Tree invasions into treeless areas: mechanisms and ecosystem processes

Non-native tree invasions occur not only in woodland or forest vegetation, but also into areas with little or no native tree presence. Limiting factors for tree establishment and survival include seasonal or annual drought, low nutrient availability, cold temperature extremes, fire, and other abiotic conditions to which trees are poorly adapted as well as biotic conditions such as herbivory and lack of soil mutualist inoculum. Tree invasions of grasslands and semi-arid riparian areas in particular are now widespread and frequently result in the rapid conversion of these habitats to woodlands or forests. In some cases, these invasions are the result of a change in extrinsic conditions such as climate, fire, and/or grazing that remove what have been previous barriers to tree establishment. However, in other cases, tree species with particular life-history and dispersal traits fill open niches or outcompete native species. Significant examples of tree invasion into treeless areas can be seen with invasions of Pinus species into temperate grasslands and fynbos shrublands, Melaleuca quinquenervia and Triadica sebifera into grassy wetlands, Prosopis and Tamarix species into semi-arid riparian zones, and Acacia and Morella invasions into nutrient-poor shrublands and barrens. The establishment of trees into treeless areas may have strong impacts on ecosystem processes, influencing biogeochemical cycling, carbon sequestration and cycling, and ecohydrology, as well possible edaphic legacies that persist even if trees are removed

No ‘home’ versus ‘away’ effects of decomposition found in a grassland–forest reciprocal litter transplant study

Plant litter often decomposes faster in the habitat from which it was derived (i.e. home) than when placed in foreign habitats (i.e. away), which has been called the home-field advantage (HFA) of litter decomposition. We tested whether the HFA of litter decomposition is driven by decomposer communities being specialized at decomposing litter in their home habitat, by reciprocally transplanting litter from grassland to early-successional forest. Unexpectedly, we found an overall disadvantage for at-home decomposition despite large differences in litter quality (lignin:N) between the two habitats. We found more evidence for habitat specialization among secondary decomposers (mites) than the primary decomposers (bacteria and fungi), suggesting that soil animals may be important in driving HFA patterns where they do exist. Grass litter decomposition in forest slowed down and became more fungal-based, while tree litter decomposition in grassland increased yet showed no shift to being bacterially-based, relative to 'at home' decomposition. This suggests a biological explanation for why a positive HFA was not observed. Our results highlight that both environmental context and soil biology can play an important and sometimes counter-intuitive role in modifying decomposition. A better understanding of the interaction between all three primary drivers of decomposition (the environment, litter quality and soil organisms) is necessary for reliable prediction of decomposition at global scale

Sample storage conditions alter colonisation structures of arbuscular mycorrhizal fungi and, particularly, fine root endophyte

Background and Aims The structures of arbuscular mycorrhizal (AM) fungi (hyphae, arbuscules, vesicles, spores) are used to make inferences about fungal activity based on stored samples, yet the impact of storage method has not been quantified, despite known effects of temperature and host condition on AM fungal colonisation. Methods We measured how four storage treatments (cool or ambient conditions, with and without plant shoots attached, i.e. n = four treatment combinations) affected AM fungal colonisation of subterranean clover (Trifolium subterraneum L.) after 0, 2, 6 and 10 days of storage. Roots were assessed for colonisation of fine root endophyte and coarse AM fungi. Results For coarse AM fungi, total colonisation was unaffected, but arbuscules were reduced at Day 6 and increased again by Day 10, except Ambient-Minus-Shoots. There was a loss of vesicles in all treatments at Day 2, and an increase in spore number at Day 6 within Cool-Plus-Shoots. In contrast, for fine root endophyte, total colonisation was greatly reduced at Day 6 but increased again at Day 10, in all except the Cool-Plus-Shoots treatment. Conclusions Our data demonstrate that AM fungal activity is not suspended in commonly used plant storage conditions. Storage method and time impacted AM fungal colonisation, particularly for fine root endophyte. We recommend samples are processed within 2 days of harvest

Fine root endophytes under scrutiny: a review of the literature on arbuscule-producing fungi recently suggested to belong to the Mucoromycotina

Fine root endophytes (FRE) are arbuscule-forming fungi presently considered as a single species—Glomus tenue in the Glomeromycota (Glomeromycotina)—but probably belong within the Mucoromycotina. Thus, FRE are the only known arbuscule-forming fungi not within the arbuscular mycorrhizal fungi (AMF; Glomeromycotina) as currently understood. Phylogenetic differences between FRE and AMF could reflect ecological differences. To synthesize current ecological knowledge, we reviewed the literature on FRE and identified 108 papers that noted the presence of FRE and, in some, the colonization levels for FRE or AMF (or both). We categorized these records by geographic region, host-plant family and environment (agriculture, moderate-natural, low-temperature, high-altitude and other) and determined their influence on the percentage of root length colonized by FRE in a meta-analysis. We found that FRE are globally distributed, with many observations from Poaceae, perhaps due to grasses being widely distributed. In agricultural environments, colonization by FRE often equalled or exceeded that of AMF, particularly in Australasia. In moderate-natural and high-altitude environments, average colonization by FRE (~10%) was lower than that of AMF (~35%), whereas in low-temperature environments, colonization was similar (~20%). Several studies suggested that FRE can enhance host-plant phosphorus uptake and growth, and may be more resilient than AMF to environmental stress in some host plants. Further research is required on the functioning of FRE in relation to the environment, host plant and co-occurring AMF and, in particular, to examine whether FRE are important for plant growth in stressful environments. Targeted molecular primers are urgently needed for further research on FRE

Podocarpaceae in tropical forests: A synthesis

The Podocarpaceae comprises 18 genera and about 173 species of evergreen, coniferous trees and shrubs. It is the most successful gymnosperm family in angiosperm-dominated tropical forests (Brodribb, this volume). Podocarps are distributed mainly in the Southern Hemisphere, with populations also extending as far north as China and Japan and to Mexico and the Caribbean in the neotropics (Dalling et al., this volume; Enright and Jaffré, this volume; Adie and Lawes, this volume)

A standardized set of metrics to assess and monitor tree invasions

Scientists, managers, and policy-makers need functional and effective metrics to improve our understanding and management of biological invasions. Such metrics would help to assess progress towards management goals, increase compatibility across administrative borders, and facilitate comparisons between invasions. Here we outline key characteristics of tree invasions (status, abundance, spatial extent, and impact), discuss how each of these characteristics changes with time, and examine potential metrics to describe and monitor them. We recommend quantifying tree invasions using six metrics: (a) current status in the region; (b) potential status; (c) the number of foci requiring management; (d) area of occupancy (AOO) (i.e. compressed canopy area or net infestation); (e) extent of occurrence (EOO) (i.e. range size or gross infestation); and (f) observations of current and potential impact. We discuss how each metric can be parameterised (e.g. we include a practical method for classifying the current stage of invasion for trees following Blackburn’s unified framework for biological invasions); their potential management value (e.g. EOO provides an indication of the area over which management is needed); and how they can be used in concert (e.g. combining AOO and EOO can provide insights into invasion dynamics; and we use potential status and threat together to develop a simple risk analysis tool). Based on these metrics, we propose a standardized template for reporting tree invasions that we hope will facilitate cross-species and inter-regional comparisons. While we feel this represents a valuable step towards standardized reporting, there is an urgent need to develop more consistent metrics for impact and threat, and for many specific purposes additional metrics are still needed (e.g. detectability is required to assess the feasibility of eradication)