Next Article in Journal
Tissue-Specific Responses of Cereals to Two Fusarium Diseases and Effects of Plant Height and Drought Stress on Their Susceptibility
Previous Article in Journal
Short-Term Responses of Soil Organic Carbon Pool and Crop Performance to Different Fertilizer Applications
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Agronomy
Volume 12
Issue 5
10.3390/agronomy12051107
agronomy-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Effects of Long-Term Mowing on Biomass Composition in Pannonian Dry Grasslands

by
Judit Házi
1,
Károly Penksza
2,
András Barczi
3,*,
Szilárd Szentes
4 and
Gergely Pápay
2
1
Department of Botany, University of Veterinary Medicine Budapest, Rottenbiller utca 50, H-1077 Budapest, Hungary
2
Department of Botany, Hungarian University of Agriculture and Life Sciences, Páter Károly utca 1, H-2100 Gödöllő, Hungary
3
Institute of Environmental Studies, Hungarian University of Agriculture and Life Sciences, Páter Károly utca 1, H-2100 Gödöllő, Hungary
4
Institute of Animal Sciences, Hungarian University of Agriculture and Life Sciences, Páter Károly utca 1, H-2100 Gödöllő, Hungary
*
Author to whom correspondence should be addressed.
Agronomy 2022, 12(5), 1107; https://doi.org/10.3390/agronomy12051107
Submission received: 12 April 2022 / Revised: 23 April 2022 / Accepted: 28 April 2022 / Published: 1 May 2022
(This article belongs to the Section Grassland and Pasture Science)
Browse Figures
Versions Notes

Abstract

:
This study is focused on the vegetation of seminatural dry grasslands. These grasslands are valuable with large biodiversity; however, their long-term preservation requires regular conservation management. This report demonstrates the results of a 13-years mowing experiment, designed to suppress the spread of an unpalatable grass species, Calamagrostis epigejos. The study site was located in mid-successional grasslands, in the Western-Cserhát, near Rád, Northern Hungary. The experimental design consisted of eight permanent plots, where mowing was applied twice a year. The vegetation was sampled annually (from 2001 to 2013). The impacts of mowing were tested using repeated–measures analyses of variance (ANOVA). In 2001, Calamagrostis epigejos was the species with the highest cover in both the mown and control sites, with an average cover value of 63%. However, as a result of mowing, a significant difference was detected in the amount of litter and legumes species as well. The number of species showed an increase in both types of treatment, from 15 to 37 in the mowed plots, but also from 18 to 27 in the control plots. We concluded that mowing twice a year proved to be a useful measure for modifying botanical composition of a grassland. It was well suited for agricultural usage, in particular grazing, which can replace the expensive and time-consuming scythe. Mowing can also be a suitable management measure for controlling native invader species such as Calamagrostis epigejos, and can significantly increase the proportion of species with higher forage values.

1. Introduction

The population of livestock has dramatically decreased in the Carpathian Basin in the last few decades [1] resulting in an increased shrub layer, and an aggressive spread of grass species such as Calamagrostis epigejos [2,3,4,5].
It is a tall-growing, unpalatable grass that is not grazed by livestock. Grasslands are often invaded by this native grass species; therefore those territories are not suitable for pasture management, and those abandoned sites or secondary grasslands are often degraded [6,7].
This is one reason for the high conservation value of such grasslands and grassland fragments. These special habitats also preserve valuable relic and endemic plant species. Therefore, the protection and preservation of these grassland patches and fragments is crucial. A suitable nature conservation management plan is also essential.
Regular, but low intensity grazing and mowing can support the maintenance of grassland ecosystems [8,9]. Suitable management can prevent dominance of invasive plant species, regardless of native or non-native species. Moderate grazing pressure can provide constant low levels of disturbance, which is necessary to prevent tree growth and preserve high species diversity.
Calamagrostis epigejos is able to settle spontaneously on waste and remediated areas and to grow and develop on sand with high pH and high calcium contents and stabilize extremely poor habitats. These species are part of Northern European crop wild relatives (CWR) and include Calamagrostis epigejos [10].
Recent changes involve land-use intensification and abandonment, and these processes are often accompanied by diversity loss in semi-natural habitats [11,12,13]. Grassland biodiversity is threatened by the collapse of extensive animal husbandry. Decreasing biodiversity due to the aggressive expansion of grasses into grasslands has been reported from various parts of Europe [14,15,16].
Calamagrostis epigejos (L.) Roth is a tall perennial clonal grass [17] and a decent example of a species that spreads successfully to man-made areas [18]. Calamagrostis epigejos has a broad distribution range in Europe. It occurs in natural grasslands [19], in forests [20,21], in river floodplains [22], and ruderal assemblages [23,24].
This species can survive in dry and nutrient-poor environments, despite the fact, that it is most successful in open, nutrient-rich, mesic habitats [25].
The competitive success of Calamagrostis epigejos is related to its high tiller density and branching frequency, as well as to its capacity for clonal spreading.
These traits allow a rapid spread of these species, by the expansion of circular clonal tussocks, which often form nearly mono-dominant stands.
Calamagrostis epigejos potentially forms monodominant patches and is able to reduce species richness considerably [19]. Frequent mowing was suggested as a potential management measure for repressing tall herbs or clonal grasses and for maintaining or improving grassland biodiversity [26,27,28]. Successful control of Calagamrostis epigejos by mowing was reported from the first five years of vegetation succession on a species-poor ruderal landfill site from Germany by Rebele and Lehmann [29]. However, there is no data available from other habitats, especially from secondary grasslands. Regular biomass removal was suggested as a potential management method for improving and maintaining grassland biodiversity [28]. Other possibilities include grazing and burning [30]. This study’s aim was to examine the effect of multi-annual mowing and litter removal on recovery of coenological composition of a Calamagrostis epigejos invaded grassland, and to introduce regular mowing to change the sward composition gradually and make it suitable for future grazing [31,32,33,34].
Furthermore, the study aims to investigate the following: Can the unpalatable Calamagrostis epigejos be suppressed by mowing? Are there possibilities to increase the diversity of sward by this? How can we change the proportion of important species from a grassland management point of view?
Our study aims, to measure potential value increasing effects of mowing, and to determine the carrying capacity aspect for grassland management.

2. Materials and Methods

2.1. Study Site

The study site was located in the Cserhát hills near by Vácduka and Rád, ca. 50 km from Budapest, Northern Hungary. The site is a typical extensively managed rural landscape. The climate is temperate with annual precipitation of 520–590 mm and 8–10 °C annual temperature [35]. The whole area is covered by a variable thickness of loess formed during the ice age. From this loess blanket, parallel ridges emerge such as Bükkös hill (190 m above sea level).
The study area is located on the north-facing slope (3.3 ha) of the Bükkös hill. Center coordinates are: 47°45′58.87″ N, 19°12′51.57″ E.
The field experiment was conducted from 2001 until 2011 on a secondary dry grassland of the Salvio-Festucetum rupicolae plant community.
The area was originally covered by the forest component of the Pannonian forest-steppe zone. For centuries, this hilly landscape was a mosaic of small vineyards, orchards, and croplands, with scattered patches of woods and steppes. Land use has often changed due to wars and changing economic conditions. Therefore, abandoned fields and the related secondary succession is well known in this area and species adapted to challenging successional stages are a part of the regional species pool.

2.2. Sampling

We carried out stratified random sampling. The shrub and Robinia pseudoacacia dominated patches were omitted, and patches with low cover of Calamagrostis epigejos (less than 60%) were also disregarded. The remaining Calamagrostis epigejos dominated patches were very abundant at the beginning of the study. The diameter of these monodominant patches was larger than 20 m. We established eight pairs of 3 × 3 m large permanent plots, positioned randomly along the north slope and arranged in a split-plot design of mown and control plots. The field experiment was conducted from 2001 to 2013, with mowing twice a year; in June and in September. Vegetation data were monitored in 2 × 2 m large permanent quadrats placed in the middle of each 3 × 3 m large plot, i.e., there was a 1 m buffer zone between the paired (mown and control, Figure 1 and Figure 2) quadrats. The cover of each vascular species was estimated visually.
Biomass investigations were applied in June and in September annually. Parallel with coenological recordings, a 2 × 2 m grassland plot was trimmed by a trimmer leaving 4 cm high stubble to model the grazing-effect of sheep.
Sampling was taken from the middle 1 × 1 m part. Sampled biomass was sorted according to important groups for grazing.
Values and notations of grassland management categories were used as follows [36].
  • Dominant Poaceae species ie: Calamagrostis epigejos
  • Subordinate Poaceae species important for grassland management
  • Fabaceae species important for grassland management
  • Dicotyledonous species neutral for grassland management
  • Stinger plants
Dry biomass values of each grassland management category were calculated from the total coverage percentage per mass ratio of each grassland management category, ie.: Calamagrostis epigejos, other grasses, Fabaceae species, other dicots, unpalatable thorny species, and litter.
The forage values of various lawns were calculated by the following formula [36,37]:
FV = ((a × A + b × B + c × C…)/100) × x
FV: Forage value of the lawn
a, b, c…: categories of forage values of species
A, B, C…: coverage of species
x: total coverage of species
Forage values of each plant species can be explained by the following: −1 is poisonous, 0 is not grazed by animals, and 1 to 8 are ever more valuable respectively, by means of protein and mineral content, palatability, time-scale of palatability, usability, harvestability, harmfulness and ideal proportion in the association.
The grassland production was estimated by Balázs-method [38,39] using the following formula:
P = ((M − s) × BM × b)/100
P: yield [Kg/ha]
M: grass height [cm]
s: stubble height [cm]
BM: grass 400 [kg/ha]; alfalfa 470 [kg/ha]
b: coverage% [%]
After measuring the average grass height and the total coverage, the annual yield and the animal capacity of the grasslands were estimated. The following data were taken into account: 60 kg/day dry weight and 210-day grazing season for cattle, 7 kg/day dry weight and 210-day grazing season for sheep, 80 kg/day dry weight and 180-day grazing season for horses.

2.3. Data Analysis

Floristical and coenological changes, such as the changes of species number and cover percentage of dominant taxa were analyzed using Shannon diversity [40]. Based on that, the effects of mowing could be tested using repeated–measures analyses of variance (ANOVA). For the post-hoc test, the Tukey HSD was applied. Data were analyzed by the R-statistical program [41]. PAST software was used.

3. Results

Composition of the grassland based on percent distribution of main components demonstrated detectable variance between mown and control plots.
As a result of 13 years of mowing, the native invader Calamagrostis epigeios has significantly decreased (Figure 3). Additionally, as a result of mowing the proportion of other grass species in the foothill region increased, Arrhenatherum elatius occurs, and in the open grassland territories are narrow-leaved Festuca species (Festuca rupicola).
There are also positive effects on the grassland management aspect, in that cover of Fabaceae species increased too (Lathyrus tuberosus, Dorycniumherbaceum).
In the mown plots, among grassland management categories, the rate of Legumes or Fabaceae species was the highest, showing constant growth in coverage. (Figure 4)
There were significant changes in Fabaceae species; p = 0.019 * p = 0.00014. Even changes in 2013 are significant: p = 0.0096. Changes in other grassland species biomass p = 0.0011.
Although, based on species composition, the forage value of the grassland has also increased during the years of the study. Legumes, which are the most important from the point of view of grassland management, grew the most in plots four and five, and resulted mainly from the proliferation of Dorycnium herbaceum and Chamaecytisus austriacus. There was no significant difference in the cover of other herbs between the samples, however, the species composition is heavily varied.

3.1. Cover of Calamagrostis epigejos

At the initial phase of the experiment (in May 2001) Calamagrostis epigejos was the dominant component of the selected patches of sward with an average cover in mown plots of 56.63%, and 57.12% in control plots. There were no significant differences here. In the autumn of 2001, after the first cutting, the average cover in mown plots was 33.12%, and 61.25% in control plots. This result showed a significant difference (paired t-test p = 0.00025).
From that point, the spring and autumn data of the given year were evaluated together, based on the higher cover value for each species.
As a result of repeated measures ANOVA there are visible differences between mown and control plots in the second year, however only the fourth year shows detectable differences. In 2004 there is also a huge difference between mown and control plots and this phenomenon lasted till 2007. From 2008 to 2010 there are no differences, both treatment plots are quite similar (Figure 3).
Mowing twice annually was effective in decreasing the cover of Calamagrostis epigejos (Figure 5). The results of the repeated–measures analyses of variance showed that the treatment significantly affected the cover of Calamagrostis epigejos. At the beginning of the experiment Calamagrostis epigejos was dominant in all plots with ca. 60% coverage. The average cover was 56.63% in the mown plots and 63.75% in the control plots on the Bükkös hill.
In contrast, with the starting year (2001), the first significant difference in the mowed plots appears in the third year and lasts until the end of the study. While in the control plots a significant difference appears in 2003, it then disappears and reappears only in 2007. In the following years, this difference remained.
A decade later in 2011 the coverage of Calamagrostis epigejos decreased significantly, from an initial 56.63% average cover to 5.63% in the mown plots. Surprisingly in the control plots, a similar decrease is observed.
In the control plots from an initial 63.75% average cover there was also a decrease to 33.88%. The total cover of all species remains, consequently, the relative cover of Calamagrostis epigejos also decreased to approx 10% (Table 1.)
The characteristic data of the grassland on the north-facing slopes of Bükkös-hill demonstrates that Shannon Diversity indices also show a steady increase in mown plots.
Both species number and total coverage confirm significant increases in the grassland with regular mowing.

3.2. Cover of Other/Subordinate Species

In parallel with the suppression of the dominant species, advance of subordinate species can be observed.
An interesting phenomenon is detectable here, if we focus on the absolute values; a significant increase in the cover of other species can be observed in the control. It happened mainly due to the progress of shrub encroachment. On the other hand, if we focus on the relative cover change divided by the total cover, it turns out that the subordinated species were more strengthened in the mown plots.

3.3. Species Rank Changes

At the beginning of the survey in 2001, the most abundant species was Calamagrostis epigejos with the highest cover out of the two treatment types, with an average cover value of 63%. As a result of mowing, a significant difference was detected in the third year compared to the control squares. 13 years later, it ranks third in mowed plots with an average coverage of 6%, while in the control plots the rank does not change.
The second-largest cover species in the mowed quadrats was Festuca rupicola, which became dominant ten years later and accounted for half of the total coverage. This is followed by Dorycnium herbaceum and Galium mollugo, which also plays a role as a fodder plant with a significant cover of Legumes (Figure 4). The results showed higher forage values in the managed plots.
The sample areas show an increase based on Klapp’s forage value and cover values, and the yield and holding capacity also show an increase in the total cover area in the mowed sample areas. Furthermore, both control and mown grasslands had higher forage values in mown squares at all three study time points (Table 2). Annual estimated hay yield in the control areas: 8.2; 8.4; 8.8 t/ha with an animal husbandry capacity of 6–7 sheep/ha. In contrast, the amount of annual hay–estimated on the basis of mown patches–is significantly higher than the control areas: 10.4; 12.4; 14.8 t/ha, with an animal husbandry capacity of 7.5–10 sheep/ha.

4. Discussion

Analyzing ten years of data, phytocoenological results and biomass samples, our results showed that a decrease in native invader species was associated with positive changes of grassland diversity. However, we did not find a rapid answer, for reliable results we need long-term regular management [42]. In contrast to our expectation, there is also a decrease in the control plots, in connection to the relative cover and absolute cover of Calamagrostis epigejos.
Based on species composition, the forage value of the grassland has increased during the observed years, parallel to the dominant grass species decreasing.
Changes in the vegetation of the grassland were strictly determined by moderate disturbance and there is a strict connection with the improvement of habitats [43].
In our experiment, mowing twice a year was effective in decreasing the cover of C. epigejos, but the significant decrease appeared only in the fourth year. A similar two-year lag effect was reported by Rebele and Lehmann [29] from another habitat. The slow decrease can be attributed to the accumulated nutrient reserves in the rhizomes of this species [12,44,45]. Calamagrostis epigejos lost a high amount of its biomass due to the frequent cutting [44]. The fact that Calamagrostis epigejos’ cover also decreased in the control plots can be explained by the natural succession of the grassland [42]. Our results suggest that mowing twice a year is probably enough to exhaust the storage organs and to produce a negative nutrient budget for this species. Most studies found that mowing increased species richness in abandoned grasslands [46]. In our study, mowing also increased species richness, diversity, species composition, and the ability for forage supply in secondary dry grasslands.
Long-term and comprehensive botanical investigations are required, because biodiversity, ratio and absolute quantity of beneficial, harmful and other species defines nature conservation values, and grasslands management values and nutrient content of meadows and pastures [7,47].

5. Conclusions

We conclude that the ten-year study was long enough, as a difference was detected after an eight-year time scale. Mowing has significantly increased the density of Calamagrostis, the species richness, and diversity in the course of secondary succession. Therefore, mowing twice a year proved to be a successful management measure for controlling Calamagrostis epigejos, and for obtaining a sward composition.
The treatment was effective in restoring grassland composition, although the achievement and maintenance of a favorable conservation status for the grassland habitat requires long-term management planning and regular treatment. According to the objectives, mowing not only promotes the control of the invasive species, but also the economic utilization of the area.

Author Contributions

Conceptualization, J.H. methodology, J.H.; software, G.P.; validation, J.H.; formal analysis, J.H.; investigation, J.H.; resources, J.H.; data curation, J.H.; writing—original draft preparation, J.H.; writing—review and editing, G.P., A.B., S.S.; visualization, G.P.; supervision, G.P. and K.P.; project administration, G.P.; funding acquisition, K.P.; English conceptualization, A.B. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by OTKA K-125423.

Data Availability Statement

Not applicable.

Acknowledgments

Thanks for OTKA K-125423 for making this survey possible.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Török, P.; Penksza, K.; Tóth, E.; Kelemen, A.; Sonkoly, J.; Tóthmérész, B. Vegetation type and grazing intensity jointly shape grazing on grassland biodiversity. Ecol. Evol. 2018, 8, 10326–10335. [Google Scholar] [CrossRef]
  2. Schuhmacher, O.; Dengler, J. Das Land-Reitgras als Problemart auf Trockenrasen Handlungsempfehlungen zur Reduktion von Calamagrostis epigejos; Ergebnisse aus einem Praxisversuch; NABU: Hamburg, Germany, 2013; pp. 10–15. [Google Scholar]
  3. Březina, S.; Koubek, T.; Münzbergová, Z.; Herbena, T. Ecological benefits of integration of Calamagrostis epigejos ramets under field conditions. Stanislav. Flora 2006, 201, 461–467. [Google Scholar] [CrossRef]
  4. Oborny, B.; Kun, A.; Czárán, T.; Bokros, S. The effect of clonal integration on plant competition for mosaic habitat space. Ecology 2000, 81, 3291–3304. [Google Scholar] [CrossRef]
  5. Zhe-fu, Y.; Shuang, S.; Xiao-lu, X.; Qing, M.; Yin, L. Sources, migration, accumulation and influence of microplastics in terrestrial plant communities. Environ. Exp. Bot. 2021, 192, 104635. [Google Scholar]
  6. Saul, W.C.; Roy, H.E.; Booy, O.; Carnevali, L.; Chen, H.J.; Genovesi, P.; Harrower, C.A.; Hulme, P.E.; Pagad, S.; Pergl, J.; et al. Assessing patterns in introduction pathways of alien species by linking major invasion databases. J. Appl. Ecol. 2017, 54, 657–669. [Google Scholar] [CrossRef]
  7. Tasi, J. Diverse impacts of nature conservation grassland management. Cereal Res. Commun. 2007, 35, 1205–1209. [Google Scholar] [CrossRef]
  8. Poschlod, P.; Wallis de Vries, M.F. The historical and socioeconomic perspective of calcareous grasslands–lessons from the distant and recent past. Biol. Conserv. 2002, 104, 361–376. [Google Scholar] [CrossRef]
  9. Lindborg, R. Recreating grasslands in Swedish rural land scapes–Effects of seed sowing and management history. Biodiv. Conserv. 2006, 15, 957–969. [Google Scholar] [CrossRef]
  10. Dostatny, D.F.; Żurek, G.; Kapler, A.; Podyma, W. The Ex Situ Conservation and Potential Usage of Crop Wild Relatives in Poland on the Example of Grasses. Agronomy 2021, 11, 94. [Google Scholar] [CrossRef]
  11. Ryser, P.; Langenauer, R.; Gigon, A. Species richness and vegetation structure in a limestone grassland after 15 years management with six biomass removal regimes. Folia Geobot. Phytotax 1995, 30, 157–167. [Google Scholar] [CrossRef]
  12. Fiala, K.; Holub, P.; Sedláková, I.; Tůma, I.; Záhora, J.; Tesařová, M. Reasons and consequences of expansion of Calamagrostis epigejos in alluvial meadows of landscape affected by water control measures. Ekológia 2003, 22 (Suppl. S2), 242–252. [Google Scholar]
  13. Bartha, S. Composition, differentiation and dynamics in the forest steppe biome. In Slope Steppes, Loess Steppes and Forest Steppe Meadows in Hungary; Illyés, E., Bölöni, J., Eds.; MTA ÖBKI: Budapest, Hungary; ISBN 978-963-06-3673-5 2007. pp. 194–211.
  14. Rebele, F. Calamagrostis epigejos (L.) Roth auf anthro pogenen Standorten–ein Überblick. Verh. Ges. Okol. 1996, 26, 753–763. [Google Scholar]
  15. Sedláková, I.; Fiala, K. Ecological degradation of al luvial meadows due to expanding Calamagrostis epigejos. Ekológia 2001, 20 (Suppl. S3), 226–333. [Google Scholar]
  16. Catorci, A.; Cesaretti, S.; Gatti, R. Effect of long-term abandonment and spring grazing on floristic and functional composition of dry grasslands in a central Apennine farmland. Pol. J. Ecol. 2013, 61, 505–518. [Google Scholar]
  17. Prach, K.; Pyšek, P. Clonal plants–What is their role in succession? Folia Geobot. Phytotax 1994, 29, 307–320. [Google Scholar] [CrossRef]
  18. Prach, K.; Pyšek, P. Using spontaneous succession for restoration of human-disturbed habitats: Experience from Central Europe. Ecol. Eng. 2001, 17, 55–62. [Google Scholar] [CrossRef]
  19. Somodi, I.; Virágh, K.; Podani, J. The effect of the expansion of the clonal grass Calamagrostis epigejos on the species turnover of a semi-arid grassland. Appl. Veg. Sci. 2008, 11, 187–194. [Google Scholar] [CrossRef]
  20. Zhukovskaya, O.; Ulanova, N.G. Influence of brushing frequency on birch population structure after felling. Ecoscience 2006, 13, 219–225. [Google Scholar] [CrossRef]
  21. Csontos, P. Light ecology and regeneration on clearings of sessile oak-turkey oak forests in the Visegrád mountains, Hungary. Acta Bot. Hung. 2010, 52, 265–286. [Google Scholar] [CrossRef]
  22. Gergely, A.; Hahn, I.; Mészáros-Draskovits, R.; Simon, T.; Szabó, M.; Barabás, S. Vegetation succession in a newly exposed Danube riverbed. Appl. Veg. Sci. 2001, 4, 35–40. [Google Scholar] [CrossRef]
  23. Prach, K. Succession of vegetation on dumps from strip coal mining, N.W.Bohemia, Czechoslovakia. Folia Geobot. Phyto tax 1987, 22, 339–354. [Google Scholar] [CrossRef]
  24. Bartha, S. Preliminary scaling for multi-species coalitions in primary succession. Abstr. Bot. 1992, 16, 31–41. [Google Scholar]
  25. Rebele, F. Competition and coexistence of rhizomatous perennial plants along a nutrient gradient. Plant Ecol. 2000, 147, 77–94. [Google Scholar] [CrossRef]
  26. Huhta, A.; Pasi, R.; Tuomi, J.; Laine, K. Restorative mowing on an abandoned semi-natural meadow: Short-term and predicted long-term effects. J. Veg. Sci. 2001, 12, 677–686. [Google Scholar] [CrossRef]
  27. Deák, B.; Tóthmérész, B. A kaszálás hatása a hortobányi Nyírőlapos csetkákás társulásában (Effect of cutting on a Bolboschoenetum maritimi eleochariosum association in the Nyirőlapos Hortobágy). Természetvédelmi Közlemények 2007, 13, 179–186. [Google Scholar]
  28. Kramberger, B.; Kaligaric, M. Semi-natural grasslands: The effect of cutting frequency on long-term changes of floristic composition. Polish J. Ecol. 2008, 56, 33–43. [Google Scholar]
  29. Rebele, F.; Lehmann, C. Biological Flora of Central Europe: Calamagrostis epigejos (L.). Roth. Flora 2001, 196, 325–344. [Google Scholar] [CrossRef]
  30. Valkó, O.; Deák, B. Increasing the potential of prescribed burning for the biodiversity conservation of European grasslands. Curr. Opin. Environ. Sci. Health 2021, 22, 100268. [Google Scholar] [CrossRef]
  31. Házi, J.; Bartha, S.; Szentes, S.; Wichmann, B.; Penksza, K. Seminatural grassland management by long-term mowing of Calamagrostis epigejos in western Cserhát, Hungary (Management sekundärer Trockenrasen durch Langzeit-Mahd von Calamagrostis epigejos im westlichen Cserhát, Ungarn). In Steppenlebensräume Europas–Gefährdung, Erhaltungsmassnahmen und Schutz; Baumbach, H., Pfützenreuter, S., Eds.; Thüringer Ministerium für Landwirtschaft, Forsten, Umwelt und Naturschutz (TMLFUN): Erfurt, Germany, 2013; pp. 331–340. ISBN 978-3-00-044248-3. [Google Scholar]
  32. Tesitel, J.; Mládek, J.; Fajmon, K.; Blazek, P.; Mudrák, O. Reversing expansion of Calamagrostis epigejos in a grassland biodiversity hotspot: Hemiparasitic Rhinanthus major does a better job than increased mowing intensity. Appl. Veg. Sci. 2018, 21, 104–112. [Google Scholar] [CrossRef]
  33. Tesitel, J.; Mládek, J.; Horník, J.; Tesitelová, T.; Adamec, V.; Tichy, L. Suppressing competitive dominants and community restoration with native parasitic plants using the hemiparasitic Rhinanthus alectorolophus and the dominant grass Calamagrostis epigejos. J. Appl. Ecol. 2017, 54, 1487–1495. [Google Scholar] [CrossRef] [Green Version]
  34. Pruchniewicz, D.; Żołnierz, I. The effect of different restoration treatments on the vegetation of the mesic meadow degraded by the expansion of Calamagrostis epigejos. Int. J. Agric. Biol. 2019, 22, 347–354. [Google Scholar]
  35. Marosi, S.; Somogyi, S. (Eds.) Magyarország Kistájainak Katasztere (Cadastral of Microregions of Hungary); MTA Földrajztudományi Kutatóintézet: Budapest, Hungary, 1991; pp. 379–388. [Google Scholar]
  36. Klapp, E.; Boeker, P.; König, F.; Stählin, A. Wertzahlen der Grünlandpflanzen. Grünland 1953, 2, 38–40. [Google Scholar]
  37. Briemle, G.; Nitsche, S.; Nitsche, L. Nutzungswertzahlen für Gefäßpflanzen des Grünlandes. Schriftenreihe für Vegetationskunde; Bundesamt für Naturschutz: Bonn, Germany, 2005; pp. 203–225. [Google Scholar]
  38. Balázs, F. A Gyepek Botanikai és Gazdasági Értékelése; Mezőgazdasági kiadó: Budapest, Hungary, 1960. [Google Scholar]
  39. Tasi, J.; Bajnok, M.; Sutyinszki, Z.; Szentes, S. Assesing the quality and quantity of green forage with the help of a three-dimensional method. In Proceedings of the 19th International Scientific Symposium on Nutrition of Farm Animals “Zadravec-erjavec Days”, Radenci, Slovenia, 28–29 October 2010; pp. 152–160. [Google Scholar]
  40. Pielou, E.C. Ecological Diversity; Wiley: New York, NY, USA, 1975. [Google Scholar]
  41. R Development Core Team. R: A Language and Environment for Statistical Computing; R Foundation for Statistical Computing: Vienna, Austria, 2009; ISBN 3-900051-07-0. Available online: http://www.R-project.org (accessed on 20 February 2018).
  42. Házi, J.; Bartha, S.; Szentes, S.; Wichmann, B.; Penksza, K. Seminatural grassland management by mowing of Calamagrostis epigejos in Hungary. Plant Biosyst. 2011, 145, 699–707. [Google Scholar] [CrossRef]
  43. Milchunas, D.G.; Sala, O.E.; Laurenroth, W.K. A generalized model of grazing by large herbivores on grassland community structure. Am. Nat. 1988, 132, 87–106. [Google Scholar] [CrossRef]
  44. Klimes, L.; Klimesova, J. The effects of mowing and fertilisation on carbohydrate reserves and regrowth of grasses: Do they promote plant coexistence in species-rich meadows? Evol. Ecol. 2002, 15, 363–382. [Google Scholar] [CrossRef]
  45. Kavanová, M.; Gloser, V. The use of internal nitrogen stores in the rhizomatous grass Calamagrostis epigejos during regrowth after defoliation. Ann. Bot. 2005, 85, 457–463. [Google Scholar] [CrossRef] [Green Version]
  46. Bobbink, R.; During, H.; Schreurs, J.; Willems, J.; Zielman, R. Effects of selective clipping and mowing time on species diversity in chalk grassland. Folia Geobot. Phytotax 1987, 22, 363–376. [Google Scholar] [CrossRef]
  47. Tasi, J.; Szemán, L. Landbewirtschaftung in Ungarn. Multifunktionale Landnutzung und Perspektiven für Extensive Weidesysteme; Fachverlag Köhler: Giessen, Germany, 2007; pp. 45–57. [Google Scholar]
Agronomy 12 01107 g001 550
Figure 1. Mown quadrat No. 7.
Figure 1. Mown quadrat No. 7.
Agronomy 12 01107 g001
Agronomy 12 01107 g002 550
Figure 2. Control quadrat No. 7.
Figure 2. Control quadrat No. 7.
Agronomy 12 01107 g002
Agronomy 12 01107 g003 550
Figure 3. Change of cover of C. epigejos in the mown and control plots on the Bükkös hill northern slopes during the 2001–2013 period, mown plot = red boxes, control plot = green boxes. Empty circles = outliers. Significant differences between mown and control plots in the same year are marked by * (p < 0.05) ** (p < 0.01) *** (p < 0.005).
Figure 3. Change of cover of C. epigejos in the mown and control plots on the Bükkös hill northern slopes during the 2001–2013 period, mown plot = red boxes, control plot = green boxes. Empty circles = outliers. Significant differences between mown and control plots in the same year are marked by * (p < 0.05) ** (p < 0.01) *** (p < 0.005).
Agronomy 12 01107 g003
Agronomy 12 01107 g004 550
Figure 4. Changes in the relative cover proportion of the most dominant species during vegetation development.
Figure 4. Changes in the relative cover proportion of the most dominant species during vegetation development.
Agronomy 12 01107 g004
Agronomy 12 01107 g005 550
Figure 5. Biomass of Fabaceae species in selected mown and control plots. * p < 0.05, ** p < 0.01. The empty circle indicates the outlier.
Figure 5. Biomass of Fabaceae species in selected mown and control plots. * p < 0.05, ** p < 0.01. The empty circle indicates the outlier.
Agronomy 12 01107 g005
Table
Table 1. The average cover of Calamagrostis epigejos and other species, number of species, and different diversity indices (p < 0.005).
Table 1. The average cover of Calamagrostis epigejos and other species, number of species, and different diversity indices (p < 0.005).
MOWNCONTROL
200120092013200120092013
Total cover103.38102.66121.15115.70103.18139.26
Cover of Calamagrostis epigejos absolute56.632.501.6263.7518.3714.25
Cover of Calamagrostis epigejos relative0.550.020.010.550.180.10
Cover of subordinated species absolute46.75100.16119.5251.9584.81125.01
Cover of subordinated species relative0.450.950.980.450.810.89
Number of species14.8829.3732.6218.2524.2527.62
Shannon Diversity1.622.072.341.662.072.53
Table
Table 2. Control and mown zones based on the average value of Klapp’s forage values (01, 02 etc.: years, C: control, M: mown).
Table 2. Control and mown zones based on the average value of Klapp’s forage values (01, 02 etc.: years, C: control, M: mown).
Plots01C01M02C03M03C03M04C04M05C05M06C06M07C07M
Klapp average values1.71.81.81.91.82.41.82.92.41.92.32.92.13.2
Grass yield (t/ha)7.110.47.110.47.110.47.112.57.414.17.114.87.114.4
Plots08C08M09C09M10C10M11C11M12C12M13C13M
Klapp average values2.12.83.43.83.33.92.53.22.13.82.13.9
Grass yield (t/ha)7.113.68.812.48.114.87.614.847.513.67.414.1
Publisher’s Note: MDPI stays neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Share and Cite

MDPI and ACS Style

Házi, J.; Penksza, K.; Barczi, A.; Szentes, S.; Pápay, G. Effects of Long-Term Mowing on Biomass Composition in Pannonian Dry Grasslands. Agronomy 2022, 12, 1107. https://doi.org/10.3390/agronomy12051107

AMA Style

Házi J, Penksza K, Barczi A, Szentes S, Pápay G. Effects of Long-Term Mowing on Biomass Composition in Pannonian Dry Grasslands. Agronomy. 2022; 12(5):1107. https://doi.org/10.3390/agronomy12051107

Chicago/Turabian Style

Házi, Judit, Károly Penksza, András Barczi, Szilárd Szentes, and Gergely Pápay. 2022. "Effects of Long-Term Mowing on Biomass Composition in Pannonian Dry Grasslands" Agronomy 12, no. 5: 1107. https://doi.org/10.3390/agronomy12051107

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop