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Chapin Mold Remediation by Whitehall
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Fire and Plants
Evaluating the Impacts of Fire on Australian Ecosystems with Reference to Past Indigenous Practices
The effects of fire on natural systems within Australia are intricate and complex. This complexity is partly due to the variety of responses to fire exhibited by native flora species, which evolved to adapt to the different climates which have occurred since the Cretaceous period (Hill 2016). The impacts of fire can be damaging to flora species (Gill 1996), plant-animal relationships, and various properties of topsoil, all of which will be examined in this essay. The impacts of fire-use on nature can also be positive, a fact which has been understood and practiced by Indigenous Australians for at least 120,000 years (Pascoe 2014). With recent changes to rainfall and peak temperatures in Australia caused by climate change (Cai & Cowan 2013), improved management regarding future fire-use is critical, and this will require the reassessment of past Indigenous practices. In order to better understand the way in which fire can benefit nature, the union of modern scientific research and Indigenous experience regarding fire use is essential.
Fire is an ancient feature of life on Earth and its occurrence is primarily dependent on the presence of oxygen, heat and fuel. The availability of these three factors has changed throughout Australia’s climate history, and as a result the prevalence of fire within the Australian environment has not been constant throughout time (Hill 2016). Research has shown that throughout the Cretaceous (145-65mya), atmospheric oxygen levels were between 23-29%, whereas todays level is 20.9% (Belcher & McElwain 2008). Professor Bob Hill (2016) states that this higher oxygen composition increased fire occurrence, which was a driving factor in the evolutionary processes that created fire-tolerant Australian plant species.
Oxygen levels soon dipped following this period, reaching a low point of 20-23% about 70 million years ago (Belcher & McElwain 2008). This coincided with higher CO2 levels, which Hill (2016) states resulted in an environment with high moisture and rainfall levels. The combination resulted in a decrease in both fire frequency and intensity (Hill 2016). It has been theorized by Hill (2016) that evolution processes in response to this climate resulted in plant species that are fire-sensitive compared to those that evolved to suit the earlier, more fire-prone climate.
This variety of fire tolerances within native flora species means that the effects of fire on ecosystems are intricate (Keeley, Pausas, Rundel, Bond & Bradstock 2011). An insight into plant response to fire by Keeley et al (2011) is that no species is fire adapted, but there are instead many species which are adapted to particular fire regimes. The significance of ecosystem-specific fire regimes was understood by the Indigenous Australians (Gott 2012; Keith, McCaw & Whelan 2002). One example of this ecosystem-specific approach was the regular burning of tussock grasslands which was practiced by Indigenous people (Gott 2005). A grassland study by Morgan (1998) noted that with regards to optimising herbaceous dicotyledon populations, disturbances to the canopy caused by fire, must occur every 1-3 years. This prevents the competitive exclusion of herbaceous species by the dominant grasses from occurring to an undesirable extent (Morgan 1998). This practice thereby ensures species diversity, by creating opportunities for herbaceous species to develop amongst the tussock grasses (Gott 2012).
A post-fire increase in diversity was also illustrated in a ten-year study of the Anglesea Woodlands in Victoria, and their recovery after Ash Wednesday in February 1983 (Gott 2012). The study, by Wark, White, Robertson & Marriot (1997), showed that the following spring after the fire, there was a mass flowering of tuberous perennials. Species richness measurements showed that after the first-year there was great diversity, with an abundance of herbaceous plant species (Wark et al. 1997). Wark et al. (1997) noted that after the third year, when canopy cover and shrub height had increased, species richness began to decrease in response. In the final year of the study, species richness was only 40% of the year 1-3 level, demonstrating that a frequent use of fire, as practiced by Indigenous Australians, helps to maintain higher levels of species richness (Gott 2012). In addition to this initial improvement in species richness, Wark et al (1997) also mentioned that through the fire, nutrients were returned to the soil.
The relationship between fire and topsoils is very important, as post-fire plant diversity is dependent on soils being able to support seed germination (Gott 2005). The impact of fire on soil is largely dependent on peak fire temperatures, and duration (Certini 2003). These two factors combine to define the term ‘severity’ as used by Certini (2003). Certini (2003) states that low-moderate severity fires, can affect nutrient availability, and research has been done on the impacts of fire on the important nutrients, nitrogen and phosphorous.
The impact of fire on topsoil nitrogen is dependent on the severity of the fire (Certini 2003). A substantial proportion of nitrogen is reported to remain unaffected when burnt at low intensity, with a change in form being unlikely to occur (Certini). For moderate-high intensity fires, most organic nitrogen becomes inorganic, in the forms of nitrate and ammonia. Certini (2003) states that nitrogen levels can experience an increase in the first to second growing season. Research has indicated that this peak in nitrogen is followed by a slow return to the pre-fire levels (Grogan, Burns & Chapin Iii 2000). The short-term peak in soil levels after a fire occurs for many different fire regimes, with the exception of very high severity wildfires in which nutrients can be lost through volatisation, which refers to the process of nutrients being vaporized (Certini 2003).
A similar response to fire occurs with regard to soil bound phosphorous. Cade-Menun, Berch, Preston & Lavkulich (2000) showed that a fire event converts organic phosphorous to orthophosphate, which is the sole form of phosphorous that biota can use (Certini 2003). Phosphorous, like nitrogen, experiences peak abundance in a short time after a fire event, and then begins to diminish, until returning to pre-fire levels (Cade-Menun et al. 2000). It is known that nitrogen and phosphorous are key components of plant growth, therefore it can be said that the effect of fire on nutrients can benefit plant growth for many different regimes. The short-term peaks in nitrogen and phosphorous levels favour the frequent use of fire as a way to sustain naturally high nutrient levels, which is reflected in the practise of Indigenous Australians, who generally used fire to maintain select areas every 1-3 years (Gott 2005).
An interesting relationship between Indigenous fire use, food gathering, and soil qualities arises when examining the effects of fire on soil hydrophobicity, or water repellency. Certini (2003), states that for low-moderate severity fires, the hydrophobicity of topsoil is enhanced, with this enhancement reported to remain for approximately 19 months in some environments (Everett, Java-Sharpe, Scherer, Wilt & Ottmar 1995). The impacts of enhanced hydrophobicity can include erosion and increased run-off, as such it can be said that the impact of fire is negative when this possible impact is not considered (Certini 2003).
However, it appears that the effects of fire on hydrophobicity were able to be counter-acted by Indigenous agricultural methods. (Pascoe 2014; Gott 2005). Tuberous perennials, a type of herbaceous plant group, were a major food source for Indigenous groups all throughout Australia (Pascoe 2014). Gott (2005) states that through the post-fire practice of collecting these tubers, hydrophobicity levels were lowered. This occurred as a result of ash and debris being turned back into the soil, which aerated and loosened the soil, thereby improving water absorption. Gott (2005) showed that through the use of traditional methods, the impacts of fire on topsoil can be made more positive and the impacts of hydrophobicity can be mitigated. Healthy soil can then go on to create to benefit the health of plants, and the animals that feed on them (Vandegehuchte, de la Pena & Bonte 2010).
The plant-animal relationships that are influenced by fire are numerous in Australia. One example is Pezoporus wallicus, a ground parrot in south-eastern Australia, that feeds primarily on graminoid seed (Meredith, Gilmore & Isles 1984). Its preferred habitat is heaths and swamps that have a high component of graminoid sedges, and it has been shown that the maintenance of flora species composition in this habitat is dependent on appropriate fire regimes being applied (Gill 1996). When fire is too infrequent, the more competitive shrubs outcompete the graminoid sedge population over time, limiting food availability for Pezoporus wallicus (Meredith et al. 1984). If fire were to be applied to this area in an appropriate regime, the balance between sedges and shrubs would be continually restored, and Pezoporus wallicus would have a more optimum environment and more secure food supply (Gill 1996).
In the likely event that an imperfect fire regime acts on an area, fire can cause great damage. Gill (1996) notes the 1960-61 fire in Central Tasmania as an example of this. As an environment that receives very high rainfall, fires are not usually able to burn. Due to this, local and endemic flora species, such as those from the genus Athrotaxis, tend to have seed production and dispersion techniques poorly adapted to fire (Kirkpatrick & Dickinson 1984). Therefore, when the high severity fire event of 1960-61 took place, local extinctions of two Athrotaxis species, as well as other endemic conifers such as Diselma archeri and Podocarpus lawrencii, occurred (Gill 1996). Gill (1996) stated that the area is unlikely to reach a pre-fire state over the next several thousand years, indicating the level of damage which can be inflicted by fire-events that are inappropriate to the environment they occur in.
Conclusion:
Fire-sensitive areas, such as alpine Central Tasmania, will be increasingly at risk of fire as rainfall decreases and peak temperatures increase (Cai & Cowan 2013). It is therefore critical that the ways in which fire can have a positive relationship with ecosystems continue to be explored. The development and use of fire-regimes that are tailored to a specific environment is necessary in order to achieve positive outcomes, and this will only occur through the incorporation of viable traditional Indigenous methods. Modern research, which has supported the viability of many of these methods (Gott 2005; Morgan 1998), has added to the body of knowledge on plant-animal relationships regarding fire use (Gill 1996). By reconciling the information from both sources of understanding, the negative effects of future fires can be mitigated, and the potential for fire to exist as a positive component of our environment can be realized.
References
Belcher, C., & McElwain, J. (2008). Limits for Combustion in Low O₂ Redefine Paleoatmospheric Predictions for the Mesozoic. Science, 321(5893), 1197-1200. Retrieved from http://www.jstor.org.libproxy.murdoch.edu.au/stable/20144700
Cade-Menun, B. J., Berch, S. M., Preston, C. M., & Lavkulich, L. M. (2000). Phosphorus forms and related soil chemistry of Podzolic soils on northern Vancouver Island. II. The effects of clear-cutting and burning. Canadian Journal of Forest Research, 30(11), 1726-1741. https://doi.org/10.1139/x00-099
Cai, W., & Cowan, T. (2013). Southeast australia autumn rainfall reduction: A climate-change-induced poleward shift of ocean-atmosphere circulation. Journal of Climate, 26(1), 189-205. Retrieved from http://libproxy.murdoch.edu.au/login?url=https://search-proquest-com.libproxy.murdoch.edu.au/docview/1317399342?accountid=12629
Certini, G. (2005). Effects of fire on properties of forest soils: a review. Oecologia, 143(1), 1-10. doi:http://dx.doi.org.libproxy.murdoch.edu.au/10.1007/s00442-004-1788-8.
Everett, R. L., Java-Sharpe, B. J., Scherer, G. R., Wilt, F. M., & Ottmar, R. D. (1995). Co-occurrence of hydrophobicity and allelopathy in sand pits under burned slash. Soil Science Society of America Journal, 59(4), 1176-1183. doi:10.2136/sssaj1995.03615995005900040033x
Gill, M.A. 1996, ‘How Fires Affect Biodiversity’, Australian National Botanic Gardens and Centre for Australian National Biodiversity Research, Canberra. Retrieved from: https://www.anbg.gov.au/fire_ecology/fire-and-biodiversity.html#ABS
Gott, B. (2005). Aboriginal fire management in south-eastern Australia: aims and frequency. Journal of Biogeography, 1203-1208. Retrieved from: https://www-jstor-org.libproxy.murdoch.edu.au/stable/3566388
Gott, B. (2012). Indigenous burning and the evolution of ecosystem biodiversity. Proceedings of the Royal Society of Victoria, 124(1), 56-60. Retrieved from: http://libproxy.murdoch.edu.au/login?url=https://search-proquest-com.libproxy.murdoch.edu.au/docview/1268714828?accountid=12629
Grogan, P., Burns, T. D., & Chapin Iii, F. S. (2000). Fire effects on ecosystem nitrogen cycling in a Californian bishop pine forest. Oecologia, 122(4), 537-544. https://doi.org/10.1007/s004420050977
Hill, B. (Lecturer). (2016, August 23). Vodcast: Fire, Air, Earth, Water – The Elemental Drivers Of The Australian Vegetation. Professor Bob Hill [Video podcast]. Retrieved from https://blogs.adelaide.edu.au/environment/2016/08/23/vodcast-fire-air-earth-water-the-elemental-drivers-of-the-australian-vegetation-professor-bob-hill/
Keeley, J. E., Pausas, J. G., Rundel, P. W., Bond, W. J., & Bradstock, R. A. (2011). Fire as an evolutionary pressure shaping plant traits. Trends in plant science, 16(8), 406-411. https://doi.org/10.1016/j.tplants.2011.04.002
Keith, D. A., McCaw, W. L., & Whelan, R. J. (2002). Fire regimes in Australian heathlands and their effects on plants and animals. Flammable Australia: the fire regimes and biodiversity of a continent. Cambridge University Press, Cambridge, 199-237.
Kirkpatrick, J. B., & Dickinson, K. J. M. (1984). The impact of fire on Tasmanian alpine vegetation and soils. Australian Journal of Botany, 32(6), 613-629. https://doi.org/10.1071/BT9840613
Meredith, C. W., Gilmore, A. M., & Isles, A. C. (1984). The ground parrot (Pezoporus wallicus Kerr) in south‐eastern Australia: a fire‐adapted species?. Australian Journal of Ecology, 9(4), 367-380. https://doi.org/10.1111/j.1442-9993.1984.tb01374.x
Morgan, J.W. (1998). Importance of canopy gaps for recruitment of some forbs in Themeda trianda dominated frasslands in south-eastern Australia. Australian Journal of Botany, 46(6), 609-627. https://doi.org/10.1071/BT97057
Pascoe, B. (2014). Dark emu black seeds: agriculture or accident?’. Broome, WA: Magabala Books Aboriginal Corporation.
Vandegehuchte, M. L., de, l. P., & Bonte, D. (2010). Relative importance of biotic and abiotic soil components to plant growth and insect herbivore population dynamics. PLoS One, 5(9) doi:http://dx.doi.org.libproxy.murdoch.edu.au/10.1371/journal.pone.0012937
Wark, M. C., White, M. D., Robertson, D. J., & Marriott, P. F. (1987). Regeneration of heath and heath woodland in the north-eastern Otway Ranges following the wildfire of February 1983. Proceedings of the Royal Society of Victoria, 99(2), 51-88.
Yan, W., Zhong, Y., & Shangguan, Z. (2016). A meta-analysis of leaf gas exchange and water status responses to drought. Scientific reports, 6, 20917. https://doi.org/10.1038/srep20917
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Whitehall Water Damage Restoration Company
Water Damage Restoration Chapin SC
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