Lakes Sample Clauses

Lakes. During meal breaks or rest breaks, Lakes District will supply free tea, coffee, milk, and sugar. Where it is impractical to supply tea, coffee, milk, and sugar free of charge, an allowance of $1.26 per week in lieu shall be paid. This allowance will continue during all periods of leave except leave without pay.

Lakes. Resident acknowledges that the Community's lakes, if any, are for aesthetic purposes only. Swimming and boating are not allowed in lakes and waterways by Resident, Occupants of the Unit or guests. Fishing, if permitted at all, is on a “catch and release” basis only. Resident shall not use or permit any guests or Occupants to use the lakes for swimming, bathing, boating or any other recreational activity. Resident acknowledges that the lakes can be deep in places and that there are no fences around or lifeguards at the lakes and that the use of the lakes for any other reason by Resident or any guests or Occupants is strictly prohibited. Resident further agrees that Owner is not liable to Resident, Resident’s guests or any other occupants for personal injury or damage or loss resulting from the use of the lakes by Resident or Resident’s guests or Occupants. Resident must take whatever steps necessary to assure compliance with this provision by you as well as Resident’s guests and Occupants who reside in the Unit. Resident agrees to comply with any and all signs and rules and regulations which Owner may, from time to time, adopt with respect to the lakes and to assure such compliance by Occupants and guests.

Lakes. Lakes shall make an Initial Capital Contribution to the Company equal to $2,105,000. Lakes shall be required to make its Initial Contributions in cash (via wire transfer) simultaneously with its execution of this Agreement. For its Initial Capital Contribution, Lakes shall receive 182,222 Membership Units.

Lakes. Large computerized and/or ecological type models are not, except in rare circumstances, recommended for use at the present. Large data requirements and lack of consensus regarding their applicability often render then impractical for use. From the standpoint of dissolved oxygen, if there are data which show that current discharges meet water quality standards and there are no nuisance problems associated with the discharger, then current effluent limitations should be adequate. The ▇▇▇▇▇▇▇▇▇▇▇▇, ▇▇▇▇▇▇-▇▇▇▇▇▇▇ or similar nutrient-budget models can be used to determine if nutrient reductions should be considered. Application of these models can be seen in Analyses of Southeastern Lakes as previously done by Region IV and the EPA-HQ AWT Review of Lake Toho. If these models indicate a problem, then nutrient reductions from point sources should be considered. The relative magnitude of non-point sources and their abatement possibilities should also be considered. Elimination of discharges to lake bays and coves should be evaluated. Diffuser outfalls for discharges to the main body of lakes should be required where needed to eliminate localized or nuisance problems. Standard stream models can often be used for run of the river type impoundments, and dispersion type models can sometimes be used on bays, however, photosynthetic activity should be taken into account.

Lakes. The literature review returned 333 lakes in which the recovery of at least one BQE was reported following external nutrient load reduction alone, 130 lakes in which only in-lake management was conducted and 51 lakes in which in-lake and external nutrient load management measures were conducted (Figure 22). Reports on phytoplankton were most common (44% of case studies reporting ecological recovery) followed by macrophytes (15%), zooplankton (14%), macroinvertebrates (13%), fish (12%), waterfowl (2%) and bacterioplankton (<1%). External In lake + external In lake Number of LECs Phytoplankton Macrophytes Zooplankton Macroinvertebrates Fish Waterfowl Bacterioplankton The study did not separate the individual restoration measures taken. A number of studies have analyzed post-▇▇▇▇▇▇ conditions of lakes and watercourses. As mentioned, chemical response is almost immediate, while response of different organism groups is taxon-specific. Fish, phytoplankton and benthic invertebrate assemblages are often monitored to determine the effects of ▇▇▇▇▇▇ on lake communities. Response times varying considerably and are often site-specific, but in general phytoplankton respond > benthic invertebrates > fish. Post-▇▇▇▇▇▇ biological restoration has often focussed on two areas of study; namely, measures to facilitate natural recolonization and re-establishment of locally extinct populations and reintroduction of locally extinct species by restocking (▇▇▇▇▇▇▇▇▇ 1995). For example, removal of migration obstacles and improvement of habitat are two measures used to facilitate recolonization and establishment. In contrast to assessing the effects of ▇▇▇▇▇▇, fewer studies have looked at natural recovery of acidified lakes and watercourses. For lakes, fossil remains of diatoms and other organism groups (e.g. chironomid midges) have been frequently used in the Nordic countries, the UK and Canada. Although seemingly costly and requiring a substantial amount of taxonomic expertise, paleo approaches have been shown to be extremely good at establishing pre-acidified conditions as well as for tracking long-term changes in assemblage composition. More recently these approaches have been used to determine if recovery trajectories follow degradation pathways. By contrast, use of contemporary data is someone limited by the scarcity of long-term monitoring data. Recent studies have shown that assessment of recovery is dependent on the response variable chosen, and that factors other than improv...

Lakes. Most lakes within the Merritt TSA have been classified through a local planning process (the Merritt TSA Lakes Classification Process), and were assigned a class of A, B, C, D or E. Each of these classifications designates a lakeshore management zone (LMZ) that in practice extends beyond the RRZ Merritt TSA TSR 4 Draft Data Package dictated by the Riparian Guidebook where one exists, and implies specific basal area retention as shown in Table 10. The TSR3 analysis assumed that any RRZ was entirely contained within the LMZ, and the same methodology has been applied to these lakes for the benchmark analysis scenarios. Lakes not classified through the local planning process were classified by applying the Riparian Guidebook criteria of lake surface area and surrounding BEC subzone (as determined from the provincial BEC ecosystem inventory). This process resulted in the L1 – L4 classifications and associated RRZ buffers listed in Table 10.

Lakes. The general data analysis approaches employed in the 46 lake equivalent case studies are summarised (Figure 10). The majority of the lakes employed ‘before and after’ and ‘time series’ approaches. The majority of lakes employed multiple data analysis approaches (4 lakes used 1 approach; 34 lakes used 2 approaches; and 8 lakes used 3 approaches). The use of statistical analyses to validate the data analysis approaches across the 46 lakes is summarised (Figure 11). The majority of the 21 lakes in which statistical analyses were used to test some aspect of the recovery process used ANOVA or regression analyses. 26 % of the 46 lakes considered longer- term recovery effects (i.e. > 10 years; Figure 12). No. of LECs % of all LECs 120 100 Number and % of LECs 80 60 40 20 Space for time Control/impact Time series Before/after No. of LECs % of all LECs 30 25 Number and % LECs 20 15 10 5 T/Z test Correlation Regression ANOVA 0 No. of LECs % of LECs 50 Number and % of LECs 40 30 20 10 6-10 11-15 Years of monitoring in excess of max. reported transient period The majority of lake ▇▇▇▇▇▇ studies lack robust pre-▇▇▇▇▇▇ conditions. Indeed, most ▇▇▇▇▇▇ projects were started simply if lake water pH dropped below 6.0. Knowledge of biological conditions was seldom measured as were other water chemistry variables. Analyses to determine the effects of ▇▇▇▇▇▇ are generally based on time-series data of surface water chemistry and comparison of lake biology with nearby reference lakes. Palaeolimnology has proved an important means of assessing the timing, extent and causes of acidification since the mid- ninteenth century. In particular the development of the diatom-pH transfer function and the use of sub-fossil material from lake sediments to identify pollution from long-range sources have provided valauble information in the absence of historical / monitoring data over this period. Palaeolimnological data can now be compared with observational time series data from monitored sites to provide a means of validating the sub-fossil based reconstructions. Diatoms and the remains of other organism groups stored in lakes sediments have been used to track both degradation and recovery phases.

Lakes. Lakes shall make an additional capital contribution to the Company equal to $7,895,000 and shall receive additional Membership Units, the number of which shall be determined by dividing the total Additional Capital Contribution made by 22.1120. For fully funding its Additional Capital Contribution, Lakes shall receive 357,045 Membership Units.

Lakes. The concept of regime shifts was apparent within the lakes although none of the studies specifically set out to quantitatively assess response trajectories. The general approach was instead to assess specific responses over a short time scale. The main reason for failure of restoration in the case studies appeared to be insufficient control of catchment or internal TP loading or through lack of sustained control of fish stocks. In terms of acidification there are very few studies (and none included in the review) which address the concept of shifting baselines. However, recent (unpublished) data show how the recovery trajectories in some lakes are not tracking back towards the species communities found at the equivalent stage of the degradation phase. Several reasons have been proposed for this including the effects of atmospherically deposited nitrogen acting as a nutrient in N limited systems and the effects of climate change driven increases in temperature. Although there is little direct evidence that climate change has altered baselines so that new system equilibria have resulted, independent of the effects of existing pressures, increasing numbers of studies have identified cases where, despite measures taken to combat the effects acidification, the recovery trajectory is not indicating a return to pre-impact reference conditions. ▇▇▇▇▇▇▇▇▇▇ et al. (2011) found a parallel trend towards increase in chlorophyl-a yield per unit nitrogen in the past decade in all regions examined and they indicate this could be the result of the major shift in the baselines for the functioning of coastal ecosystems resulting from the combined effect of climate change, overfishing and, possibly, other components of global change. The shift in the functional relationship between chlorophyl-a and TN over time reported by ▇▇▇▇▇▇▇▇▇▇ et al. (2011) helps to explain reported failure to revert eutrophied coastal ecosystems to their previous state following reduction of nutrient input (▇▇▇▇▇▇ et al. 2009). Despite observed increases in chlorophyl-a concentrations it is still important to stress that nutrient do release pressure on the ecosystem and improve conditions relative to what these would have been under a ‘do nothing scenario’. The Nervión estuary is an example of shifting baselines. In this estuary, recovery occurred with decreasing pressures but the system did not return to its original state, since many ecosystems had been reduced or lost (e.g. intertidal areas, salt-m...