of biodiversity by maintaining the species pool and preventing the advance of invasive alien species. The conservation of ecologically valuable coastal reeds must also be given serious emphasis, as their decline in the long-term could mean a serious threat to the ecological status of the lake and even to its use for tourism [19,27]. The shore of Lake Balaton in Fenékpuszta is a good example of the fact that high species richness can occur even in an area that is currently primarily used for touristic purposes. Fortunately, near our sample area, there are other high-diversity habitat patches over the other side of River Zala. We should ensure their permanent connection in order to provide better chances for species to survive. These habitats serve as ecological corridors to larger natural habitats, namely to the Kis-Balaton [28]. Even in development plans determining utilization of the study area, the primary goal should be the preservation of biodiversity. The coast of Lake Balaton at Fenékpuszta could be a great target for eco-tourism and can play an important role in environmental education as well, which has a long tradition in the area [29,30]. It is also worth considering organizing botanical trips besides the bird-ringing programs, but we must not forget to continue the extensive use of the grassland, which can be well aligned with the basic goals of the establishment of the Natura 2000 network. We would also suggest that in the future the overall area of treatments should be increased at least to their previous largest extent (in 2002). Author Contributions: Conceptualization, B.F., J.B. and B.P.; investigation, B.F. and B.P.; resources, B.F. and J.B.; data curation, B.P.; writing—original draft preparation, B.F. and J.B.; writing—review and editing, B.F. and B.P.; visualization, B.P.; supervision, J.B.; project administration, B.F. and J.B.; funding acquisition, J.B. and B.F. All authors have read and agreed to the published version of the manuscript. Funding: The publication is supported by the EFOP-3.6.3-VEKOP-16-2017-00008 project. The project is co-financed by the European Union and the European Social Fund. Institutional Review Board Statement: Not applicable. Informed Consent Statement: Not applicable. Data Availability Statement: Data presented in this study are available on request from the corre- sponding author. Acknowledgments: The article is dedicated to the memory of Sándor Palkó (1959–2002), who discovered the natural value of Fenékpuszta and became a committed protector of this area, which he loved very much. The authors are thankful to Kinga Zentai for the detailed descriptions, to Anikó Benke and Szabolcs Benke for their valuable help in the field, and as well as to Zoltán Botta-Dukát for suggestions to the earlier version of the manuscript. Agronomy 2021, 11, 1540 11 of 12 Conflicts of Interest: The authors declare no conflict of interest. The funders had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or in the decision to publish the results. References 1. Carboni, M.; Dengler, J.; Mantilla-Contreras, J.; Venn, S.; Török, P. Conservation Value, Management and Restoration of Europe’s Semi-Natural Open Landscapes. Hacquetia 2015, 14, 5–17. [CrossRef] 2. Török, P.; Penksza, K.; Tóth, E.; Kelemen, A.; Sonkoly, J.; Tóthmérész, B. Vegetation type and grazing intensity jointly shape grasing on grassland biodiversity. Ecol. Evol. 2018, 8, 10326–10335. [CrossRef] 3. Penksza, K.; Csík, A.; Filep, A.F.; Saláta, D.; Pápay, G.; Kovács, L.; Varga, K.; Pauk, J.; Lantos, C.; Lisztes-Szabó, Z. Possibilities of Speciation in the Central Sandy Steppe, Woody Steppe Area of the Carpathian Basin through the Example of Festuca Taxa. Forests 2020, 11, 1325. 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Journal

Agronomy – Multidisciplinary Digital Publishing Institute

Published: Jul 31, 2021

Keywords: nature conservation; grassland management; habitat loss; semi-natural habitats; reed bed

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