The introduction of livestock to the vast majority of public lands may be used to simulate the conditions provided by herbivorous grazers in the past, however little data has been collected on the effects of livestock grazing in Sonoran desert habitats. Vegetative species that are characteristic of the Arizona Upland subdivision of the Sonoran desert did not evolve with extensive grazing by large ungulate populations, and therefore the response to livestock grazing is of particular interest. Four historic Parker 3-step clusters in south-central Arizona were sampled in three cohorts between 1953 and 2016 to interpret changes in rangeland health using soil coverage data, species richness and frequency, and long-term photo point comparisons. Cattle grazing was active across the allotment until 1984, allowing approximately 30 years of rest before the third and final cohort was measured. Over the entirety of this study, there was a 66.67% increase in perennial basal hits, a 56.29% increase in rock, and a 44.55% increase of forage basal hits. Decreases were seen in litter (-57.69%) and bare soil hits (-8.76%). Cluster 3 consistently had a lower percent of cover across all classes of vegetation in the 2014 cohort

(-81.61%), however the average percent of cover increased by 63.16% (40 hits) across the allotment. Available species richness data from 1971 and 2014 cohorts indicates a 112% increase in unique species; however, species richness increases in the 2014 cohort are largely based on recruitment of non-palatable species (71%). Although the status of some species were undetermined, all individuals identified to species in the invader class (non-palatable) were determined to be native to the study site. Perennial grass frequency became less abundant over the duration of this study, while growth was predominantly observed in shrubs. Increases in species frequency was detected on two of the four clusters measured in the 2014 cohort; the growth was primarily observed in jojoba (Simmondsia chinensis), oak (Quercus spp.), and catclaw acacia (Senegalia greggii) in C4, and hopseed bush (Dodonaea viscosa) in C2.

This study was conducted to determine the effect of various sodium and calcium-based saline treatments on the germination and early growth of Leucaena leucocephala. The evaluation of calcium-based salts has never been studied for its effects on Leucaena leucocephala. This experiment utilized 5 increasing concentrations of sodium chloride, calcium chloride, and a 1:1 ratio of NaCl: CaCl2. The growth and germination of these seeds were recorded over the course of 11 days. Two trials of this experiment were run- the first using seeds collected from ASU's Polytechnic campus and the second using seeds collected from roadside landscaping. The results of both trials indicated that germination and early growth are affected by the different saline treatments. For trial one, the seeds germinated best under treatments involving either 0.0125 or 0.025 M CaCl2 or NaCl: CaCl2. For trial two, the seeds germinated best under treatments involving either 0.025 or 0.05 M CaCl2 or NaCl: CaCl2. Thus, seeds from Leucaena leucocephala are best germinated under saline treatments consisting of either just calcium chloride or a 1:1 mixture of sodium chloride and calcium chloride.

Die-off of screwbean mesquite (Prosopis pubescens), a species native to the American Southwest, has been documented regionally within the last decade. Historical causes for episodic mortality of the more widely distributed velvet mesquite (Prosopis velutina) and honey mesquite (Prosopis glandulosa) include water table declines and flood scour. Causes of the recent die-offs of P. pubescens have received little study. Numerous riparian restoration projects have been implemented regionally that include screwbean mesquite. Restoration propagules from foreign sources can introduce diseases, and low genetic diversity plantings may allow for disease irruptions. I asked: 1) Are die-offs associated with a particular age class, 2) Is die-off suggestive of a pathogen or related to specific environmental stressors, 3) Are mortality influences and outcomes the same between restoration and local populations, 4) Are particular land uses and management associated with die-off, and 5) Are populations rebounding or keeping pace with mortality?

I documented the screwbean mesquite population status at rivers and wetlands in Arizona with varying levels of restoration. I used logistic regression and Pearson correlation analysis to explore mortality response to site factors and disease related variables. I compared mortality response and disease severity between local and restoration populations.

Biotic damage surfaced as the most important factor in statistical analyses, suggesting that mortality was caused by a pathogen. Mortality was greatest for young size classes (3 to 14 cm), and biotic damage was higher for individuals at infrequently flooded areas. Strong differences were not found between local and restoration populations – however restoration populations were less stressed and had lower biotic damage. Novel urban and restored sites may provide refuge as site conditions at other locations deteriorate. A culmination of past water diversion, development and land use may be surfacing, rendering riparian species vulnerable to diseases and triggering such events as region-wide die-off.

Mycorrhizal fungi form symbiotic relationships with plant roots, increasing nutrient and water availability to plants and improving soil stability. Mechanical disturbance of soil has been found to reduce mycorrhizal inoculum in soils, but findings have been inconsistent. To examine the impact of restoration practices on riparian mycorrhizal inoculum potential, soil samples were collected at the Tres Rios Ecosystem Restoration and Flood Control Project located at the confluence of the Salt, Gila, and Agua Fria rivers in central Arizona. The project involved the mechanical removal of invasive Tamarix spp.( tamarisk, salt cedar) and grading prior to revegetation. Soil samples were collected from three stages of restoration: pre-restoration, soil banks with chipped vegetation, and in areas that had been graded in preparation for revegetation. Bioassay plants were grown in the soil samples and roots analyzed for arbuscular mycorrhizal (AM) and ectomycorrhizal (EM) infection percentages. Vegetations measurements were also taken for woody vegetation at the site. The mean number of AM and EM fungal propagules did not differ between the three treatment area, but inoculum levels did differ between AM and EM fungi with AM fungal propagules detected at moderate levels and EM fungi at very low levels. These differences may have been related to availability of host plants since AM fungi form associations with a variety of desert riparian forbs and grasses and EM fungi only form associations with Populus spp. and Salix spp. which were present at the site but at low density and canopy cover. Prior studies have also found that EM fungi may be more affected by tamarisk invasions than AM fungi. Our results were similar to other restoration projects for AM fungi suggesting that it may not be necessary to add AM fungi to soil prior to planting native vegetation because of the moderate presence of AM fungi even in soils dominated by tamarisk and exposed to soil disturbance during the restoration process. In contrast when planting trees that form EM associations, it may be beneficial to augment soil with EM fungi collected from riparian areas or to pre-inoculate plants prior to planting.