Research Article |
Corresponding author: Blanka Wiatrowska ( blanka.wiatrowska@up.poznan.pl ) Academic editor: Tiffany Knight
© 2023 Blanka Wiatrowska, Przemysław Kurek, Dawid Moroń, Waldemar Celary, Artur Chrzanowski, Paweł Trzciński, Łukasz Piechnik.
This is an open access article distributed under the terms of the Creative Commons Attribution License (CC BY 4.0), which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Citation:
Wiatrowska B, Kurek P, Moroń D, Celary W, Chrzanowski A, Trzciński P, Piechnik Ł (2023) Linear scaling – negative effects of invasive Spiraea tomentosa (Rosaceae) on wetland plants and pollinator communities. NeoBiota 81: 63-90. https://doi.org/10.3897/neobiota.81.95849
|
Invasive plants directly and indirectly disrupt the ecosystem functioning, of which indirect effects, for example, through trophic cascades, are particularly difficult to predict. It is frequently assumed that the impact of an invading species on the ecosystem is proportional (linearly related) to its density or abundance in a habitat, but this assumption has rarely been tested. We hypothesised that abundance and richness of plants and potentially pollinators of wet meadows change as a result of invasion of steeplebush Spiraea tomentosa and that these changes are proportional to the density of the shrub. We selected 27 sites amongst wet meadows habitats invaded by S. tomentosa with coverage ranging from 0% to 100% and examined the diversity of plants, as well as the abundance and diversity of flower visitors (bees, butterflies with moths and flies). Our results showed that the richness of plants, as well as the richness and number of individuals of flower visitors, decrease significantly and linearly with an increase of the S. tomentosa cover. This finding supports the hypothesis that the impact of an invasive species can be proportional to their population density, especially if this species is limiting the available resources without supplying others. Our study is the first to show such an unequivocal negative, linear effect of an invasive shrub on the abundance and richness of potential pollinators. It proves that the negative impact of S. tomentosa on the wetland ecosystem appears even with a minor coverage of the invader, which should be taken into account when planning activities aimed at controlling the population of this transformer species. The simultaneously detected linear dependence allows us to assume that the benefits of controlling secondary populations of the shrub can be proportional to the incurred effort.
bees, biodiversity, biological conservation, butterflies, flies, flower visitors, invasive plants, non-native species, wetlands
Freshwater wetlands are important refuges for hygrophilous and hygrobiont plants and animals and, as such, they support diverse and unique species assemblages (
Amongst animals, insects are a group particularly sensitive to disturbances resulting from plant invasions (
The direction of the impact of invasive plants on pollinators is strongly dependent on the scale of the invasion (
The North American steeplebush (Spiraea tomentosa L., Rosaceae) is a highly invasive shrub found in central and northern Europe (
In Europe, S. tomentosa has been cultivated as an ornamental plant since the 18th century (
Spiraea tomentosa in wet meadows located in the Lower Silesian Forests (photo by B. Wiatrowska).
However, still very little information is available on its effects on pollinators – flower visitors and the plant species composition. These data are urgently needed to communicate management priorities in times when invasions are a threat and challenge in nature conservation (
Spiraea tomentosa interacts with pollinators (
Based on these premises, our main goal was to assess whether there was a relationship between the abundance of S. tomentosa and the diversity of plants, as well as the abundance and diversity of potential pollinators in wet meadow communities. We considered what influence the invader – non-linear or linear – has on plants and potential pollinators of indigenous communities. In the case of a non-linear relationship, the question arises whether there is a certain minimum point (tipping point), at which a pollinator population changes as the invasive plant becomes dominant.
We tested the hypotheses that: (1) the richness of plants and the abundance and richness of visiting pollinators change as a result of Spiraea tomentosa invasion and (2) changes are proportional (linearly) to the density of the shrub. The implementation of these studies was essential to provide insight into the density-dependent impact of the invasive alien species S. tomentosa on biodiversity, focusing on plants and pollinator species.
The research was carried out in a wet meadow complex located in the Lower Silesian Forests, in south-western Poland, where one of the first documented observations of S. tomentosa naturalisation in Europe was made (
In the Lower Silesian Forests from the 1890s, large-scale drainage works were carried out, but after the Second World War, the maintenance of hydrotechnical structures was abandoned, which resulted in secondary bogging of the area (
In 2021, amongst six wet meadow complexes, 27 study sites were randomly selected for further analyses, each characterised with different S. tomentosa coverage. Wet meadows were at least 5000 ± 620 m apart, while the study sites located in the same meadow, but differing in S. tomentosa density, were at least 60 ± 42 m apart. To control the disruptive effects of the potential spatial gradients (distance from forests, human settlements, farmlands and meadows), we applied the Spearman test to make sure that these features did not correlate with steeplebush cover. We ensured that the selected study sites do not correlate with the distance of places to the closest forest areas (woodlands) (rS = −0.08, p = 0.703), human settlements (rS = 0.36, p = 0.069), farmland (rS = 0.04, p = 0.844) and meadows (rS = 0.14, p = 0.461). The distances were measured with QGIS 3.16 (
In each of the study sites (n = 27), permanent circular plots of 100 m2 were established. On each of these sites, the S. tomentosa cover was determined, a list of vascular plants was made and flower visitors were caught using a pan-trap placed in their centre. Data were collected during the period of full flowering of the shrub (
The estimation of S. tomentosa coverage in the study sites was performed between 18 and 20 July 2021. Shrub cover was estimated visually using a cover class method (a modified Braun-Blanquet method) (
The plants species composition was surveyed twice (18–20 July and 27–29 August 2021) at each study site (n = 27) located in wet meadows at permanent circular plots (100 m2). The vast majority of plant communities consisted of native species (74). However, in addition to S. tomentosa, the presence of single seedlings or juveniles of five other alien species was found (seedlings of Prunus cerasifera, P. serotina, Quercus rubra and juvenile of Solidago canadensis and Juncus tenuis). All the identified plant species, including S. tomentosa, were included in the analysis. Due to the fact that alien species other than S. tomentosa did not bloom during the field study, their presence was found on single sites and all had a negligible coverage (< 1%), thus it was assumed that they had no effect on flower visitors. Additionally, there was no relationship between S. tomentosa cover and the number of non-native species (generalised linear mixed-effects models; t = −0.513, R2 = 0.01, p = 0.618). All plants were identified according to
Pan traps to catch insects (n = 27) were set up in the central part of each of the 27 study sites. This type of trap was used because they are an effective method of trapping insects in semi-natural habitats, including open areas with a wider field of vision (
The traps were positioned in sunny places, on poles at the height of S. tomentosa inflorescences (ca. 70 cm above the ground and approx. 10 cm from the inflorescences of the shrub). The traps were 15 cm in diameter and filled to 2/3 volume with a mixture of water (95%), ethylene glycol (4.8%) and detergent (0.2%). Traps were first installed on 21 July 2021 and inspected three times at 14-day intervals during the peak of flowering and the peak of pollen season of this species. The samples were collected 03, 17 and 31 of August (exposure 21 July-03 August, 04 August-17 August, 18 August-31 August 2021), which made a total of 81 samples (pan traps). The caught insects were poured through a strainer and preserved in test tubes with 75% ethyl alcohol. Each selected group of flower visitors was identified according to
All data analyses and visualisations were performed using the R ver. 4.2.1 software (
In addition, to understand if possible differences in the composition of potential pollinator communities depending on S. tomentosa cover are caused by pollinator species replacement or loss, we calculated the mean rank of the samples in a maximally packed matrix for overall pollinators: nestedness means that species-poor sites (i.e. those with a high rank in the nested matrix) are subsets of species-rich sites (those with a low rank). Data analyses and visualisation were performed using BIPARTITE ver. 2.18 (
We compared the rank of samples in the maximally packed matrix with GLMM (Gaussian distribution with the meadow and site identities as the nested random factors). The models’ assumptions were verified using the DHARMA ver. 0.4.6 package (
During overall 27 216 hours of the pan-trap deployment, we collected 3649 individuals of 191 potential pollinator species or families (in the case of flies). Flies (Diptera) formed the most abundant pollinator group, accounting for 75% of all trapped insects. Butterflies and moths (Lepidoptera) comprised 15% of the collected insects. Bees (Apoidea, Hymenoptera) were only a minor fraction of flower visitors (10% of the specimens). A total of 80 vascular plant species were recorded in the investigated study sites (Table
List of vascular plants and flower visitors found at study sites with their numbers.
Plants | Bees | No. | Butterflies and moths | No. | Flies | No. |
---|---|---|---|---|---|---|
Achillea millefolium L. | Ammophila sabulosa (Linnaeus, 1758) | 2 | Abrostola tripartita (Hufnagel, 1766) | 5 | Chalcosyrphus nemorum (Fabricius, 1805) | 2 |
Achillea ptarmica L. | Andrena bimaculata (Kirby, 1802) | 1 | Abrostola triplasia (Linnaeus, 1758) | 1 | Cheilosia longula (Zetterstedt, 1838) | 1 |
Agrostis capilaris L. | Andrena dorsata (Kirby, 1802) | 3 | Actinotia polyodon (Clerck, 1759) | 2 | Chloromyia formosa Scopoli, 1763 | 1 |
Agrostis gigantea Roth | Andrena flavipes Panzer, 1799 | 3 | Agrotis segetum (Denis & Schiffermüller, 1775) | 4 | Chrysotoxum bicinctum (Linnaeus, 1758) | 3 |
Agrostis stolonifera L. | Andrena minutula (Kirby, 1802) | 1 | Amphipoea oculea (Linnaeus, 1761) | 22 | Chrysotoxum festivum (Linnaeus, 1758) | 1 |
Alnus glutinosa (L.) Gaertn. | Apis mellifera Linnaeus, 1758 | 25 | Apamea monoglypha (Hufnagel, 1766) | 7 | Chrysotoxum verralli Collin, 1940 | 3 |
Alopecurus pratensis L. | Astata boops (Schrank, 1781) | 9 | Aphantopus hyperantus (Linnaeus, 1758) | 8 | Dasysyrphus tricinctus (Fallen, 1817) | 1 |
Angelica sylvestris L. | Bombus bohemicus Seidl, 1837 | 3 | Aporia crataegi (Linnaeus, 1758) | 1 | Episyrphus balteatus (De Geer, 1776) | 21 |
Athyrium filix-femina (L.) Roth | Bombus jonellus (Kirby, 1802) | 2 | Araschnia levana (Linnaeus, 1758) | 8 | Eristalinus sepulhralis (Linnaeus, 1758) | 1 |
Betula pendula Roth | Bombus lapidarius (Linnaeus, 1758) | 2 | Argynnis adippe (Denis & Schiffermüller, 1775) | 3 | Eristalis arbustorum (Linnaeus, 1758) | 11 |
Calamagrostis canescens (Weber) Roth | Bombus lucorum (Linnaeus, 1761) | 17 | Argynnis aglaja (Linnaeus, 1758) | 3 | Eristalis lineata (Harris, 1776) | 3 |
Calamagrostis epigejos (L.) Roth | Bombus pascuorum (Scopoli, 1763) | 24 | Argynnis paphia (Linnaeus, 1758) | 17 | Eristalis obscura Loew, 1866 | 1 |
Campanula patula L. | Bombus terrestris (Linnaeus, 1758) | 22 | Autographa gamma Linnaeus, 1758 | 16 | Eristalis pertinax (Scopoli, 1763) | 3 |
Cardamine pratensis L. | Colletes fodiens (Geoffroy, 1785) | 1 | Boloria selene (Denis & Schiffermüller, 1775) | 5 | Eristalis tenax (Linnaeus, 1758) | 14 |
Carex hirta L. | Crabro cribrarius (Linnaeus, 1758) | 29 | Calophasia lunula (Hufnagel, 1766) | 1 | Helophilus hybridus Loew, 1846 | 11 |
Carex ovalis Gooden. | Crossocerus nigritus (Lepeletier & Brülle, 1834) | 1 | Carterocephalus palaemon (Pallas, 1771) | 1 | Helophilus pendulus (Linnaeus, 1758) | 6 |
Carex praecox Schreb. | Dasypoda hirtipes (Fabricius, 1793) | 2 | Celaena leucostigma (Hübner, 1808) | 1 | Helophilus trivittatus (Fabricius, 1805) | 12 |
Cirsium arvense (L.) Scop. | Ectemnius cephalotes (Olivier, 1791) | 1 | Cerapteryx graminis (Linnaeus, 1758) | 1 | Myathropa florea (Linnaeus, 1758) | 3 |
Cirsium palustre (L.) Scop. | Ectemnius confinis (Walker, 1871) | 3 | Chiasmia clathrata (Linnaeus, 1758) | 2 | Oxycera leonina (Panzer, 1798) | 1 |
Deschampsia caespitosa (L.) P.B. | Ectemnius continuus (Fabricius, 1804) | 44 | Coenonympha arcania (Linnaeus, 1761) | 1 | Parhelophilus versicolor (Fabricius, 1794) | 6 |
Dryopteris cartchusiana (Vill.) H.P.Fuchs | Ectemnius lapidarius (Panzer, 1804) | 5 | Coenonympha glycerion (Borkhausen, 1788) | 1 | Scaeva pyrastri (Linnaeus, 1758) | 2 |
Epilobium palustre L. | Ectemnius ruficornis (Zetterstedt, 1838) | 1 | Coenonympha pamphilus (Linnaeus, 1758) | 20 | Sericomyia silentis (Harris, 1776) | 1 |
Equisetum arvense L. | Evylaeus albipes (Fabricius, 1781) | 3 | Cyclophora albipunctata (Hufnagel, 1767) | 1 | Sicus ferrugineus (Linnaeus, 1761) | 27 |
Festuca rubra L. | Evylaeus calceatus (Scopoli, 1763) | 1 | Diachrysia chrysitis (Linnaeus, 1758) | 2 | Sphaerophoria scripta (Linnaeus, 1758) | 7 |
Filipendula ulmaria (L.) Maxim. | Evylaeus laticeps (Schenck, 1869) | 1 | Diarsia brunnea (Denis & Schiffermüller, 1775) | 10 | Syritta pipiens (Linnaeus, 1758) | 9 |
Frangula alnus Mill. | Evylaeus malachurus (Kirby, 1802) | 1 | Diarsia mendica (Fabricius, 1775) | 10 | Syrphus ribesii (Linnaeus, 1758) | 1 |
Galeopsis tetrachit L. | Gorytes albidulus (Lepeletier, 1832) | 1 | Diarsia rubi (Vieweg, 1790) | 1 | Syrphus torvus (Osten-Sacken, 1875) | 3 |
Galeopsis bifida Boenn. | Gorytes laticinctus (Lepeletier, 1832) | 2 | Dioryctria simplicella Heinemann, 1863 | 1 | Tropidia scita (Harris, 1780) | 1 |
Galium aparine L. | Gorytes quinquecinctus (Fabricius, 1793) | 2 | Endotricha flammealis (Denis & Schiffermüller, 1775) | 3 | Xylota segnis (Linnaeus, 1758) | 30 |
Galium palustre L. | Halictus maculatus Smith, 1848 | 1 | Epirrhoe alternata (Müller, 1764) | 8 | Xylota tarda Meigen, 1822 | 15 |
Galium saxatile L. | Halictus sexcinctus (Fabricius, 1775) | 3 | Euclidia glyphica (Linnaeus, 1758) | 2 | Anthomyiidae | 482 |
Galium uliginosum L. | Hylaeus brevicornis Nylander, 1852 | 1 | Eupithecia virgaureata Doubleday, 1861 | 1 | Calliphoridae | 800 |
Glechoma hederacea L. | Hylaeus cardioscapus Cockerell, 1924 | 1 | Euxoa tritici (Linnaeus, 1761) | 1 | Fanniidae, Muscidae, Scathophagidae | 400 |
Holcus lanatus L. | Hylaeus communis Nylander, 1852 | 18 | Gonepteryx rhamni (Linnaeus, 1758) | 1 | Rhinophoridae | 156 |
Holcus mollis L. | Hylaeus confusus Nylander, 1852 | 1 | Heliothis viriplaca (Hufnagel, 1766) | 1 | Sarcophagidae | 184 |
Hydrocotyle vulgaris L. | Hylaeus difformis (Eversmann, 1852) | 2 | Hemaris fuciformis (Linnaeus, 1758) | 1 | Tachinidae | 530 |
Hypericum maculatum Crantz | Hylaeus dilatatus (Kirby, 1802) | 1 | Hesperia comma (Linnaeus, 1758) | 33 | ||
Juncus articulatus L. | Hylaeus leptocephalus (Morawitz, 1870) | 1 | Hipparchia semele (Linnaeus, 1758) | 1 | ||
Juncus effusus L. | Hylaeus moricei luteifrons (Strand, 1909) | 1 | Hyloicus pinastri (Linnaeus, 1758) | 2 | ||
Juncus tenuis Willd. | Hylaeus pectoralis Förster, 1871 | 5 | Hypena proboscidalis (Linnaeus, 1758) | 9 | ||
Linaria vulgaris Mill. | Lasioglossum leucozonium (Schrank, 1781) | 2 | Idaea aversata (Linnaeus, 1758) | 3 | ||
Lotus uliginosus Schkuhr | Lasioglossum zonulum (Smith, 1848) | 29 | Idaea emarginata (Linnaeus, 1758) | 1 | ||
Lychnis flos-cuculi (L.) Greuter & Burdet | Lestica clypeata (Schreber, 1759) | 1 | Inachis io (Linnaeus, 1758) | 1 | ||
Lycopus europaeus L. | Lindenius pygmaeus (Van der Linden, 1829) | 1 | Issoria lathonia (Linnaeus, 1758) | 1 | ||
Lysimachia thyrsiflora L. | Macropis europaea Warncke, 1973 | 6 | Lacanobia oleracea (Linnaeus, 1758) | 2 | ||
Lysimachia vulgaris L. | Megachile centuncularis (Linnaeus, 1758) | 2 | Lacanobia suasa (Denis & Schiffermuller, 1775) | 1 | ||
Lythrum salicaria L. | Megachile ligniseca (Kirby, 1802) | 2 | Lycaena alciphron (Rottemburg, 1775) | 3 | ||
Mentha arvensis L. | Megachile versicolor Smith, 1844 | 2 | Lycaena phlaeas (Linnaeus, 1761) | 4 | ||
Molinia caerulea (L.) Moench | Megachile willughbiella (Kirby, 1802) | 1 | Lycaena tityrus (Poda, 1761) | 2 | ||
Peucedanum palustre (L.) Moench | Melitta haemorrhoidalis (Fabricius, 1775) | 2 | Lycaena virgaureae (Linnaeus, 1758) | 43 | ||
Phalaris arundinacea L. | Nomada zonata Panzer, 1798 | 1 | Lycophotia porphyrea (Denis & Schiffermüller, 1775) | 2 | ||
Plantago lanceolata L. | Oxybelus trispinosus (Fabricius, 1787) | 6 | Macaria alternata (Denis & Schiffermüller, 1775) | 3 | ||
Poa pratensis L. | Oxybelus uniglumis (Linnaeus, 1758) | 1 | Macaria liturata (Clerck, 1759) | 2 | ||
Poa trivialis L. | Pemphredon inornata Say, 1824 | 1 | Mamestra brassicae (Linnaeus, 1758) | 2 | ||
Polygonum hydropiper (L.) Delarbre | Pemphredon lethifer (Schuckard, 1837) | 2 | Maniola jurtina (Linnaeus, 1758) | 64 | ||
Populus tremula L. | Pemphredon rugifer (Dahlbom, 1845) | 1 | Manuela complana (Linnaeus, 1758) | 3 | ||
Potentilla anserina L. | Philanthus triangulum (Fabricius, 1775) | 1 | Mecyna flavalis (Denis & Schiffermüller, 1775) | 3 | ||
Potentilla erecta (L.) Raeusch | Podalonia affinis (Kirby, 1798) | 1 | Melanargia galathea (Linnaeus, 1758) | 8 | ||
Prunus cerasifera Ehrh. | Seladonia tumulorum (Linnaeus, 1758) | 2 | Melanchra pisi (Linnaeus, 1758) | 2 | ||
Prunus serotina Ehrh. | Sphecodes hyalinatus Hagens, 1882 | 1 | Mesapamea secalis (Linnaeus, 1758) | 2 | ||
Quercus robur L. | Sphecodes pellucidus Smith, 1845 | 1 | Miltochrista miniata (Forster, 1771) | 3 | ||
Quercus rubra L. | Tachytes panzeri Dufour, 1841 | 5 | Mythimna albipuncta (Denis & Schiffermuller, 1775) | 43 | ||
Ranunculus repens L. | Trypoxylon attenuatum Smith, 1851 | 3 | Mythimna ferrago (Fabricius, 1787) | 8 | ||
Ranunculus acris L. | Trypoxylon deceptorum Antropov, 1991 | 2 | Mythimna pallens (Linnaeus, 1758) | 34 | ||
Rubus idaeus L. | Trypoxylon figulus (Linnaeus, 1758) | 9 | Noctua interjecta Hübner, 1803 | 1 | ||
Rubus plicatus Weihe & Nees | Noctua pronuba Linnaeus, 1758 | 3 | ||||
Rumex acetosa L. | Nymphalis antiopa (Linnaeus, 1758) | 1 | ||||
Rumex acetosella L. | Ochlodes venata (Bremer & Grey, 1853) | 1 | ||||
Salix aurita L. | Oligia versicolor (Borkhausen, 1792) | 1 | ||||
Scirpus sylvaticus L. | Pandemis heparana (Denis & Schiffermüller, 1775) | 1 | ||||
Scutelaria galericulata L. | Pelosia obtusa (Herrich-Schäffer, 1847) | 2 | ||||
Solanum dulcamara L. | Perizoma alchemillata (Linnaeus, 1758) | 1 | ||||
Solidago canadensis L. | Pieris brassicae (Linnaeus, 1758) | 5 | ||||
Sorbus aucuparia L. | Pieris napi (Linnaeus, 1758) | 1 | ||||
Spiraea tomentosa L. | Platyptilia nemoralis Zeller, 1841 | 1 | ||||
Stellaria graminea L. | Plusia festucae (Linnaeus, 1758) | 1 | ||||
Stellaria palustris Retz. | Rusina ferruginea (Esper, 1785) | 1 | ||||
Urtica dioica L. | Scopula immutata (Linnaeus, 1758) | 2 | ||||
Veronica chamaedrys L. | Scotopteryx chenopodiata (Linnaeus, 1758) | 3 | ||||
Viola palustris L. | Synaphe punctalis (Fabricius, 1775) | 1 | ||||
Thalpophila matura (Hufnagel, 1766) | 1 | |||||
Thyatira batis (Linnaeus, 1758) | 1 | |||||
Timandra comae A. Schmidt, 1931 | 2 | |||||
Tineola bisselliella (Hummel, 1823) | 1 | |||||
Vanessa atalanta (Linnaeus, 1758) | 1 | |||||
Xestia baja (Denis & Schiffermüller, 1775) | 19 | |||||
Xestia c-nigrum (Linnaeus, 1758) | 13 | |||||
Xestia ditrapezium (Denis & Schiffermüller, 1775) | 25 | |||||
Xestia stigmatica (Hübner 1813) | 1 | |||||
Xestia xanthographa (Denis & Schiffermüller, 1775) | 16 |
A negative relationship was found between steeplebush cover and plant species richness (t = −7.15; Fig.
The relationship between species richness of plants and site cover by Spiraea tomentosa. Points represent each of 27 sites. Point colours correspond to a meadow. The 95% CI are marked with polygons. Jittering was added to aid visualisation.
An increase in S. tomentosa cover correlated also with a decline in the number of bee, butterfly and moth and fly individuals by about 70%, 80% and 45% (Fig.
The relationship between abundance of A bees C butterflies and moths and E flies, as well as species richness of B bees D butterflies and moths F flies and site cover by Spiraea tomentosa. Points represent each of 81 surveys. Point colours correspond to a meadow and point shapes correspond to a survey number. Legend as in Fig.
The potential pollinator community in the habitats studied was significantly nested, indicating that species-poor samples (pan traps with a high rank) constituted subsets of species-rich samples (pan traps with a low rank) and that this pattern was not random. The nestedness rank significantly increased in proportion to S. tomentosa cover (t = 6.40; Fig.
The direction (negative vs. positive), the shape (linear vs. non-linear) and the strength of the relationship between the abundance of the invasive species and the diversity of native species determine which invaders pose the greatest threat to ecosystems (
In our research, we found a strong, negative, linear impact of the Spiraea tomentosa cover on vascular plant species richness, so this result positively validates the hypothesis. Our results showed that the diversity of plants decreased due to the increased invasive shrub coverage. These results correspond with a global meta-analysis that assessed the direction, shape and strength of the response of native communities to the increasing abundance of invasive species (
In other studies on the impact of alien species on plant species richness, it was found that, amongst alien species entering wetlands in Central Europe, the invasion of Mimulus guttatus DC and Impatiens glandulifera Royle does not reduce the species richness of native plants. The invasion of Solidago gigantea Aiton and Rudbeckia laciniata L. decreases species richness by about 26% and 30%, while the invasion of Fallopia sachalinensis (F. Schmidt) Ronse Decraene, F. japonica (Houtt.) Ronse Decraene and F. × bohemica (Chrtek & Chrtková) JP Bailey contributes to the reduction of species richness by 86%, 73% and 66%, respectively (
The direction, shape (linear vs. non-linear) and strength of the impact of an invasive plant species on insects, including potential pollinators, is more difficult to predict (
In our research, we found a strong, negative, linear influence of S. tomentosa on the abundance and diversity of flower visitors, which allows us to positively verify our hypothesis regarding the negative effect of the shrub cover on potential pollinators.
Butterflies and moths seem to be least resistant to S. tomentosa infestation, as in dense populations of this shrub, the number of individuals decreased by 80% and species richness was reduced by 70%. The strong response of this group of insects is understandable, because Lepidoptera species strongly depend on plants throughout their life cycle – they use them for breeding and as a source of food for larvae and adults (
Other insects that have strong, often reciprocal, relationships with native species of flowering plants include bees. Pollinator bees are very sensitive to a particular diet source and combination of nutrients (
Another important order amongst insects pollinating flowers around the world are flies from the Syrphidae, Bombyliidae and Muscoidea families (
For all the studied groups of potential pollinators, it was found that the influence of S. tomentosa is proportional to its density coverage. The number of individuals and richness of butterflies and moths, bees and flies significantly, linearly decreased with the increase in the steeplebush cover, which supports the thesis that the impact, at least of some invasive plants, is proportional to invader population density (
Most studies indicate that the impact of invasive species on potential pollinators depends on whether the invasive species reduces resources, upon which the native species depends and also whether it acts as a novel resource for the native species (
Effective nature conservation and management of invasive plant species should be based on a comprehensive understanding of the role they play in our ecosystems (
The number and diversity of plants, butterflies and moths, bees and flies change at all points in the S. tomentosa invasion pathway (representing a linear response to invasion). Although it was assumed that invasive plant impacts are highly scale-dependent (
Many studies showed that the management effort in the case of invasive species populations largely depends on the density–impact curve of the species and optimisation of management relies on minimising the sum of the costs of their impact and management (
This research was financially supported by the statutory activities of the Faculty of Forestry, the Poznań University of Life Sciences and partially financed by National Science Centre’s grant (UMO-2020/37/B/NZ8/01743) for Dawid Moroń.
Study sites | The nearest village | Geographical coordinates (DMS) | S. tomentosa cover (%) |
---|---|---|---|
1 | Ruszów | 51°23'39"N, 15°09'26"E | 80 |
2 | Ruszów | 51°23'38"N, 15°09'28"E | 40 |
3 | Ruszów | 51°23'36"N, 15°09'26"E | 40 |
4 | Ruszów | 51°23'33"N, 15°09'30"E | 50 |
5 | Ruszów | 51°23'31"N, 15°09'30"E | 50 |
6 | Ruszów | 51°23'29"N, 15°09'31"E | 30 |
7 | Ruszów | 51°23'26"N, 15°09'47"E | 70 |
8 | Ruszów | 51°23'26"N, 15°09'44"E | 60 |
9 | Ruszów | 51°23'26"N, 15°09'40"E | 40 |
10 | Poświętne | 51°22'42"N, 15°14'03"E | 90 |
11 | Poświętne | 51°22'41"N, 15°13'57"E | 100 |
12 | Poświętne | 51°22'43"N, 15°13'49"E | 100 |
13 | Ołobok | 51°18'32"N, 15°15'54"E | 5 |
14 | Ołobok | 51°18'33"N, 15°15'51"E | 10 |
15 | Ołobok | 51°18'35"N, 15°15'52"E | 0,5 |
16 | Gozdnica | 51°24'45"N, 15°04'06"E | 100 |
17 | Gozdnica | 51°24'44"N, 15°04'04"E | 100 |
18 | Gozdnica | 51°24'45"N, 15°04'02"E | 100 |
19 | Iłowa | 51°30'11"N, 15°11'11"E | 0 |
20 | Iłowa | 51°30'12"N, 15°11'10"E | 0 |
21 | Iłowa | 51°30'13"N, 15°11'11"E | 0 |
22 | Stary Węgliniec | 51°17'55"N, 15°11'06"E | 20 |
23 | Stary Węgliniec | 51°17'55"N, 15°11'03"E | 60 |
24 | Stary Węgliniec | 51°17'57"N, 15°11'07"E | 70 |
25 | Stary Węgliniec | 51°17'59"N, 15°11'20"E | 40 |
26 | Stary Węgliniec | 51°17'59"N, 15°11'22"E | 30 |
27 | Stary Węgliniec | 51°17'58"N, 15°11'18"E | 0 |